Growth and Survival Responses to Experimental Fishing: models, experiments and lessons from the Northern pikeminnow of South Central British Columbia by Nathan Gabriel Taylor B.Sc. (Hons.), The University of British Columbia, 2001 A THESIS SUBMITTED IN PARTIAL FULFILMENT OF THE REQUIREMENTS FOR THE DEGREE OF DOCTOR OF PHILOSOPHY The Faculty of Graduate Studies (Zoology) THE UNIVERSITY OF BRITISH COLUMBIA August 2006 Â© Nathan Gabriel Taylor, 2006 Abstract n Abstract The objective of this was study was to determine if species specific fishing could produce "cultivation-depensation effects" in an aquatic ecosystem with two predatory, competing fish species. I identified a unique stock of northern pikeminnow living in series of connected lakes that has obligatory rearing in specific nursery lakes; developed two novel likelihoods to measure the growth, movement and mortality responses; developed an ecosystem model to predict how the system would respond to fishing, and finally, compared the ecosystem modeling predictions to observed responses. My research showed northern pikeminnow in South Central B.C. have obligatory rearing in specific nursery lakes then disperse to other lakes as adults. I argue that this large scale spatial ontogeny can be solely explained by temperature cues to spawn and that the distribution of adults is deter mined by density-dependent dispersal that equalize very large productivity and effective density differences between lakes. I showed that in spite of being included in many stock assessments, and being used as proxies for natural mortality estimates and for exploitation rate targets, von Bertalanffy growth parameters are not generally estimated correctly. The data used to do so are virtually always biased due to: size-selective gears, populations subjected to fishing and natural mortality and in some cases, size-dependent movement. I developed two new likelihoods to si multaneously estimate growth and mortality parameters: one for length-age data, and another for mark-recapture data. The first performs well across a range of recruitment anomalies and steady state fishing mortalities but fails when fishing rates have been variable (especially increasing) and when gear selectivity is dome-shaped. The second likelihood works well with simulated data but is not robust to assumptions of constant recruitment and measure ment error being violated. I combined length-age and mark-recapture data to show using simulated sampling that it is possible to simultaneously esti mate growth, mortality, and movement parameters where sufficient numbers of fish are observed moving. The assumptions required for these models to Abstract 111 perform well are very restrictive. I used a simple ecosystem model and compared the predictions to ob served responses following depletion fishing in two-fish lake systems with rainbow trout and northern pikeminnow. Consistent with model predictions, growth was slower and mortality of juvenile rainbow trout higher relative to the control in lakes where northern pikeminnow were removed, while adult rainbow trout survival remained unchanged. Visual survey indices of north ern pikeminnow fry indicated survival of 1+ fish worsened and 2+ improved following fishing. Consistent with model predictions, no obvious mortal ity or growth responses were observed in adult fish in either rainbow trout or northern pikeminnow removals. While the agreement between the model and observations was encouraging, field testing such complex predictions was fraught with difficulty. The probability distributions of the parameters of in terest were very broad. Also, the model predicts that survival and behavioral dynamics producing the greatest differences in direction and magnitude of ecosystem response occur in size classes of fish and groups of zooplankton that are difficult to observe. It was not possible to conclude whether an alternate state was produced through cultivation-depensation effects. To do so would require longer term data on recruitment responses, vulnerability exchange processes and survival data of young age classes of fish. This study identifies several shortcomings in our ability to predict and detect how ecosystems will respond to fishing. First, our ability to measure even simple response variables such as growth and mortality is not good. Sec ondly, even if we could, the direction and magnitude of these responses can be highly counter-intuitive. Finally, those processes with the most violent effects on our predictions are those for which we have very little informa tion, namely dynamics determining the spatial distribution of the stock, the dynamics of young fish and behaviorally mediated predation rates. Contents iv Contents Abstract ii Contents v List of Tables vii List of Figures ix Acknowledgements xvi 1 Introduction 1 1.1 Review 2 1.1.1 Compensation in fish stocks 2 1.1.2 Stock-Recruit Curve Analysis: Compensation Versus Depensation 4 1.2 Research Hypothesis and Experiment 5 1.2.1 The Cultivation Depensation Hypothesis 5 1.2.2 Experimental depletions 8 2 Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 12 2.1 Introduction 3 2.2 Methods 5 2.2.1 Study site 12.2:2 Spawning and Visual Surveys ' â€˘ â€˘ â€˘ 16 2.2.3 Apparent mortality 18 2.2.4 Hydrography and Productivity 20 2.2.5 Bioenergetics modeling . 22.2.6 Lake feeding load 25 2.3 Results 26 2.3.1 Spawning and Visual Surveys 2Contents v 2.3.2 Apparent mortality 27 2.3.3 Hydrography and Productivity 22.3.4 Bioenergetics predictions 30 2.4 Discussion 36 2.5 Appendix 41 3 Estimating Growth from Length At Age Data 50 3.1 Introduction 53.2 Methods 4 3.2.1 Likelihood derivation 53.2.2 Model 1 growth with no history of fishing 54 3.2.3 Model 2 reduced likelihood 57 3.2.4 Model 3 growth under harvesting 59 3.2.5 Model 4 Reduced likelihood with fishing 62 3.2.6 Simulations 63.2.7 Growth parameter estimation for northern pikeminnow 64 3.3 Results 65 3.3.1 Northern pikeminnow growth parameter estimates ... 73 3.4 Discussion 73.5 Acknowledgements 79 4 Estimating movement and growth parameters given size-dependent spatial ontogeny 81 4.1 Introduction4.2 Methods 4 4.2.1 Length-age likelihood 84.2.2 Mark-Recapture Data 7 4.2.3 Mark-Recapture Likelihood for Growth 89 4.2.4 Mark-Recapture Likelihood for Survival with no Move ment 91 4.2.5 Mark-Recapture Likelihood for estimating survival pa rameters and movement 94 4.2.6 Movement Model 7 4.2.7 Combined Likelihoods 100 4.2.8 Simulation Stock-Assessment Using Combined Likeli hoods with No Movement 101 4.2.9 Simulation of growth parameter estimates with length-dependent movement 105 Contents vi 4.2.10 Effects of Gear Selectivity and Capture Probability on Mortality and Movement Parameters 106 4.3 Results 107 4.3.1 Estimation Trials with No Movement 104.3.2 Simulation of growth parameter estimation with length-dependent movement 112 4.3.3 Effects of Gear Selectivity and Capture Probability on Mortality and Movement Parameters 114 4.4 Discussion 118 5 Predicted and Observed Ecosystem Responses to Fishing . 124 5.1 Introduction 125 5.2 Methods 8 5.2.1 Ecosim Model of Predicted Observations 125.2.2 Experimental fishing 135 5.2.3 Fish ageing 138 5.2.4 Depletion Experiments 140 5.2.5 Visual Surveys 141 5.2.6 Estimation of Survival and Growth Parameters .... 142 5.2.7 Prior Distributions 146 5.2.8 Markov Chain Monte Carlo Sampling for parameter uncertainty 147 5.3 Results 148 5.3.1 Predicted responses to experimental fishing of using Ecosim 145.3.2 Estimated Depletion 150 5.3.3 Visual Surveys 163 5.3.4 Northern pikeminnow growth, mortality and movement parameter estimates '. 163 5.3.5 Rainbow trout growth and mortality estimates 166 5.4 Discussion 176 General Conclusions 181 6.1 The difficulty of properly estimating growth and mortality pa rameters 186.2 Evaluating Ecosystem Impacts of Fishing 183 Bibliography 186 List of Tables vii List of Tables 2.1 Table of lake areas, maximum depths and perimeters 16 2.2 Parameter values used in northern pikeminnow bioenergetics model from Petersen and Ward (1999) 22 2.3 Table of fish marked, marked fish killed during handling, re captured, and unmarked by date and length-converted age in Dad's lake 42.4 Table of fish marked, marked fish killed during handling, re captured, and unmarked by date and length-converted age for July, August and September 2002 in Mom's lake 43 2.5 Table of fish marked, marked fish killed during handling, re captured, and unmarked from June to August 2002 by length-converted age in Nestor lake 44 2.6 Table of fish marked, marked fish killed during handling, re captured, and unmarked from August to September 2002 by length-converted age in Nestor lake 45 2.7 Table of fish marked, marked fish killed during handling, re captured, and unmarked by length converted age from June to August 22 2002 in Moose Pasture Lake 46 2.8 Table of fish marked, marked fish killed or removed during handling, recaptured, and unmarked by length converted age for August 23 to September 2002 in Moose Pasture Lake. ... 47 2.9 Table of fish marked, marked fish killed or removed during handling, recaptured, and unmarked by length converted age from June to September in Cheryl Lake 48 2.10 Table of fish marked, marked fish killed or removed during handling, recaptured, and unmarked by length converted age from June to September in Wilderness Lake 49 3.1 Parameters used to generate fake data 64 3.2 Estimated parameter values for each model 75 List of Tables viii 4.1 Format of mark-recapture data by cohort R released and re captured at times t and estimated parameters for survival <j)t and capture probability pt ' 88 4.2 Parameters used to generate fake data for combined likelihoods 102 5.1 Parameters for multi-stanza representation of northern pikeminnow and rainbow trout populations 132 5.2 Diet composition matrix for Ecopath model. Each column is the diet composition of a particular predator, as a proportion of total annual biomass food intake 133 5.3 Basic parameter inputs for Ecopath Model 134 5.4 Total length and proportions by bar length (cm) Cheryl Lake 136 5.5 Total length and proportions by bar length (cm) Mom's Lake . 136 5.6 Total number of marked and recaptured northern pikeminnow by drainage, lake and treatment. NPM=northern pikeminnow, RBT=rainbow trout and dep=depletion 143 5.7 Total number of marked and recaptured rainbow trout by size group and lake 144 List of Figures ix List of Figures 1.1 Trophic triangle describing where the survival of the juvenile of the dominant is negatively affected by the prey of the dom inant species. 9 2.1 Map of study lakes. Arrows indicate the direction of stream flow and light grey colored lakes represent nursery lakes. ... 17 2.2 Mean temperature integrated from lake surface to 1 m in depth for Dad's Lake (squares) and Mom's Lake (diamonds). Lines represent linear interpolations between observed temperatures 24 2.3 Maximum likelihood estimates of numbers at each length con verted age. The pasted text is the slope of the fit line through the log numbers at a,ge (log Na) representing the apparent mortality of fully recruited ages (5+) 28 2.4 Chlorophyll A (//gC/iML_1)measurements over time. Top panel is Western drainage: Dad's Lake (squares), Mom's Lake (diamonds) and Nestor Lake (triangles). Bottom panel is Eastern drainage: Moose Pasture (squares), Cheryl Lake (di amonds) and Wilderness Lake (triangles) 29 2.5 Effective density per hectare as represented by the sum of squared fish lengths l 2ha~ l (top) Effective density per hectare per figChlAL^ 1 as represented by the sum of squared fish lengths per hectare l 2ha~ x divided by mean ChlA (figL -1 for Dad's (d), Moose Pasture (p), Mom's (m), Cheryl (c), Nestor (n) and Wilderness (w) lakes 31 2.6 Proportion of the total lake area by depth contour, Dad's open circles, Mom's open squares, Nestor, open diamonds, Moose Pasture closed circles, Cheryl closed squares, Wilder ness closed diamonds 32 List of Figures x 2.7 Predicted weights (in grams) of fit bioenergetics model to ob served weight at age in the nursery area (open circles, P = 0.14) and the predicted weight at age of a fish hatched 15 days later in the head lake (solid line, P = 0.18) 33 2.8 Fit weight-length relationship of northern pikeminnow weight as a function of length 34 2.9 Predicted proportion of maximum consumption rate Piiead (top) required to reach observed size at age 1 and Phead/Pnursery (bottom) vs. delays in headwater lake hatch date 35 3.1 Proportional error in parameter estimates for each likelihood formulation with F = 0. (a) Fabens, (b) model 1, (c) model 2, (d) model 3, and (e) model 4, (circles represent outliers). . . 67 3.2 Proportional error in parameter estimates for each likelihood formulation with F = K. (a) Fabens, (b) model 1, (c) model 2, (d) model 3, and (e) model 4, (circles represent outliers). . . 68 3.3 Proportional error in parameter estimates for each likelihood formulation with F â€” 1. (a) Fabens, (b) model 1, (c) model 2, (d) model 3, and (e) model 4, (circles represent outliers). . . 69 3.4 Proportional error of Fabens (a,b), model 3 (c,d), model 4 (e,f), where F increases in increments of 0.1 to F = 0.5 (a,c,e) and to F = 1.0 (b,d,f). F over time was estimated but the proportional bias is not included here since the true F used to simulate the data changed annually 71 3.5 Growth curves fit to northern pikeminnow data using all 5 models: solid=fabens, dashed=full likelihood, dotted=reduced likelihood, dotdash=full likelihood with fishing, longdash=reduced likelihood with fishing 74 3.6 Plot of vulnerability curve (solid line) for northern pikeminnow estimated using likelihood 3 and direct estimates of vulnera bility using mark-recapture 76 4.1 Movement model used to simulate data. Fish enter the move ment pool at the length-dependent movement rate a-i from the nursery area then divide into areas 2 and 3 with the propor tion /i2 going to area 2, 1 â€” fi2 going to area 3, and 1 â€” <L\ staying in the nursery area 96 List of Figures xi 4.2 Proportion of the population in each area as a function of length ipi, in area 2 (red, ip2) and 3 (green ip3). 99 4.3 Plot of a used to simulate ageing error 104 4.4 Boxplots of proportional bias ((true â€” estimate)/true) of 100 growth and mortality parameter estimates for scenarios a) data generated with no tag loss and fit assuming no tag loss using only the growth increment likelihood L2 (Eq. 4.8), b) data generated with tag loss and fit assuming no tag loss us ing the growth increment L2 and tag survival likelihoods L3 (Eqs. 4.8 and 4.17), c) data generated with tag loss and es timating this tag loss using the growth increment L2 and tag survival likelihoods L3 (Eqs. 4.8 and 4.17), and d) data gener ated with tag loss and estimating this tag loss using length-age (L\), growth increment (L2) and tag survival likelihoods (L3) (Eqs. 4.8, 4.17 and 4.1) with CVR = 0, no measurement or ageing error 108 4.5 Boxplots of proportional bias ((true â€” estimate)/true) of 100 growth and mortality parameter estimates for scenarios a) data generated with no tag loss and fit assuming no tag loss using only the growth increment likelihood L2 (Eq. 4.8), b) data generated with tag loss and fit assuming no tag loss us ing the growth increment L2 and tag survival likelihoods L3 (Eqs. 4.8 and 4.17), c) data generated with tag loss and es timating this tag loss using the growth increment L2 and tag survival likelihoods L3 (Eqs. 4.8 and 4.17), and d) data gener ated with tag loss and estimating this tag loss using length-age (Li), growth increment (L2) and tag survival likelihoods (L3) (Eqs. 4.8, 4.17 and 4.1) with CVR = 0.2, no ageing error, measurement error= 5mm 110 List of Figures 4.6 Boxplots of proportional bias ((true â€” estimate)/true) of 100 growth and mortality parameter estimates for scenarios a) data generated with no tag loss and fit assuming no tag loss us ing only the growth increment likelihood L2 (Eq. 4.8), b) data generated with tag loss and fit assuming no tag loss using the growth increment L2 and tag survival likelihoods L3 (Eqs. 4.8 and 4.17), c) data generated with tag loss and estimating this tag loss using the growth increment L2 and tag survival like lihoods L3 (Eqs. 4.8 and 4.17), and d) data generated with tag loss and estimating this tag loss using length-age (L\), growth increment (L2) and tag survival likelihoods (L3) (Eqs. 4.8, 4.17 and 4.1) with CVR = 0.2, ageing error, measurement error = 5mm " Ill 4.7 Boxplots of proportional bias ((true â€” estimate)/true) of 100 growth and mortality parameter estimates for scenarios a) data generated with no tag loss and fit assuming no tag loss us ing only the growth increment likelihood L2 (Eq. 4.8), b) data generated with tag loss and fit assuming no tag loss using the growth increment L2 and tag survival likelihoods L3 (Eqs. 4.8 and 4.17), c) data generated with tag loss and estimating this tag loss using the growth increment L2 and tag survival likeli hoods L3 (Eqs. 4.8 and 4.17), and d) data generated with tag loss and estimating this tag loss using length-age (Li), growth increment (L2) and tag survival likelihoods (L3) (Eqs. 4.8, 4.17 and 4.1) with variance in length at age parameters (A] and A2 fixed at their true values) 113 4.8 Boxplots of proportional bias ((true â€” estimate)/true) of 100 growth (Loo, K, Ai, A2), mortality (M), length at halfgear selectivity (//,), and gear selectivity function slope (7) param eters when each area is assumed to be separate stock, while simulated data come from a stock with ontogenetic movement from area 1 to areas 2 and 3 115 4.9 Boxplots of proportional bias ((true â€” estimate)/true) in 100 estimates of M and movement parameters with capture prob ability (rows) set to 0.05, 0.35, 0,55 and with ratio of length at half gear selectivity to the mean length at movement set to 0.16, 1.16 and 1.83 117 List of Figures xiii 5.1 Proportion of gillnet meshes used on all depletions 137 5.2 Map of experimental lakes showing the location of rainbow trout density reductions (RBT depletion), and northern pikeminnow density reductions (NPM depletion) 139 5.3 Predicted relative biomass (B) changes after depletion fishing of 4+ northern pikeminnow. The biomass of 2+ RBT and 4+ NPM have been arbitarily set to 1 and the other groups scaled accordingly 151 5.4 Predicted changes in M after simulated depletion fishing of 4+ northern pikeminnow 152 5.5 Predicted body weight changes (kg) after 4+ northern pikeminnow depletion fishing 153 5.6 Predicted changes in relative feeding time after 4+ northern mikeminnow depletion fishing â€˘ â€˘ â€˘ â€˘ 154 5.7 Predicted relative changes in biomass B following 2+ rain bow trout depletion fishing. The biomass of 2+ RBT and 4+ NPM have been arbitarily set to 1 and the other groups scaled accordingly 155 5.8 Predicted changes in M following 2+ rainbow trout depletion fishing 6 5.9 Predicted changes in weight (in kg) after rainbow trout deple tion fishing 157 5.10 Predicted relative changes in feeding time after rainbow trout depletion fishing.' '. . . . 158 5.11 Depletion catches of northern pikeminnow (in numbers) by date for Cheryl lake in 2001 (top), Mom's lake in 2001 (middle) and Moose Pasture lake in 2002 (bottom). . 159 5.12 Estimated northern pikeminnow vulnerable numbers (N) and percent depletion estimates by length for Cheryl and Mom's lake 160 5.13 Northern pikeminnow population and percent depletion esti mates by length, V represent 95 percent CI 161 5.14 Fit of proportion northern pikeminnow leaving the nursery area function by length for each drainage 162 5.15 Percent change in visual survey index in Dad's (blue) and Moose Pasture (red) 164 List of Figures xiv 5.16 Fit of von Bertalanffy growth curve through length-age data in western (top) and eastern (bottom) data. Jitter added to better see overlay 165 5.17 Posterior samples of growth parameters (/og(L00),. K), histor ical natural motality M, and tag loss tl for unfishecl western (left column) and fished eastern drainage (right column). . . . 167 5.18 Posterior samples of movement parameters (maximum pro portion leaving the nursery area fin, proportion of the moving pool going to lake 2 ^2 (Cheryl and Mom's), and the beta dis tribution parameter (3 for the unfished western (left column) and fished eastern drainage 168 5.19 Posterior samples of northern squawfish tagged cohort mor tality Mt by lake '. 169 5.20 Posterior samples of Mt for rainbow trout greater than 200 mm by lake 175.21 Posterior samples of the log asymptotic length log^^ for rain bow trout smaller than 200 mm by lake 171 5.22 Posterior samples of the von Bertalanffy K for rainbow trout smaller than 200 mm by lake 172 5.23 Posterior samples of the instantaneous annual mortality of tagged fish by lake for rainbow trout smaller than 200 mm. . . 174 List of Figures xv Prior Publications Taylor, N., Walters, C, and Martell, S. A new likelihood for simultane ously estimating the von Bertalanffy growth parameters, vulnerability, nat ural mortality and fishing mortality. Canadian Journal of Fisheries and Aquatic Sciences. 62:215-223 A ckn owledgem en ts xvi Acknowledgements Financial support for this project was provided by NSERC and Pew Fel lowships to my supervisor, Carl Walters and by Habitat Conservation Trust Fund Grants to Eric Parkinson. I owe a considerable debt to the people working in the Ministry of Water, Land and Air protection in Kamloops who provided much in terms of equipment and advice to this project. In addition to financial support, the project would not have been possible at all without the practical and intellectual contributions of Eric Parkinson. I am grateful to my fellow graduate students during the research and writing of this PhD. In particular, all the field work for this project was done with my fellow PhD candidate David O'Brien whose experience and good hu mour made field work possible and under many difficult circumstances, fun. Outstanding field help was provided by Sheldon Reddecopp, Shaun Mac-Gloughlan, Clark Bartlett, Hannah Murphy, Annie Brown, Garett Cooper and Christie Stewart. I owe Rob Ahrens and Bob Lessard a lot for their time and tutelage learning new software, analytical techniques, beers to make the whole process tolerable. In addition to his contribution to the latter, I owe much to Steve Martell, since my participation in his master's thesis resulted in the cascade of accidents that brought me to study fish at UBC in the first place. While my supervisor frequently introduces me as a first experiment at tempting to supervise a PhD student with only "don't screw up" as advice, nothing could be further from the truth. Much of the intellectual content of this thesis stems from conversations with Carl while carrying equipment, smoking outside the huts and sitting in on courses. Finally none of this would have been possible without considerable finan cial and emotional support of my parents and loved ones. 1 Chapter 1 Introduction Fisheries science typically assumes the relationship between the number of new juvenile fish produced and adult biomass to be density-dependent so that the number of juveniles produced per adult increases as adult popu lation size decreases (called compensation). It is also earnestly hoped that this relationship is stationary, meaning parameters describing it do not vary with time. Explaining the failure of some fish stocks to recover following sustained fishing, notably Newfoundland cod (Gadus morhua) (Shelton and Harley, 1999; Rose et al., 2001), has led to the development of a new hy pothesis called Cultivation-Depensation (Walters and Kitchell, 2001) that predicts how trophic interactions can cause juvenile fish survival to decline at low stock size (called depensation) in a pattern that may not be stationary. Here I review the traditional theory used to describe fish population dynam ics, introduce the Cultivation-Depensation hypothesis and describe modeling and experimental research testing this hypothesis using lake ecosystems with only two fish species, rainbow trout and stunted northern pikeminnow Pty-chocheilus .oregonensis. Chapter 1. Introduction 2 1.1 Review 1.1.1 Compensation in fish stocks There has been considerable debate about density-dependent increases in stock productivity at low stock size, or compensation, but there is little debate that some resource will eventually limit the size of a fish population (Rose et al., 2001). The majority of the remaining debate is about the magnitude of compensation and processes that cause it (Rose et al., 2001). The processes that can produce compensation can be examined by looking at the following population dynamics tautology (Walters and Martell, 2004): where Nt represents abundance at time t, Sa adult survival, F the mean fecundity of individuals, and Sj juvenile survival. If a population is at equi librium, so that Nt â€” Nt-i then Eq. 1.1 reduces to the following: In order that this relationship be satisfied where harvesting has reduced Sa and/or Sj, at least one of the three rates must show compensatory change. Though density-dependent changes in fecundity have been reported (Rothchild et al., 1989) some authors doubt the whether changes in fecundity are suffi cient to stabilize populations (Craig and Kipling, 1983; Koslow, 1992; Koslow Nt = Nt_iSa + FNt^Sj (1.1) 1 = Sa + FSj. (1.2) Chapter 1. Introduction 3 et al., 1995) and in any case, harvesting fish typically reduces mean size hence F because in semelparous species increases in size often result in higher fecun dities. However, the total fecundity of a population has been documented to change in response to changes in density, with younger individuals spawning earlier (Funakoshi, 1994) or with a greater proportion of females spawning (Koslow et al., 1995). Documented changes in adult survival as a function of density are relatively rare. The most compelling arguments about which rate is compensatory are those involving density dependent responses occurring in the early stages of life i.e. those processes that affect Sj. Given the apparent stability and/or ambiguities in the relationship be tween fecundity, adult survival and adult density, it is reasonable to assume that most of the actual compensatory responses in fish stocks are occurring with the younger individuals. There are some excellent field examples of den sity dependent survival at various early life stages. Beverton and lies (1992) document how the density dependent component of mortality changes over three time periods between settlement and the second year. They were able to show that the dramatic dampening effect of density dependent mortality of juveniles was sufficient to reduce the 200 fold variation in adult abundance to larval settlement to only a 4 fold variation in the second year. Using 14 pop ulations of Atlantic cod (Gadus morhua), haddock (Melanogrammus aieglefi-nus), whiting (Merlangius merlangus), place (Pleuronectes platessa) and sole (Solea vulgaris) Myers and Cadigan (1993) showed both strong evidence of density-depended mortality within cohorts and relatively little interannual Chapter 1. Introduction 4 variability in the density-independent component of juvenile mortality. Juvenile survival is often related to the rate at which juvenile fish can reach sizes that make them invulnerable to predation. Post et al. (1999) showed using a series of experimental lakes stocked at different densities that at low density, age-1 growth increased and there was a corresponding increase in juvenile survival. Healey (1980) showed that exploited lakes of whitefish had a higher frequency of increased growth and recruitment than unexploited lakes. He also documented somewhat ambiguous changes in fecundity and proposed that adult suppression of young could be the result of adults con fining juveniles to marginal habitats. Marshall and Frank (1999) also show empirical evidence that mean length of age-1 haddock were negatively related to the density of age-4 and older fish, that differences in age-1 length were persistent through life, and that recruitment was positively related to length at age-4. 1.1.2 Stock-Recruit Curve Analysis: Compensation Versus Depensation Regardless of the mechanisms by which compensation is taking place, there is now a considerable amount of data from stock recruitment relationships to support such an assertion. The most important contribution comes from the work of Myers et al. (1995b) who analyzed over 700 spawner-recruitment series looking for parameters that were constant at the species level. Their Chapter 1. Introduction 5 work shows a remarkable result, that the standardized slope at the origin of a stock recruitment curve (or the maximum reproductive rate) is consistently between 1 and 5, i.e. juvenile survival rates'at low density are 1 to 5 times higher than at natural "unfished" densities. Equally importantly, Myers et al. (1995a) show most (125/128) fish stocks do not show any evidence of depensation (or decreasing juvenile survival at low stock size). Considerable work followed Myers et al. (1995a)'s analysis of stock-recruit data with particular attention devoted to determining whether or not mod els parameterized with depensation fit the data better than those without it (Liermann and Hilborn, 1997; Shelton and Harley, 1999; Liermann and Hilborn, 2001; Frank and Brickman, 2000). However, most studies concerned themselves with detecting a stationary depensatory relationship; that is, one with a domain on the stock recruitment curve where juvenile survival con sistently and immediately decreases as adult density decreases resulting in a second low density equilibrium for the fished species. 1.2 Research Hypothesis and Experiment 1.2.1 The Cultivation Depensation Hypothesis The main difference between the cultivation-depensation hypothesis and clas sical depensation is rooted in foraging arena theory (Walters and Juanes, 1993). In classical models of depensation such as that of Holling (1959), the proportion of prey consumed by a predator is limited by handling time or by Chapter 1. Introduction 6 satiation. Classical depensation (Holling, 1959) arises by assuming that the probability of prey encountering predator is a linear function of the densities of predators and prey (akin to first order chemical kinetics) but with preda tor searching times reduced at higher prey densities clue to handling time effects, so that as prey density is reduced, the proportion of prey removed by predators increases. Foraging arena theory (Walters and Juanes, 1993) on the other hand predicts that risk-sensitive foraging on the part of the prey (juvenile fish in this case) mitigates their interaction with predators through exchange rates between the vulnerable prey pool (available to predators) and the non-vulnerable pool. It assumes that juveniles are confined to refuges away from predators (inshore shallow habitats, hiding places etc.) and that predation occurs mainly when juveniles are forced to enter risky states (the foraging arena, Walters and Juanes 1993; Walters and Kitchell 2001). In aquatic systems there is a growing body of evidence to support such a risk sensitive foraging structure (Tonn and Paszkowski, 1992; Tonn et al., 1994; Post et al, 1999). Foraging arena theory predicts that a key factor determining the prob ability of an encounter of predator with prey is prey behavior, not overall prey density. At high densities, prey are forced to make more risky forag ing trips in order to meet their energy demands because food density in the refuges is depressed. Foraging arena theory predicts that in the absence of other trophic effects, when adult density is reduced there is a corresponding decrease in the density of juveniles in the refuge areas meaning higher lo-Chapter 1. Introduction 7 cai food densities and hence fewer risky trips in the foraging arena to feed. One of the emergent properties of foraging arena theory is that it gives rise to the classic compensatory Beverton-Holt spawner-recruit model (Beverton and Holt, 1958; Walters and Korman 1999) and several testable hypotheses about how changes in behavior, productivity, and predation risk can alter the relationship between the number of recruits produced per spawner. There are many hypotheses that explain the existence of alternate stable states in ecosystems (reviewed in Scheffer et al. 2001a). The Cultivation Depensation hypothesis (Walters and Kitchell, 2001) argues that fishing and juvenile dynamics can be the crucial elements in producing a 'flip' in the ecosystem state. Cultivation-depensation effects arise in Ecosim II (Walters et al., 2000) models though the following sequence of events (Walters and Kitchell 2001, represented in Fig. 1.1). Fishing reduces the adult population size of a "dominant" fish species and hence, the total number of juveniles in predation refuges. Juveniles reduce feeding time or time spent at body sizes small enough to be vulnerable to predation risk. Juvenile mortality then decreases so that the net number of recruits stays nearly constant even though fewer juveniles are being produced. However, if there is high predation by the adult fish on some smaller predator or competitor of the juveniles (a 'forage' fish) then as adult density is reduced, the forage fish is released to increase in abundance. Then one or two negative effects can occur. If the forage fish prey directly on juveniles, then predation mortality is directly increased. If the forage fish and juveniles are competitors, increased forage fish abundance Chapter 1. Introduction 8 leads to reduced food density and hence, increased juvenile foraging time and general predation risk. Direct predation of forage fish on the juveniles of the dominant fish species is not necessary for cultivation-depensation. If the forage fish species is "re leased" to increase in abundance, the forage fish may directly prey on juve niles of the dominant species but if some foods are shared, then increased forage fish density means reduced food density and hence increased juvenile foraging time (Walters and Kitchell, 2001). From a management perspective cultivation-depensation effects can have profound impacts. Firstly, they mean that excessive fishing can produce a permanent low density state of the target (or dominant predator) species. They also mean that ecosystem "flips" can happen in the opposite direc tion; ecosystems dominated by the forage species can be flipped back to the dominant predator state. Such transitions need not be solely the product of fishing either, since it is the ratio of risk to productivity that determines the number of recruits per spawner (Walters and Juanes, 1993). Whether concurrent with changes in productivity or not, cessation of fishing in a stock pushed into the forage fish dominated state will not recover without some additional management intervention (such as fishing the forage species). 1.2.2 Experimental depletions The cultivation-depensation hypothesis is well suited to testing using ex perimental depletions since it makes specific predictions about how survival, Chapter 1-. Introduction 9 Figure 1.1: Trophic triangle describing where the survival of the juvenile of the dominant is negatively affected by the prey of the dominant species. Chapter 1. Introduction 10 growth and foraging time should change in response to density manipulations. In this study, I tested if cultivation-depensation effects described above could be produced in the field using depletion fishing. Specific predictions include (Walters and Kitchell, 2001): â€˘ Increase in abundance of small forage fishes or invertebrates if preda tory stock size decreases â€˘ increasing rather than decreasing juvenile foraging time when adult abundance is low due to competition with forage fishes â€˘ decreased juvenile survival rate at low adult population size due to increased foraging time and (or) direct predation by forage species. â€˘ diet and habitat overlap between juvenile fish and the forage fish and/or direct evidence of predation by the forage fish on juveniles should be observed in stomach contents. I conducted depletion fishing of northern pikmminow Ptychocheilus orego-nensis in a series of lakes on Bonaparte Plateau in South Central B.C. having two predacious species: rainbow trout Onchorhynchus mykiss and stunted northern pikeminnow. The objectives of my study were a) to model the system to see under what parameter combinations cultivation-depensation effects could be observed, b) fish the system and c) measure how growth and survival variables of both species responded to depletion fishing. I first iden tified a unique system of lakes where northern pikeminnow have obligatory Chapter 1. Introduction 11 rearing in nursery lakes; I conducted depletion fishing; I developed new statis tical methodologies to measure growth and survival responses to such fishing; I developed an ecosystem model of the study system to see what parameter combinations would produce cultivation-depensation (Walters and Kitchell, 2001) effects; and finally compared the predicted and observed responses to the experimental manipulations; Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 12 Chapter 2 Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow Abstract This is the first report of a freshwater fish population that has obligatory rearing in specific 'nursery' lakes. In two South Central British Columbia drainages, I identified two northern pikeminnow populations having either a single or multiple lake life-history type. I argue that such large scale spatial organization is controlled by temperature driven spawning cues and density-dependent migration from the nursery areas to outlying lakes. I used visual surveys and mark-recapture experiments to show the position of fry and apparent mortality rates in each drainage. I used bioenergetics modeling and showed it is physiologically possible to spawn and hatch in the headwater lakes, but considerable additional consumption would be required, for fish rearing in non-nursery lakes to reach the same mass observed in nursery areas by the following year to compensate for delays in spawning. Using Chlorophyll A, I showed the nursery lakes to be more productive but that this advantage disappears once scaled to the effective density of northern pikeminnow between nursery and non-nursery areas. keywords: unit stock, northern pikeminnow, ontogenetic shift Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 2.1 Introduction Fisheries biologists typically treat lakes as unit stocks where little movement between lakes is assumed even where movement is possible and there are gradients in productivity and density between lakes. While it is understood that fish move between lakes over long time scales, the population dynamics of a typical lake population are assumed to be dominated by local birth and death processes. Following the research of Gerking (1959), many stream pop ulations are also assumed.to occupy only a small range of the stream in spite of the fact that many of the methods used to estimate the total displacement of fish population are biased against detecting larger scale dispersal in the first place (Gowen et al., 1994). However, at drainage scale, lakes are both connected to each other and have gradients of temperature, sediments, water, nutrients, and organic matter (Gomi et al., 2002) that animals could utilize over the course of their ontogeny provided that streams between lakes permit movement between them. Use of more than one lake has been observed in Arctic charr in response to productivity and temperature difference between lakes (Naslund, 1990). Ontogenetic movement can happen over very large scales in marine systems (Rooker et al, 2003). Ecological theory has long predicted ontogenetic niche shifts in response to ontogenetic changes in resource and predation gradients (reviewed in Werner and Gilliam, 1984) and more recently in response to predation risk from larger sized fish of the same or different species (Persson and Eklov, Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 14 1995). In fresh-water systems, habitat shifts in response to such gradients are observed, but the scale of these shifts and the experimental designs to detect them tend to be at small scale, for example, habitat refuges in small ponds or enclosures (Persson and Eklov. 1995; Olson, 1996; Osenberg et al., 1994). Fish in seasonal environments such as temperate lakes have only a short growing season to acquire sufficient energy to survive winter. Young fish face a very strong tradeoff between growing large enough to survive win ter versus the predation risk associated with the additional feeding needed to do this (Post and Parkinson, 2001; Biro et al., 2005). Also, bioenerget-ics (Kerr, 1971; Kitchell et al., 1977) show strong dependence of swimming, consumption and digestion on temperature. The end of season length for age 0+ perch exhibit a nearly linear relationship between length and cumulative degree days (Power and van den Heuvel, 1999). Finally, the number of degree days for recruitment also seems to limit the northern edge of range for many species (Schuter and Post, 1990) when the growing season (as dictated by each species bioenergetics) is not long enough for species to reach sizes large enough to avoid being eaten, have sufficiently large lipid reserves to survive winter. Northern pikeminnow Ptychocheilus oregonensis (Cyprindae) are distributed from Oregon to South Central British Columbia. They have been studied extensively as the target of predator removal programs in Idaho (Jeppson, 1959), British Columbia (Ricker, 1941) and most recently in the Columbia River (Rieman and Beamesderfer, 1990; Beamesderfer, 1992b; Friesen and Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 15 Ward, 1999). In more temperate climes northern pikeminnow grow to asymp totic lengths of 350 â€” 450mm F.L. at which sizes they are prolific predators (Petersen and DeAngelis, 1992). At the northern limit of their distribution, they appear to be stunted growing only to approximately asymptotic lengths 200mm. Here I document the first population of stunted northern pikeminnow that takes advantage of temperature, productivity and density gradients be tween lakes. I use bioenergetics modeling to show that large differences in consumption rates would be needed in order to compensate for delayed spawning caused by cooler temperatures, and argue that the distribution of adults is determined by the ratio of effective density to productivity. 2.2 Methods 2.2.1 Study site The study site was approximately 100 km North of Kamloops in South Cen tral British Columbia, Canada. I studied northern pikeminnow in two sep arate sub-drainages of the Thompson River system. The western drainage (Fig. 2.1) includes Dad's Lake, with two 'head-end' lakes above it: Mom's and Nestor. In the eastern drainage I intensively studied Moose Pasture Lake, which also had two lakes above it called Cheryl and Wilderness (Fig. 2.1). The eastern lakes drain into the Deadman River and the western ones directly into the Thompson River. The other lakes in Fig. 2.1 were given cur-Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 16 Table 2.1: Table of lake areas, maximum depths and perimeters Lake Total Area (ha) Max Depth (m) Perimeter(m) Cheryl 13.5 15 1563 Wilderness 11.9 11 1628 Moose.Pasture 7.3 0 1411 Dads * ' 9.8 9 2044 Nestor... 7.3 ' 12 1531 Moms 7.1 5 1213 sorial visual surveys to check for the presence or absence of juvenile northern pikeminnow. Larger pikeminnow were abundant in all lakes. Since Moose Pasture and Dad's lakes were the only lakes where juveniles were found, f refer to them as 'nursery lakes' and the lakes above them as 'head-end' lakes. Evidence of the spatial organization of these two stocks came from two sources: visual surveys of fry (0+) and early juveniles (1 â€” 3+) in each lake, and the age structure of each lake estimated from population sizes at age. The area, depth and perimeters of the study lakes are listed in table 2.2.1. 2.2.2 Spawning and Visual Surveys From mid-June to mid-July 2002, I observed the location of spawning in the inflow and outflow creeks of Wilderness, Moose Pasture, Cheryl, Dad's, Nestor and Mom's lakes. During this period I also pole seigned and elec-trofished in these same creeks every 2-3 days. In August of 2002 and 2003 I surveyed all the lakes included in figure 2.1 for the presence of absence of emerging fry. fn August of that same year in Dad's and Moose Pasture lakes, Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 18 I enumerated the number of 0+, 1+ and 2+ and greater than 2+ fish visible around the perimeter of the lake. In every case I counted using polarized sunglasses and either walking the shoreline, or by boat between the hours of 10:00 and 14:00. The global positioning satellite (GPS) position of each aggregation of juveniles was recorded (virtually all juveniles observed were in schools of 5-200 individuals each). 2.2.3 Apparent mortality I estimated the apparent mortality using length converted catch curves (Pauly, 1990). This was done because any migration from nursery lakes to head-end lakes would appear as higher apparent mortality (as fish leave). From June to September 2002, fish were continuously tagged using 5 or 15 mm Floy numbered tags during bouts of mark-recapture in each lake conducted at 1-2 week intervals. Fish as small as 55 mm were marked and only those fish released in perfect condition were included in this analysis. Summaries of marked, recaptured, unmarked and killed fish by date, length-converted-age, and lake are in section 2.5. I converted observed lengths into ages using the von Bertalanffy growth parameter estimates fit to length-age data using the reduced likelihood with fishing model 4 (chapter 3, table 3.2) following Pauly (1990) but assuming no seasonal growth. While Pauly (1990) show that considerable bias can be produced in growth parameters by not including seasonality, I did not attempt to estimate the parameters to do so. Firstly, there were no length-Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 19 age data collected during the colder months to provide any contrast between slow and fast growing periods. In winter months lakes are frozen and access is impossible. The bioenergetics data for the Columbia River indicated that growth in length below 4 C was effectively zero, I assumed that growth in length is assumed to be zero from November to end of April. Secondly, I was only interested in the relative comparisons of apparent mortality, so as long as growth parameter biases (and corresponding apparent mortality) can be assumed constant across lakes, then the absolute bias the apparent mortality estimates is irrelevant. Northern pikeminnow depletions were conducted in 2001 in Cheryl and Mom's lakes (described in section 5.2.2). Therefore, catches-at-length from the depletion were also converted to ages, survived forward by one year at a rate of 0.7 (Rieman and Beamesderfer, 1990), and added to the estimated numbers at age in 2002 from the mark-recapture. The apparent mortality Z was calculated as the slope of the log numbers-at-age of fully recruited (5+) fish, f used a Peterson estimator to estimate numbers at age Na where the negative log likelihood of both the marked and unmarked fish (Eq. 2.1) was: J2Ralog(Pa) + Ua\og(l-Pa) (2.1) I where Ra is the number of recaptured fish at age a and pa is the proportion of marked fish Ma to the estimated number at age Na in that lake. While Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow tag-loss and mortality were surely present, the purpose of this analysis was to compare across lakes so I implicitly assumed these to be constant across all lakes. 2.2.4 Hydrography and Productivity I made contour maps of lake depth by measuring depth at 10 transects per lake at approximately 10 m intervals. The GPS position of each depth mea surement was recorded and 1 m depth contour plots made. The proportion of the total lake area occupied by each depth contour was calculated using Arc View 3.0. As a measure of lake shallowness, I plotted the total proportion of lake area versus depth in meters (m). At approximately two week intervals, I measured Chlorophyll A at fixed stations in the middle of each lake by filtering 50 ml of lake water through 2 400 um filter. Filters were then dissolved in acetone overnight and Chloro phyll A was measured using mass spectroscopy. 2.2.5 Bioenergetics modeling The goal of the bioenergetics modeling was to compare, all other things being equal, what proportion P of the maximum physiological consumption rate an age 0+ fish would have to use in order to compensate for delays in hatching. In particular, given expected delays in spawning and hatching due to cooler water in inflows creeks (Beamesderfer, 1992a), I was interested in Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow determining whether or not northern pikeminnow could hatch and rear to age 1 in head-end streams/lakes and if so, how much additional consumption would be needed in order to make up for any delays in spawning produced by colder inflow creeks. I lacked specific data on hatch time, weight at hatching and age 1 for northern pikeminnow, so a number of assumptions were needed.. I set the hatch date (t = 0) in the outflow creeks to July 15. I used the von Bertalanffy growth model to predict weight-at-age 0 and 1, from lengths (model 4, chap ter 3, table 3.2). I fit observed weight at length by fitting w = al13 to 1001 observations of length and weight in the Western drainage. I then converted predicted lengths to weights using the fit a and (5 values. I estimated P by fitting the bioenergetics model to these 'observed weights' at age 0 and 1. I used the bioenergetic parameter set for northern pikeminnow developed by Petersen and Ward (1999). I assumed the diet composition of 0+ northern pikeminnow to be 100 % zooplankton. These parameter values are listed in table 2.2.5. To simulate the effects of delayed hatching with inflow creek spawning in Mom's lake, I simply delayed spawning by increments of one day and compared the P value in Mom's lake that would have been needed to see the 'observed' size at of age 1 fish in Dad's lake. I compared the Phead from the simulations to the observed P of fish reared in the nursery area PnUrs-I drove the bioenergetics model with observed temperatures integrated over the first meter of the water column in Dad's and Mom's lakes. Temper-Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 22 Parameter description Symbol Value Consumption parameters Allometric scaling parameter Ac 0.278 slope of allometric mass function Be -0.197 Temperature dependent growth function threshold T 1(C) tel 0 threshold T 2 (C) te2 20.1 threshold T 3 (C) teS 22.7 threshold T 4 (C) te4 27 proportion consumed at threshold temp 1 xkl 0.001 proportion consumed at threshold temp 2 xk2 0.98 proportion consumed at threshold temp 3 xkS 0.98 proportion consumed at threshold temp 4 xk4 0.01 Respiration Parameters Intercept of allometric mass function for respiration Ar 0.00165 slope of allometric mass function for respiration Br -0.085 QlO approximation Cr 0.18 Coefficent of swim speed to metabolism Dr 0.003 slope fo the function for temperature effect on respiration rate tau 0.105 Activity Parameters Intercept of allometric mass function Aa 0.1 slope of allometric mass function Ba 0.149 QlO approximation Ca 0.149 Diet Energy Density Zooplankton Energy Density Ed (J/g02) .. Ed 2500 Egestion and Excretion Proportion of consumption egested Af 0.2 Proportion of (consumption-egested) Ae 0.07 Specific Dynamic Action SDA 0.163 Table 2.2: Parameter values used in northern pikeminnow bioenergetics model from Petersen and Ward (1999) Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 23 ature profiles were taken at mid-day from fixed stations at two-week intervals over the summer and the input temperatures for the simulations were inte grated over the first meter of the water column. The choice of depth to measure temperature was consistent with observations of fry position and those of Barfoot et al. (1999) and Gadomski et al. (2001) showing fry prefer ence for shallow warm water. Temperatures between observations were linear interpolations of the observed temperature. A number of additional parameter assumptions were needed in order to completely parameterize the model. Lacking data on swimming speed of fry or any published functional relationship, I set swimming speeds of lar vae in terms of body length per second to those of the northern squawfish's congener the Colorado pikeminnow Ptychocheilus lucius. Bainbridge (1958) measured the sustained swimming speed of 30, 43 and 52 mm TL for Col orado pikeminnow as 4.00 body lengths per second. Similar speeds for larval Colorado pikeminnow were measured more recently by Childs and Clarkson (1996) across a range of temperatures. I assumed the swimming speed of northern pikeminnow 0+ fish to be the same as Colorado pikeminnow in terms of body lengths per second and used the von Bertalanffy predictions of length-at-age (chapter 3, table 3.2) calculated over daily rather than annual time steps. Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow Figure 2.2: Mean temperature integrated from lake surface to 1 m in depth for Dad's Lake (squares) and Mom's Lake (diamonds). Lines represent linear interpolations between observed temperatures Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 25 2.2.6 Lake feeding load Following Walters and Post (1993), I measured the effective density De of northern pikeminnow per hectare in each lake summed across ages a as This metric assumes the 'effective density' (Post et al., 1999; Walters and Post, 1993) of any age class in a size' structured predator (or competitor) on the prey population is the product of two length-dependent factors: the predator gape size and swimming speed. Such a metric was necessary to compare the effective density of those lakes with many small fish versus those with fewer larger ones. Since lakes differed in productivity, I scaled Eq. 2.2 to relative productive inputs as approximated by measured mean seasonal chlorophyll A in p,gL~l, p,gChlAL~x so that the standardized effective density Ds was calculated as n De oc ^ l2ha -l (2.2) n DsocJ2 l2harl[igChlA-xL. (2.3) a-l Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 26 2.3 Results 2.3.1 Spawning and Visual Surveys I observed large spawning aggregations in the outflow creeks of Cheryl, Moose Pasture, Tasha, Nestor and Mom's lakes over large cobble. Even though suitable cobble and flow rates were available in the inflows of Cheryl, Mom's, Nestor and Wilderness lakes, no fish were ever observed or captured in fishing gear in these inflow creeks. I observed no fish spawning in the outflow creek of Dad's Lake although the outflow creek of this lake is dammed so it would not have been possible for large numbers of northern pikeminnow from Dad's lake to actually form spawning aggregations there. Hatching northern pikeminnow are poor swimmers ?? and apparently unable to swim upstream into head-end lakes from outflow creek spawning areas. Hence the fry drift downstream to develop in the nursery lakes (Dad's, Moose Pasture). There were fry and juvenile northern pikeminnow only in Dad's, Moose Pasture, North Island, Tasha and Estelle lakes (Fig. 2.1). Fry appeared in schools varying between 5-1000 individuals along the littoral area by early August. They preferred the very shallow margins of the lakes in water gen erally no deeper than 10 cm, with some plant cover. Such schools were only visible at mid-day and at warm temperatures. Fry were only present in those lakes where there was a lake upstream with northern pikeminnow. Both Mom's and Cheryl lakes have lakes upstream of them, but these up-Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 27 stream lakes have no northern pikeminnow. Northern pikeminnow in both cases have no access to the upstream lakes due to small waterfalls. 2.3.2 Apparent mortality The apparent M was similar in all lakes except for Wilderness. Since move ment should appear as higher apparent mortality, represented by the slope of the length-converted-catch curve, population estimates in Fig. 2.3 showed that most fish must move before the age of 5+. There were very high num bers of 1-3+ age classes in the two nursery lakes, and correspondingly few or none estimated in the head-end lakes. If movement were occurring in fully recruited age classes, the apparent mortality would be significantly higher in the Moose Pasture and Dad's lakes. 2.3.3 Hydrography and Productivity The two nursery lakes were both more productive with respect to their mean \igChlAL~1 values than the head-end lakes in their respective drainages (Fig. 2.4). The difference is particularly striking in the case of Dad's lake. Here the mean chlorophyll A was 23.59 u,gL~l compared to values of 3.29 and 3.41 fj,gL~l in Mom's and Nestor lakes. In the case of the eastern drainage this difference was much smaller with the nursery lake (Moose Pasture) having a mean Chi A of 2.92 ngL~l compared to 2.29 and 2.12 in Wilderness and Cheryl lakes respectively. The effective density of fish in the nursery lakes Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 28 Figure 2.3: Maximum likelihood estimates of numbers at each length con verted age. The pasted text is the slope of the fit line through the log numbers at age (log Na) representing the apparent mor tality of fully recruited ages (5+) Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 29 < JZ O o o oo o c\i "i 1 r Jul Aug Sep Oct Date Figure 2.4: Chlorophyll A (//gC/iML-1)measurements over time. Top panel is Western drainage: Dad's Lake (squares), Mom's Lake (dia monds) and Nestor Lake (triangles). Bottom panel is Eastern drainage: Moose Pasture (squares), Cheryl Lake (diamonds) and Wilderness Lake (triangles). Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow is correspondingly very high (Fig. 2.5 top panel). So while the productivity of the nursery lakes is higher than the head-end lakes (Fig. 2.4), once it is partitioned among the greater number of mouths in Dad's and Moose Pasture, these lakes are on par or (in the case of Dad's), have even higher Dc that the headwater lakes (Fig. 2.5 bottom). The nursery lakes also have a greater proportion of shallow littoraf area, the preferred habitat of the northern pikeminnow juveniles. Greater than 60 % of the cumulative area of Dad's and Moose Pasture lakes is in water between 0 and 3 m (figure 2.6). 2.3.4 Bioenergetics predictions The model showed that it was physiologically possible for fish to hatch as many as 50 days after the nursery hatch date and still be the same size the one year later. In order to do so however, very large increases in Phead were needed (Fig. 2.9 top). Interpreted in a behavioral sense, those fish hatched in inflow creeks would have to spend more time feeding relative to those hatched earlier in outflows (Fig. 2.9 bottom) in order to be the same size one year later and most of that feeding would have to take place before winter (Fig. 2.7). Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 31 Figure 2.5: Effective density per hectare as represented by the sum of squared fish lengths l 2ha~ l (top) Effective density per hectare per figChlAL -1 as represented by the sum of squared fish lengths per hectare Z2/ia_1 divided by mean ChlA (figL~ l for Dad's (d), Moose Pasture (p), Mom's (m), Cheryl (c), Nestor (n) and Wilderness (w) lakes Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow Depth contour Figure 2.6: Proportion of the total lake area by depth contour, Dad's open circles, Mom's open squares, Nestor, open diamonds, Moose Pas ture closed circles, Cheryl closed squares, Wilderness closed dia monds Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 33 0 100 200 300 Day of Hatching Figure 2.7: Predicted weights (in grams) of fit bioenergetics model to ob served weight at age in the nursery area (open circles, P = 0.14) and the predicted weight at age of a fish hatched 15 days later in the head lake (solid line, P â€” 0.18) Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 34 50 100 150 200 250 Fork Length (mm) Figure 2,8: Fit weight-length relationship of northern pikeminnow weight as a function of length. Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 35 Figure 2.9: Predicted proportion of maximum consumption rate Phead (top) required to reach observed size at age 1 and Phead/Pnursery (bot tom) vs. delays in headwater lake hatch date. Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 36 2.4 Discussion I show that fish undergo large-scale ontogenetic shifts between lakes. No fry were ever observed in non-nursery lakes. In addition, the differences in the age structures of the nursery lakes and head end lakes indicate migration occurs between the ages of 1 and 5+. The only distinctive feature of the nursery lakes is the presence of a lake containing northern pikeminnow above it. Note that both Cheryl and Mom's lake have lakes in the drainage above them (Fig. 2.1), but neither of these has northern pikeminnow. This pattern holds at a reasonably large scale and in two river drainages. The ratio of effective density to ChlAL~x as an index of the relative pro ductivity of the lakes is very important for determining the distribution of the adults. Any advantage of the additional productivity of Dad's Lake or Moose Pasture is eliminated by the very high density of northern pikeminnow there. Dad's Lake is apparently much more productive than any of the other lakes but the benefits of such high productivity are completely neutralized by the higher density of fish there. While Moose Pasture Lake was not significantly more productive than any of the headwater lakes, the ratio of l2ha"1pJgChlA~1L makes that lake a much worse lake to rear in than those head-end lakes near it. Contrary to the situation with Dad's, the lakes above Moose Pasture are actually larger and support more adult fish, so that rela tive to its size and productivity, Moose Pasture receives many more fry than Dad's does. Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 37 The bioenergetics modeling shows the most likely reason for the spatial distribution of fry is temperature dependent spawning behavior, rather than productivity and hydrographic differences between the lakes. While I did not have stream temperature data to support this argument directly, it is reason able to assume that the inflow creeks temperature to be approximately the same as the mean annual air temperature (2-5 C) for this Montane Spruce biogeoclimatic Zone (?) and the outflow creek temperature to be the same as the lake temperature. If the proportion of the maximum consumption rate is interpreted in a behavioral sense (a higher proportion of the maxi mum consumption rate is equivalent to greater time spent in risky foraging behavior instead of hiding and growing) then delays in spawning are paid for by increasing predation risk. A delay of 25 days corresponds to doubling this risk. Natural selection predicts strong selection against such increased risk taking. Furthermore, the results are optimistic predictions of growth and spawning potential in the head-end systems. Inflow creeks go dry in low rain/snow years by the end of July. So while it might be possible to rear in a head-end lake and still reach the same size as in a nursery lake as late as fifty days after spawning in an outflow creek, there may be no inflow creek left to hatch/emerge from. The bioenergetics predictions should be viewed with considerable caution. These predictions depend on two assumptions not tested and likely incorrect. The Petersen and Ward (1999) parameter values come from adult fish in the Columbia river system. Fish in the study system are very different to those Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 38 in the Columbia. The fish in this study system are much smaller than in the Columbia, reaching asymptotic lengths of 200 mm, compared to the maximum size of 350 mm+ observed in the Columbia. Whether or not these differences are the result of phenotypic plasticity or genetic differences is not known. Local physiological adaptations have been shown to make large difference in the bioenergetics parameters (Munch and Conover, 2002). Secondly, the predictions rely on the assumption that the parameters are similar between adults and juveniles which is also incorrect (Post, 1990). That said, the purpose of the modeling exercise was to determine how much addition consumption would be required in order to compensate for later spawning. The temperature profiles in each lake were almost identical so any biases in P produced by incorrect parametrization would be consistent between nursery and head areas so the comparison between the two is still legitimate. The number of growing degree days seems to limit the northern distribu tion of perch and bass species (Schuter and Post, 1990). Norther pikeminnow fry in the study area likely face a similar growth survival trade-off to that observed in rainbow trout studies 200 km South of the study area. Post and Parkinson (2001) show rainbow trout in small B.C. lakes face a tradeoff between allocating energy to somatic growth or to lipids. Energy allocated to somatic growth improves fitness of larger individuals by reducing size-dependent predation risk but at the expense of lower winter survival. Post and Parkinson (2001) showed that once fish reach a size large enough to Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 39 reduce their predation risk, they allocate resources to lipid stores for win ter survival rather than to somatic growth. For both reducing predation and for storing lipids to survive winter early hatching is critical for northern pikeminnow. The spatial organization of these stocks of northern pikeminnow is similar to that observed in river systems with respect to the habitat preference for rearing areas. Gadomski et al. (2001) described a model of early life history in the Columbia River. In it, adults spawn in tributaries at 18-20 C, planktonic larvae drift into the mainstem and then rear in backwaters with fine sediment or sand substrates. Our observations are identical, except that the preferred areas for rearing are entire lakes, not river backwaters. How unit stocks are defined spatially needs closer examination in lacus trine systems, especially where lakes are not isolated from each other. Theory predicts ontogenetic movement should be widespread in size-structured pop ulations. In addition, there are both excellent theoretical and field examples of it in fish populations. In response to different resources gradients, shifts occur particularly in situations where adults present a predation risk to juve niles (Persson and Greenberg, 1990; Gowen et al., 1994; de Roos et al., 2002). However the scale of such modeling and field studies tends to be small, that is, within lakes. In the study systems there are productivity (ChlA) and temperature gradients between upper end and nursery lakes. Watershed sys tems in general have such gradients on larger (multi-lake) scales (Gomi et al., 2002), and in my watersheds fish should have no difficulty distributing them-Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 40 selves at such scales, provided streams are seasonally adequate to permit movement. Examples of fish movement at larger scale are appearing in the literature. Naslund (1990) showed spectacular density-dependent migrations between lakes of arctic char. Movement from streams to lakes has also been observed (Olsson and Greenberg, 2004). Contrary to the "restricted move ment paradigm" (Gerking 1959), there is an increasing number of examples where movement in streams is significant (Gowen et al., 1994) and references therein) and many examples supposedly confirming the restricted movement paradigm use methods biased against detecting any such movement (Gowen et al., 1994). Juvenile fish living in seasonal environments have to choose life-history strategies that allow them maximize their growth advantage while not ex posing themselves to significant predation in order to do so. I show here that in addition to solving the small space/time scale problem of balancing growth with predation risk, northern pikeminnow must also solve a larger space/time scale problem of choosing life-history strategies that are phys iologically favorable, in terms of allowing for the greatest amount of time to grow. Since there are large scale gradients in productivity and tempera ture between lakes, and in many cases relatively simple connections between them, the applied implication is that the initial survey effort in lacrustine systems should be distributed widely before assuming that lakes consist of individual stocks. We typically assume that ontogenetic life-history movements are shaped Chapter 2. Ontogenetic Habitat Shifts Between Lakes by the Pygmy Pikeminnow 41 by selections on a variety of phenological (timing), bioenergetic, and be havioral traits so as to maximize fitness given local environmental condi tions. But in the stunted pikeminnow case, we may simply be seeing two key preadaptations, a minimum temperature for spawning, and a tendency to disperse upstream from crowded areas. Just the minimum temperature trait would lead to avoidance of inflow spawning in headwater lakes and hence to downstream fry dispersal. All that would be needed for the observed drainage wide organization is upstream return later' in life. 2.5 Appendix age 04-Jul 31-Jul 01-Aug 10-Aug 13-Aug 21-Aug 22-Aug 28-Aug 06-Sep 10-Sep 17-Sep 25-Sep 1 0 0 0 0 0 0 0 0 0 0 0 0 2 0 0 27 25 0 0 0 39 0 0 0 0 3 0 0 64 85 0 0 0 191 0 0 0 0 4 0 0 8 49 0 0 0 8 0 0 0 0 5 70 0 25 69 0 0 0 9 0 0 0 0 6 90 22 41 0 0 0 3 0 0 0 0 7 51 0 11 26 0 0 0 2 0 0 0 0 8 29 0 5 11 0 0 0 0 0 0 0 0 9 25 0 0 13 n 0 0 2 0 0 0 0 10 23 0 1 6 0 0 0 2 0 0 0 0 11 14 0 0 7 0 0 0 0 0 0 0 0 12 10 0 0 5 0 0 0 1 0 0 0 0 13 5 0 0 5 0 0 0 0 0 0 0 0 14 3 0 0 2 0 0 0 0 0 0 0 0 15 7 0 0 6 0 0 0 0 0 0 0 0 16 + 24 0 1 15 0 0 0 1 1 0 0 Killed 1 0 0 0 0 0 0 0 0 0 0 0 0 2 0 0 0 U 0 0 0 0 0 0 0 0 a 0 0 0 0 0 0 0 0 2 0 0 0 4 0 0 0 0 0 0 0 0 3 0 0 0 5 0 2 0 0 0 0 0 0 . 1 0 0 0 G 0 2 0 0 0 0 u 0 4 0 0 0 7 0 2 0 0 0 u 0 0 2 0 0 0 8 1 3 0 0 0 0 0 0 0 0 0 0 U 1 1 u 0 0 0 0 0 0 0 0 0 10 0 0 0 0 0 0 0 0 1 0 0 0 1 0 2 0 0 0 0 0 0 0 0 0 12 0 1 0 0 0 0 0 0 0 0 0 0 13 0 0 0 0 0 0 0 0 0 0 0 0 14 0 1 0 0 0 0 0 0 0 0 0 0 15 0 0 0 0 0 0 0 0 0 0 0 0 10+ 0 0 0 0 0 0 0 0 0 0 0 0 Recaptured 1 0 0 0 0 0 0 0 0 0 0 0 0 2 0 0 0 0 0 0 0 1 0 0 0 0 3 0 0 0 0 4 4 0 0 0 4 0 0 0 0 0 0 0 0 5 0 1 0 5 0 1 0 5 0 0 0 2 13 1 â€˘ 0 1 6 0 0 4 0 0 0 0 15 0 0 2 7 0 1 0 4 0 0 0 0 7 0 0 0 8 0 1 1 2 1 0 0 0 11 0 0 1 9 0 1 0 0 0 0 0 1 5 0 0 0 10 0 0 0 5 0 0 0 0 3 0 0 0 11 0 1 0 0 n 0 1 0 4 0 0 0 12 0 1 0 0 0 0 0 0 3 0 0 0 13 0 0 0 0 0 1 0 0 1 0 0 0 14 0 1 0 2 0 0 0 0 1 0 0 0 15 0 0 0 1 0 0 0 0 2 0 0 0 10 + 0 0 0 1 0 2 0 0 17 0 0 0 Unmarked 1 0 0 0 1 0 0 0 0 0 0 0 0 2 0 0 27 25 0 0 0 53 27 0 0 1 3 0 0 05 103 0 0 0 218 374 0 0 22 4 2 0 8 93 0 0 0 9 150 0 0 4 5 74 50 25 163 0 16 0 9 235 u 10 18 0 98 10G 22 109 0 12 0 3 176 0 23 13 7 51 55 11 56 0 2 0 2 59 0 2 11 8 31 31 5 28 0 1 0 0 26 0 0 8 9 27 29 0 29 0 0 0 2 10 0 2 5 10 24 13 1 15 0 1 0 2 12 0 0 6 11 10 9 0 13 0 0 0 0 7 0 0 0 12 10 9 0 10 0 0 0 1 5 0 0 5 13 5 2 0 9 0 0 0 0 3 0 0 2 14 5 0 0 4 0 0 0 0 2 0 0 0 15 8 4 0 7 0 0 0 0 3 0 1 2 10+ 33 27 1 26 0 0 0 1 14 0 2 13 Q I 4^ to Table 2.3: Table of fish marked, marked fish killed during handling, recaptured, and unmarked by date and length-converted age in Dad's lake. age 20-Jun 26-Jun 30-Jul 31-Jul 12-Aug 22-Aug 2 7-Aug 08-Sep 23-Sep 2 1 0 0 0 0 0 4 0 0 3 7 0 0 0 10 0 18 0 0 4 15 12 0 0 3 0 0 0 0 5 8 30 0 0 1 0 1 0 0 0 5 12 0 0 0 0 0 0 0 7 3 8 0 0 1 0 0 0 0 S 8 0 0 0 0 0 1 u 0 i) 5 0 0 0 0 0 0 0 0 10 1 2 0 0 0 0 0 0 0 11 1 4 0 0 0 0 0 0 0 12 1 1 0 0 0 0 0 0 0 13 1 3 I) 0 0 0 0 0 0 14 0 1 0 0 0 u 1 0 0 15 0 1 I) 0 0 0 0 0 0 10 + 4 a â€˘"' 0 0 0 u 0 0 lecaptured 2 U 0 0 0 0 0 0 0 0 3 0 2 0 0 0 0 1 10 0 4 0 0 1 u 0 0 0 0 0 5 0 7 2 0 0 0 0 4 0 0 0 3 3 0 1 1 0 12 0 7 0 4 0 0 1 1 u 15 0 8 0 8 0 0 0 0 u 8 0 9 0 5 0 0 0 4 0 1 0 10 0 2 0 0 0 1 0 2 0 11 0 3 0 1 0 1 0 1 0 12 0 0 0 0 1 0 0 1 0 13 0 4 2 7 2 6 0 2 0 14 0 0 0 0 0 0 0 0 0 15 0 0 0 0 0 0 0 0 0 10 + 0 1 0 0 0 0 0 0 0 Unmarked 2 1 0 0 0 0 0- 4 0 0 3 7 1 0 0 10 0 18 3 0 4 17 13 0 0 3 0 0 0 0 5 9 39 5 0 1 0 1 1 1 G 5 13 G 0 0 0 0 1 8 7 3 10 U 0 1 1 0 1 1 8 8 0 0 0 0 2 1 0 2 D 5 G 0 1 0 0 0 0 2 10 1 3 1 0 0 0 0 0 0 11 1 4 1) 0 0 0 0 0 0 12 1 1 0 1 0 0 0 0 0 13 1 3 0 0 0 0 0 0 0 14 0 1 0 0 0 0 1 0 0 lo 0 1 0 0 0 0 0 0 0 10 + 4 13 1 2 u 1 0 30 1 Q Table 2.4: Table of fish marked, marked fish killed during handling, recaptured, and unmarked by date and length-converted age for July, August and September 2002 in Mom's lake. o 4^ CO Marking age 2 6-Jun 06-Jul 14-Jul 15-Jul 23-Jul 24-Jul 25-Jul 26-Jul 2 0 0 0 0 0 0 0 0 3 1 0 0 0 0 0 0 0 4 14 8 0 0 0 0 0 0 5 44 50 1 11 0 0 0 0 (i 36 52 0 13 1 0 0 0 7 25 44 1 3 0 0 0 1 8 19 35 2 I 0 u 0 1 9 10 27 0 0 0 0 0 0 10 9 13 0 0 0 0 0 0 11 8 12 0 0 0 0 0 0 12 2 9 0 0 0 0 0 1 13 2 5 0 0 0 0 0 0 14 3 6 0 0 0 0 0 0 15 0 2 0 0 0 0 0 0 16 + 5 10 0 1 0 0 0 1 Killed 2 0 0 0 0 0 0 0 0 3 0 0 0 0 0 0 0 0 4 0 0 0 1 0 0 0 0 5 0 0 0 1 3 0 0 0 6 0 0 0 0 2 2 0 1 7 0 0 0 2 10 6 3 2 8 0 0 0 0 15 6 3 1 9 0 0 0 0 14 0 0 1 10 0 0 0 0 13 6 2 1 11 0 0 0 0 12 8 0 1 12 0 0 0 0 3 2 0 1 13 0 0 0 0 5 2 0 0 14 0 0 0 0 2 0 2 1 15 0 0 0 0 2 0 0 1 10+ 0 0 0 0 4 0 0 0 Recaptured 2 0 0 0 0 0 0 0 0 3 0 0 0 0 0 0 0 0 4 0 0 0 1 0 0 0 0 5 4 8 0 1 2 0 0 0 0 6 6 0 3 4 0 0 0 7 1 4 2 2 2 4 2 1 S 0 4 0 2 10 4 2 2 9 0 3 1 1 14 4 2 0 10 2 7 0 0 16 2 0 1 11 0 4 1 0 12 2 2 2 12 0 2 0 0 4 0 0 0 13 0 1 0 0 16 8 0 0 14 0 2 0 0 2 4 0 0 15 0 0 0 0 4 2 2 1 16 + 0 1 0 0 16 10 2 5 Unmarked 1 0 0 0 0 0 0 0 0 2 0 0 0 0 0 0 0 0 3 1 0 0 0 0 0 0 0 4 14 8 0 3 0 0 0 0 5 44 52 3 26 2 0 4 0 6 36 52 7 33 18 4 6 1 7 25 44 1 6 50 12 3 3 8 19 35 3 3 58 2 9 5 9 10 27 0 1 14 4 0 0 10 9 13 0 0 16 12 0 1 11 8 12 3 0 14 0 2 2 12 2 9 0 0 6 4 2 3 13 2 5 0 0 4 0 0 0 14 3 0 0 0 6 0 0 0 15 0 2 0 0 0 0 1 1 10 + 5 11 0 1 10 10 2 4 Table 2.5: Table of fish marked, marked fish killed during handling, recaptured, and unmarked from June to August 2002 by length-converted age in Nestor lake. Marking age Ol-Aug 12-Aug 13-Aug 20-Aug 21-Aug 22-Aug 23-Aug 27-Aug 07-Sep 18-Sep 24-Sep 200 0 00 0 00000 000000000 0 00 000200 0 0 0001 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 18 0 0 0 0 0 0 0000 15 00000000 000700003000 000 '100000000 00010 0 000000 000000000000 000 2 00000000 0000 0 0000000 000000000000 Killed 2 00000000000 000000000000 2 ODOO 10000 5 01 0 0 0 0 2 3 1 0 0 1 0 1 01001 1100100 00 0 071 100001 0 0 0 0 14 2000000 0 0 0 0 5 1 0 o-o 0 0 0 0000 GO 0 0000 0 5 0000000 000000000000 0 0 0 0 10.0 0 0 0 0 0 00000 0 0 00 0 0 1G+ 00 0 100000 0 0 Recaptured 2 0 0 0 0 0 0,0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 00 0 0 0 0 0 0, 0 0 0 0 1 1 2 1 3 0 0 ()' 0 0 2 1 3 0 7 0 1 0 0.0.0 0 G 0 1 04052210 0 4 0 3 1 1 1 1 1 2 00 0 300 02013110010 2 0002 11 0 100010 000282000000 0000G 2 000000 0000 2 0000000 010050000000 0 0 0 0 1 0.0 0 000 0 0 0 0 0 7 00 00 0 0 Unmarked 000000000000 0 000000000100 000200000301 0 13 0 9 0 1 0 00904 0 15 0 18 4 3 1-2 1 10 1 15 0 12 0 15 7 9 3 5 0 13 3 28 0 3 0 7 14 14 0 9 1 9 1 6 0104 12 4080 5 1 0 0 0 1 20 3 0 4 0 1 0 2 0 1 0 0 14 0 0 4 0 0 0 0 0 0 0 2 5 1 1 1 0 0 00000 5 1010000 000011110000 Q I 0010000 0 00 jljj Table 2.6: Table of fish marked, marked fish killed during handling, recaptured, and unmarked from to September 2002 by length-converted age in Nestor lake. August Marking 04-Jun 18-Jun 27-Jun 08-Jul 10-Jul 02-Aug 07-Aug 08-Aug 16-Aug 18-Aug 19-Aug 22-Aug 1 0 0 0 0 6 1 0 4 0 0 0 1 2 3 0 0 4 3 2 8 145 0 19 142 47 3 3 3 4 0 1 0 85 28 0 9 31 10 4 0 32 2 1 0 0 71 12 0 1 26 23 5 0 14 2 0 0 0 13 4 0 0 19 0 6 0 16 3 0 0 0 8 2 0 0 8 n 7 0 17 1 0 1 0 4 2 0 0 6 0 8 0 21 0 0 0 1 10 0 0 0 9 0 9 0 13 1 0 0 0 2 0 0 0 4 4 10 0 7 2 0 0 n 4 0 0 0 1 5 11 0 5 0 0 0 0 1 0 0 0 0 0 12 0 1 0 0 0 0 2 0 0 0 0 0 13 0 4 0 0 0 0 2 0 0 0 0 0 14 0 2 0 0 0 0 1 0 0 0 1 0 15 0 1 0 0 0 0. 1 0 0 0 0 0 16 + 0 12 1 0 0 0 10 0 0 1 1 1 Killed or Removed 1 0 0 0 0 0 0 0 0 0 0 0 0 2 0 0 0 0 0 â€˘ 0 0 0 0 0 0 0 3 0 0 0 0 0 0 0 0 0 0 0 0 4 0 0 0 0 0 0 0 0 0 0 0 0 5 0 0 0 0 0 0 ' 0 0 0 0 0 0 0 0 0 0 0 0 n 0 0 0 0 0 0 7 0 0 0 0 0 0 0 0 0 0 0 0 8 0 0 0 0 0 0 0 0 0 0 0 0 9 0 0 0 0 0 0 0 0 0 0 0 0 10 0 0 0 0 0 0 0 0 0 0 0 0 11 0 0 0 0 0 0 0 0 0 - 0 0 0 12 0 0 0 0 0 0 0 0 0 0 0 0 13 0 0 0 0 u 0 0 0 0 0 0 0 14 0 0 0 0 0 0 0 0 0 0 u 0 15 0 0 0 0 0 0 0 0 0 0 0 0 16 + 0 0 0 0 0 0 0 0 0 0 0 0 ures 1 0 0 0 0 0 0 0 0 0 0 0 1 2 0 0 0 0 2 ' 0 0 1 0 0 1 8 3 0 0 0 0 0 0 2 1 0 0 9 8 4 0 0 0 0 0 0 3 1 0 0 10 17 5 0 0 0 0 0 0' 1 0 0 0 4 6 6 0 0 0 0 0 0 3 0 0 0 3 5 7 0 0 0 0 0 0 3 0 0 0 2 0 8 0 0 0 0 0 0 3 0 0 0 f> 11 9 0 0 0 0 0 0 3 1 0 0 3 13 10 0 0 0 0 0 0 2 1 0 0 2 5 11 0 0 0 0 0 0 4 0 0 0 1 4 12 0 0 0 0 0 0 3 0 0 0 1 5 13 0 0 0 0 0 0 0 0 0 0 0 1 14 0 0 0 0 0 0 3 0 0 0 0 4 15 0 0 0 0 0 0 1 0 0 0 0 4 10+ 0 0 0 0 0 0 5 0 0 0 3 10 rked 1 19 0 0 1 7 3' 0 4 7 0 0 10 2 7 0 0 4 3 2 14 148 0 24 147 509 3 3 0 4 0 1 0 190 28 0 2 51 50 4 0 33 2 1 0 0,., â€˘ 200 12 0 1 52 50 5 0 16 2 0 0 0 42 4 0 0 28 12 C 0 16 3 0 0 0 28 2 0 0 11 0 7 0 17 1 0 1 0 19 2 0 0 6 5 8 0 21 1 0 0 â€˘ 1 20 0 ' 0 0 9 10 9 0 13 1 0 0 0 10 0 0 0 5 4 10 0 8 2 0 0 0 10 0 0 0 1 8 11 u 5 0 0 0 0 7 0 0 0 2 4 12 0 1 0 0 0 0 3 0 0 0 0 2 13 0 4 0 0 0 0 6 0 0 0 0 3 14 0 2 0 0 0 0 3 0 0 0 1 3 15 0 1 0 0 0 0 2 0 0 0 0 0 16+ 0 12 1 0 0 0 19 1 0 1 4 17 Table 2.7: Table of fish marked, marked fish killed during handling, recaptured, and unmarked by length converted age from June to August 22 2002 in Moose Pasture Lake. Marking 23-Aug 25-Aug 09-Sep 10-Sep 11-Sep 13-Sep 14-Sep 15-Sep 16-Sep 27-Sep 1 1 0 0 0 0 0 0 0 0 0 2 8 0 0 0 0 0 0 0 0 20 3 0 0 0 0 1 0 0 0 0 0 4 0 0 0 0 ' 0 0 0 0 0 0 5 0 0 0 0 0 0 0 0 0 0 6 0 0 0 0 0 0 0 0 0 0 7 0 0 0 0 0 0 0 0 0 0 8 0 0 0 0 0 0 0 0 0 0 9 0 0 1 0 0 0 0 0 0 0 10 0 0 0 0 0 0 0 0 0 0 11 0 0 0 0 0 0 0 0 0 0 12 0 0 0 0 0 0 0 0 0 0 13 0 0 0 0 0 0 0 0 0 0 14 0 0 0 0 0 0 0 0 0 0 15 0 0 0 0 0 0 0 0 0 0 16 + 0 . 0 0 0 0 0 0 0 0 0 or Removed 1 0 0 0 0 0 0 0 0 0 0 2 0 0 7 6 3 18 1 1 0 1 3 0 0 113 17 10 31 0 1 0 0 4 0 0 134 13 5 15 0 0 0 0 5 0 2 25 9 4 6 0 0 0 0 6 0 0 23 4 3 3 0 0 0 0 7 0 0 9 4 3 4 0 0 0 0 8 0 0 19 6 11 8 0 0 0 1 9 0 0 12 6 7 1 1 0 0 0 10 0 1 3 5 2 5 0 0 0 0 11 0 0 2 3 3 0 0 0 0 0 12 0 0 1 1 1 1 0 0 0 0 13 0 0 0 1 2 0 0 0 0 0 14 0 0 0 2 2 0. 0 0 0 0 15 0 0 1 1 0 0 0 0 0 0 16 + 0 0 0 5 4 0 0 0 0 0 Recaptures 1 0 0 0 0 0 0 0 0 0 0 2 3 0 0 6 3 23 7 6 0 5 3 0 0 56 17 15 28 2 3 0 1 4 0 0 71 13 5 16 1 1 0 0 5 0 2 13 9 3 7 0 0 0 0 6 0 0 12 4 1 3 0 0 0 0 7 0 0 4 ' 4 â€˘ 3 5 0 0 0 1 8 0 0 7 6 6 5 0 0 0 0 9 0 0 9 6 4 2 0 0 0 1 10 0 1 2 5 1 5 1 0 0 0 11 0 0 1 3 2 1 0 0 0 0 12 0 0 1 1 1 0 0 0 0 0 13 0 0 0 1 1 1 0 0 0 0 14 0 0 0 2 0 0 0 0 0 0 15 0 0 0 1 0 0 0 0 0 0 16 + 0 0 5 5 4 6 0 0 0 1 Unmarked 1 3 0 0 6 11 38 11 3 26 11 2 20 0 26 42 178 725 425 67 54 40 3 1 0 258 43 81 131 34 7 5 0 4 1 0 143 25 20 46 6 2 0 0 5 2 1 27 6 8 10 1 0 0 0 6 0 0 15 6 4 4 0 0 0 0 7 0 0 8 5 â€˘i 4 1 0 0 0 8 0 0 6 3 0 0 0 0 0 0 9 0 0 1 0 0 0 1 0 0 0 10 0 0 0 0 1 1 1 0 0 0 11 0 0 0 0 0 1 0 0 0 0 12 0 0 0 4 0 1 0 0 0 0 13 0 0 1 0 2 0 0 0 0 0 14 0 0 0 2 1 0 0 0 0 0 15 0 0 1 1 1 2 0 0 0 0 16 + 0 1 12 4 4 5 0 2 0 0 o Table 2.8: Table of fish marked, marked fish killed or removed during handling, recaptured, and unmarked by length converted age for August 23 to September 2002 in Moose Pasture Lake. Marking age 19-Jun 25-Jun 26-Jun or-jui 09-Aug 23-Aug 25-Aug OS-Sep 16-Sep 26-Sep 1 3 0 0 l 0 0 0 0 0 0 2 0 0 0 4 0 0 109 0 0 0 3 0 0 30 1 31 0 74 0 0 0 4 0 1 00 0 57 0 27 0 0 0 5 0 1 13 0 20 9 7 0 0 0 a 0 0 0 0 8 0 2 0 0 0 7 0 0 2 0 1 0 2 0 0 0 8 0 0 4 0 4 0 0 0 0 0 9 0 0 1 0 1 0 0 0 0 0 10 0 0 0 0 1 0 1 0 0 0 11 0 0 1 0 0 0 0 0 0 0 12 + 1 0 2 0 0 0 1 0 0 0 Killed age 1 0 0 0 0 0 0 0 0 0 0 2 0 0 0 0 0 0 0 0 0 0 3 0 0 0 0 0 1 0 0 0 0 4 0 0 0 0 0 0 0 1 0 1 5 0 0 0 0 0 0 0 0 0 0 6 0 0 0 0 0 0 0 1 0 0 7 0 0 0 0 0 0 0 0 0 0 8 0 0 0 0 0 0 0 0 0 0 9 0 0 0 0 0 0 0 0 0 0 10 0 0 0 0 0 0 0 0 0 0 11 0 0 0 0 0 0 0 0 0 0 12 + 0 0 0 0 0 - 0 0 0 0 0 Recaptures age 1 0 0 0 0 0 0 0 0 0 0 2 0 0 0 0 0 0 5 0 0 0 3 0 0 0 0 0 0 0 0 0 0 4 0 0 5 0 4 0 7 1 0 0 5 0 0 1 0 2 i 1 0 1 4 0 0 0 0 0 0 0 i 1 1 0 7 0 0 1 0 0 0 0 0 0 0 8 0 0 0 0 1 0 2 0 0 0 9 0 0 0 0 0 0 1 0 0 0 10 0 0 0 0 1 0 0 0 0 1 11 0 0 0 0 0 0 0 0 1 0 12 + 0 0 0 0 2 0 1 0 0 0 Unmarked age 1 3 0 0 2 1 0 0 0 0 0 2 0 0 0 4 1 0 120 1 0 1 3 0 2 143 1 31 0 86 6 0 4 4 0 1 118- 1 59 3 38 6 8 12 0 1 21 0 20 13 11 12 12 18 6 0 0 0 0 8 1 3 3 4 5 7 0 0 2 0 1 1 2 0 1 2 8 0 0 4 0 4 1 1 1 0 0 9 0 0 1 0 1 1 0 0 0 1 10 0 0 0 0 1 1 1 0 0 1 11 0 0 1 0 0 0 0 0 0 1 12 + 1 0 6 0 0 0 2 0 1 0 Table 2.9: Table of fish marked, marked fish killed or removed during handling, recaptured, and unmarked by length converted age from June to September in Cheryl Lake. Q râ€”) â€˘8 o OO Marking age 16-Jun 18-Jun 19-Jun 13-Jul 14-Jul 27-Jul 07-Aug 26-Aug 04-Sep 14-Sep 16-Sep 28-Sep 2 0 3 0 0 0 0 0 0 1 0 0 0 3 0 70 1 0 0 0 23 0 0 0 9 0 4 0 49 0 0 1 0 24 0 0 0 5 0 5 0 24 0 0 0 0 6 0 1 0 1 0 6 0 26 0 0 0 0 2 0 0 0 4 0 7 0 6 0 0 0 0 2 0 0 0 3 0 8 0 12 0 0 0 0 2 0 0 0 1 0 9 0 3 0 0 0 0 2 0 0 0 0 0 10 0 1 0 0 0 0 1 0 0 0 0 0 11 + 0 1 0 0 0 0 0 0 0 0 0 0 Recaptures age 2 0 0 0 0 0 0 0 0 0 0 0 0 3 0 0 0 1 0 0 0 0 0 0 0 0 4 0 1 0 0 0 0 1 0 0 0 1 0 5 0 1 0 0 0 0 1 2 2 0 0 1 6 0 0 0 0 1 0 0 1 1 0 0 0 7 0 2 0 0 0 0 1 0 0 0 0 0 8 0 0 0 0 0 0 1 0 1 0 0 0 9 0 0 0 0 0 0 1 1 0 0 0 0 10 0 0 0 0 1 0 0 0 ' 0 0 0 0 11 + 0 0 0 0 0 0 0 0 1 0 0 1 Unmarked age 2 0 3 1 0 0 0 0 0 5 0 0 24 3 7 82 1 0 c 0 25 0 12 0 9 6 4 5 53 0 0 1 0 24 12 18 1 5 1 5 1 25 0 0 5 0 6 17 10 2 1 1 6 4 28 0 0 0 6 ' 2 10 1 0 4 0 7 3 6 0 0 1 4 2 6 2 0 3 0 8 1 13 0 0 0 0 2 1 0 0 1 0 9 0 3 0 0 0 1 2 1 1 1 0 2 10 0 1 0 0 0 0 1 0 0 0 0 0 11 + 0 0 0 0 0 c 0 0 1 0 0 1 Table 2.10: Table of fish marked, marked fish killed or removed during handling, recaptured, and unmarked by length converted age from June to September in Wilderness Lake. Q to Chapter 3. Estimating Growth from Length At Age Data 50 Chapter 3 Estimating Growth from Length At Age Data Abstract Gear selectivity and cumulative effects of size-selective fishing bias length-at-age samples used to estimate the von Bertalanffy growth parameters. In fished populations, fast growing young fish and slow growing old fish are over represented in size-age samples. To account for such effects, I treated size-at-age observations as multinomial samples, with expected catches in each size-age category dependent on growth parameters, growth variation, size se lectivity, abundance at age, and the history of exploitation. Using simulated data sets, estimated growth parameters using the multinomial likelihood were unbiased when 'fishing mortality was not too high and the shape of the vul nerability function was correct. In contrast, estimated growth' parameters using a least squares approach over-estimated the metabolic growth coeffi cient (K) and under-estimated mean asymptotic length (Leo). I estimated growth parameters for the northern pikeminnow Ptychocheilus oregonensis as an example of the method and documented a stunted "pigmy" population with an L^ of 175 mm fork-length (FL), attributing its small size to effects of high density and/or a short growing season. keywords: growth estimation, von Bertalanffy, size-selective fishing, gear selection Chapter 3. Estimating Growth from Length At Age Data 51 3.1 Introduction Estimating parameters for the von Bertalanffy growth model assumes a rep resentative sample of lengths from each age class has been collected, then either fitting the growth function to length-age data directly or to data on changes in length between the time of marking and time of recapture such as Fabens (1965). This assumption can fail if the sampling process is size selective and there are cumulative effects of fishing on the distribution of size-at-age. Growth rates vary among individuals (Sainsbury, 1980; Burr and Doksum, 1980) and intensive size selective harvesting removes faster growing individuals. The result is that length-age samples are biased for larger fast growing young individuals, and biased for older slow growing individuals that avoided capture (Lee, 1912; flicker. 1969; Sinclair et al., 2002a). Almost'all length-age data sets collected for growth analysis involve size-selective cap ture methods that favor fast growing individuals. In addition, many come from populations that have historically been exposed to harvest so as to produce cumulative effects on size-structure at age (Hanson and Chouinard, 1992; Kristiansen and Svasand, 1998). In both cases, the result is a down ward bias in estimation of mean asymptotic length (Loo), upward bias of the metabolic growth parameter (K) and upward bias in the apparent age where length is zero tQ. Biased estimates of growth parameters will cause bias in mortality rate estimates (where length-age keys are used to convert length to age), bio-Chapter 3. Estimating Growth from Length At Age Data 52 logical reference points for management such as yield per recruit (Ricker, 1969; Parma and Deriso, 1990), and management actions (quotas for ex ample). Changes in size-selectivity over the course of a fishery complicate matters further, where size selectivity changes may be mis-interpreted as changes in growth rates. Sinclair et al. (2002b) documented changes in size selectivity for the Atlantic cod (Gadus morhua) fishery in the southern Gulf of St. Lawrence, and Sinclair et al. (2002a) noted that historical effects of temperature on measured annual growth increment and density-dependent increases in growth rate were relatively small in comparison to the effect of size selective mortality caused by the fishery. In some cases, researchers wish to solely estimate growth parameters de scribing the age structure of the current population available to harvest with the understanding that these growth parameters represent the remaining fish that are targeted, fn this case, the effects of size-selective fishing do not need to be accounted for. However growth parameters describing the harvested targeted population will change as vulnerability changes (as fishers target smaller fish for example). If a researcher wishes to estimate the potential growth under no harvesting or under managed selectivity changes (e.g. size limits), then growth parameters representing entire population are needed. Recently, Laslett et al. (2002) derived a likelihood function for analysis of growth data from tagging experiments, that accounts for individual variation in growth through variation in individual asymptotic lengths L^, measure ment errors, and possible changes in the von Bertalanffy metabolic parameter Chapter 3. Estimating Growth from Length At Age Data ' 53 K with fish age. Unfortunately, they follow previous workers (James, 1991; Palmer et al., 1991; Wang et al., 1995) in assuming away one of the most com mon sources of bias in growth data; they assume independence of sampled individual Lx and age despite much evidence that higher L^ (fast growing) individuals have a higher capture probability in fishing and sampling gear used to collect the length-age samples. To deal with non-independence of age and individual L^, likelihood func tions for the analysis of length-age samples should include parameters repre senting probabilities of capture-at-age and probabilities of capture-at-length (i.e., size selectivity). Where applicable, the cumulative effects of size selec tive harvesting on apparent growth should also be considered. In this paper, I derive likelihood functions that include size selectivity, mortality, and growth parameters based on the assumption that size-age data are sampled from a multinomial distribution. I derive four likelihoods: (1) a full likelihood and (2) a "reduced" likelihood using the conditional maximum likelihood esti mates for numbers at age instead of estimating total mortality, (3) a full likelihood that includes cumulative effects of F, and (4) a reduced likelihood with cumulative effects of F. I test the performance of these formulations with 100 simulated data sets, and show that they are better estimators of growth parameters than previous statistical models for growth data. Fi nally, I fit all four models to real length-at-age data from the pigmy northern pikeminnow (Ptychocheilus oregonensis) of south central British Columbia. Chapter 3. Estimating Growth from Length At Age Data 54 3.2 Methods 3.2.1 Likelihood derivation I assume that the basic data available for analysis consists of a matrix n^a with elements numbers of fish sampled at (discrete) lengths / and ages a, and that this is a random sample of the number of vulnerable fish of length I and age a available in the population to be sampled. In this case, the general form of the likelihood for nita given the parameter vector (O) used to predict nita is multinomial, and the log likelihood is the product of the data ni, a and the log of the predicted proportions pi<a of length I and age a: In L1(n\e) = Y,2Z ni,*HPi,a) (3.1) How the pi<a term of the likelihood is computed depends on which of the four likelihoods presented below is being used. 3.2.2 Model 1 growth with no history of fishing Where there has been no history of fishing, I calculate the predicted propor tions in the matrix piiU as the proportion of vulnerable numbers of fish at age a and length I (in mm fork length (FL)) in the total population VT of vulnerable fish. Pi,a = ViJVT, where VT = ]T ]T Vla. I a (3.2) Chapter 3. Estimating Growth from Length At Age Data 55 I begin by assuming that V[A can be expressed as the product of three factors: a size dependent vulnerability ui that depends on size I but not age, relative abundance Na of age a fish, and the conditional probability P(l\a) of being in a discrete length interval I given age a: Vla = viNaP(l\a). (3.3) I assume that vi has a functional form with increasing vulnerability at length "O = (1+e-V-.>) <") I describe the length at 50 % vulnerability (//,) as a fraction of L^ and a shape parameter (7) that describes the slope of the curve through lh (Deriso et al., 1985). If I assume a stable recruitment in the population, then relative numbers-at-age (Na) can be calculated using: Na = Re-M<a-1). (3.5) Equation 3.5 computes the exponential decay of older cohorts relative to an arbitrary recruitment rate R of age 1 individuals. The natural mortality rate M is estimated with the growth and vulnerability parameters using Eq. 3.1. Where the assumption of a stable recruitment fails, it can be relaxed in the reduced likelihoods described below. If I assume variation in growth among individuals of age a is caused Chapter 3. Estimating Growth from Length At Age Data 56 mainly by variation in individual asymptotic lengths L^^ (Wang et al., 1995), then the von Bertalanffy prediction of size at age for any individual i is L00tif(o) where the basic age effect /(a) is shared by all individuals i. Using the von Bertalanffy growth model this shared effect is described by: /(a) = 1 - e(-^Â«-*-))) (3.6) where K is the metabolic growth parameter and t0 is the theoretical time of zero length. Assuming that individuals with L^, present at the start of cohort life are drawn from a normal distribution with mean L^, and variance o^, any sub-cohort with a specific will follow a growth trajectory determined by the Loo,i with which they were born. This implies that the integral defining P(l\a) for each age a should be evaluated with mean la = Locf(a) and variance in mean length at age o\. 1 rl+d P(l\a) = j= \ exp CTav27T Jl-d where I is the length of the fish, d is half the length interval width, la is the mean length-at-age, and o~\ is the variance in length-at-age. In most species of fish, the absolute value of o~\ increases with age (o\ gets larger as a increases). In order to avoid estimating o\ for each age, I assume that standard deviation at age oa can be expressed as a simple function of the mean length at age la. This function can be la multiplied by some coefficient 2ol dl (3.7) Chapter 3. Estimating Growth from Length At Age Data 57 of variation (cv) which is assumed to be constant across all ages, or more complicated functions can be used, f chose to use equation 3.8 derived by Fournier and Sibert (1991). aa = Al6A2(-1+2^) (3.8) In this formulation p is the Brody growth coefficient (p = e^~K^), A, the num ber of ages, Ai represents the magnitude of the standard deviations at age a and A2 determines the length dependent trend in the standard deviations (if A2=0, the standard deviations are independent of length) (Fournier and Sibert, 1991). This formulation has the disadvantage of adding two param eters rather than one if o\ is expressed as cv * la. The rationale for using it however, is that it makes a less restrictive assumption about how oa changes as fish grow older, ft also reduces the covariation in the parameters by mak ing the standard deviation of length-at-age depend on one growth parameter (p = eK) rather than all three as it would if it were expressed as la * cv. 3.2.3 Model 2 reduced likelihood An option for avoiding the assumption of stable recruitment is to construct the model using the conditional maximum likelihood estimates for numbers-at-age Na and using these in the predicted sample proportions at length and age (pi,a) instead of the Na predicted by equation 3.5. This relaxes the as sumption of stable age structure which would be violated with highly variable Chapter 3. Estimating Growth from Length At Age Data 58 recruitment. Differentiating the log likelihood with respect to N-a, setting this derivative to zero and solving for Na gives the conditional maximum likeli hood estimates Na: <M> where TIT is the total of the number aged in the sample, na is the total number in the sampled aged a years, Vr the total vulnerable numbers from equation 3.2. The. value of va must first be calculated from the product of vulnerability-at-length and the conditional probability of being in length interval I given age a: *a = ÂŁ^(*|a)- (3.10) i which is the sum of the weighted mean vulnerability for age a, with vulner abilities at length weighted by P(l\a). If the prediction of Na from total mortality rate (equation 3.5) is replaced in the likelihood by these conditional maximum likelihood Na estimates (al lowing for any possible age structure in population being sampled), the mul tiplicative term ^ which does not vary with the parameters can be dropped (along with Vr) and p^a expressed as: Pl,a OC (3.11) instead of equation 3.2, so the reduced likelihood (L2) to be maximized with-Chapter 3. Estimating Growth from Length At Age Data 59 out M becomes: lnL2 oc X^zC7Vln a ( utP(l\a) a ) (3.12) 3.2.4 Model 3 growth under harvesting To model the effects of growth under harvesting, I again take the approach that n/i0 is a random sample from a population where ViA is the total number of vulnerable fish of length I and age a. The same general form of the likelihood function (equation 3.1) applies but a historical fishing rate (F) must now be incorporated into the estimated sample proportions pi>a. To do this I multiply each V/i(l element by a length and age specific survivorship ÂŁita that accounts for a growth pattern that exposes each individual fish to a possibly unique history of the cumulative impact of fishing and natural mortality. Absent temporal information on past variation in recruitment, natural mortality rate M, and overall (fully vulnerable ages) fishing mortality rate F, I treat these factors as having been stable for enough years to result in a stable age-size distribution. When a population has been subjected to a fishery, the numbers at each age cannot be described by equation 3.5 because each individual fish will be subject to a fishing mortality dependent on the growth trajectory of that individual. In this case, the Na component of ViA in equation 3.3 becomes Ni<a which must be computed for each I and a combination. Ni_a represents the survivors of fish that had individual Loo,i equal to ///(a), i.e. followed a growth pattern that subjected them to Chapter 3. Estimating Growth from Length At Age Data 60 cumulative instantaneous mortality (now including the fishing mortality F) at length and age: Zl,a = zZ{M + vl(6)F}, (3.13) d to give NUa = Re~z>>\ (3.14) where the sum (or integral) over d represents mortality over ages up to age a and where represents the time sequence of vi vulnerabilities seen by fish that followed the growth trajectory l& = L0Oiif(d) = [1/f(a)]f(d) over ages a. The initial recruitment can be set to R = 1 for convenience, since only the ratios of the Vitâ€ž, to total Vf appear in the likelihood function (the composition information ni>a carry no direct information on total population size). For typical vulnerability functions v(l) describing vi, there is no simple analytical solution for the sum or integral of values over ages d, but these sums can be easily evaluated numerically given any assumed form for p(l). This integral needs to be evaluated for all I, a combinations, since each such combination is assumed to have had a different and hence a different exploitation history. With a history of exploitation, the vulnerable numbers at age and length V^a are calculated as: Vla = viRe-Zl-'P{l\a) (3.15) Pita in equation 3.1 is now calculated with Via calculated using equation Chapter 3. Estimating Growth from Length At Age Data 61 3.15: Vla VlRe-z^P{l\a) = VT = Vr (3-16) so that the full likelihood (L3) that includes size selective fishing mortality is: -z, 2 a ' T The only numerically complex part of this growth under fishing formulation is computing the length-age specific survivorship (ez'-n) for each /, a element. Consider for example, the function in equation 3.4. Representing 1(d) as 1(d) = L00iif(d), then this age function can be substituted for lengths in the vulnerability function for all length intervals /. For example, the substitution for the vulnerability function in equation 3.4 is: uAd) = -. (3.18) which then has to be integrated over d and then multiplied by F in order to predict cumulative fishing mortality effects on the "subcohort" of fish that started life with asymptotic size L^^. For alternative vulnerability functions that are difficult to integrate (i.e. dome-shaped curves), I recommend simply summing the function over ages d from 1 to a, using a age steps of 1-year for long-lived fish and shorter steps (e.g. 0.5 year) for fish that live only a few years. Chapter 3. Estimating Growth from Length At Age Data 62 3.2.5 Model 4 Reduced likelihood with fishing Calculating the reduced likelihood in the fishing case is essentially the same as in the non-fishing case in the sense that the JVa's are replaced by their conditional maximum likelihood estimates. However, the cumulative effect of F on each I and a element must be included in the calculation Eq. 3.10 using Eq. 3.18 so that: Ua = Y,^i(&)Fp^\a)- (3-19) I Once this is done va gets updates automatically with changes with F. The Pi<a matrix now is computed as: Pia cx _ ' ; (3.20) and the reduced likelihood now including fishing becomes: lâ€žL4o< f^^y (3.2!) la \ Va ) 3.2.6 Simulations To test the derivations above I simulated data using known parameters (Table 3.2.6). Variation in past recruitment anomalies was included as log-normal process error with a mean of zero and standard deviation of 1 multiplied by a coefficient of variation CVR. Chapter 3. Estimating Growth from Length At Age Data 63 I compared the performance of the standard Fabens (after Rothchikl et al. (1989)) method that assumes'a representative sample of numbers-at-age and minimizes the sum of squares difference between predicted and observed lengths-at-age to the four models I derive above using simulated data. I generated 100 data sets with no fishing (F = 0), with a sustainable fishery (F = K) and an overfished population (F = 1). Fisheries where the fishing mortality has been stable for a long time are uncommon. Using the same parameters (Table 3.2.6) and a fully length-age structured simulation model, I tested models 3 and 4 with simulated data from stocks where F increased in increments of 0.1 per year for 5 years and where F was increased in increments of 0.1 per year for 10 years. For these cases, new recruits each year were assumed to have a fully representative distribution of individual asymptotic lengths (with mean L^ ^ and variance (Too computed with equation 3.8 evaluated at an infinite age ). Individuals of specific asymptotic lengths (Loo,i) across all ages were then exposed to fishing mortality every year according to the size (and hence v{) they were in that year. As in the simulations with stable fishing mortality, natural mortality was assumed constant and CVR was set to 0.5. The sensitivity of all of the models to changes in parameters used to simulate data were tested by using extreme parameter values. I conducted simulations with: the length at half vulnerability 4 set to 0.05*Loo and 0.9*Loo, knife-edged vulnerability (7 = 0.9 and with low variability in length at age (Ai set to 5). Finally I tested the models with a short lived, fast Chapter 3. Estimating Growth from Length At Age Data 64 Table 3.1: Parameters used to generate fake data. Parameter NT Value 1000 5 0.15 -0.25 0.2 0.6 0.1 Ax 16 A2 0.5 CVR 0.5 growing population with K = 0.7, M = 0.7. 3.2.7 Growth parameter estimation for northern pikeminnow I collected data for northern pikeminnow Ptychocheilus oregonensis from Moose Pasture lake located on the Bonaparte Plateau approximately 100 km north of Kamloops, British Columbia. I collected fish for ageing during a depletion experiment aimed at killing a high proportion of the population. Fish were captured during 6 bouts of fishing using four hoop nets. Three of these nets consisted of 6 m x 1 m fiberglass hoops covered in 1 cm mesh, 20 m center lead, and 15 m side leads. The other consisted of 6 m x 0.7 m steel hoops covered in 0.5 cm mesh, 15 m center lead, and 10 m side leads. Lapilli otoliths were taken from each fish and 945 were aged. I cut larger otoliths along the ventral/dorsal axis using an Isomet Bueller slow speed Chapter 3. Estimating Growth from Length At Age Data 65 saw, burned and counted annuli. Otoliths too small to cut were burned and counted directly. For fish older than 5 years, failing to cut otoliths along the long axis sometimes resulted in significant underestimates of age. During the three months preceding the depletion (9-15 September 2002), 1004 fish were tagged using 5 and 15 mm Floy numbered tags during four bouts of mark-recapture conducted at approximately 2 week intervals. Only those fish that were released in perfect condition are included in this analysis. Because the functional form of the vulnerability-at-length is unknown for fyke nets and northern pikeminnow, I used these tagging data to directly estimate vulnerabilities-at-length . I divided the fish into 5 mm size bins and estimated the gear selectivity for each bin using the likelihood described by Myers and Hoenig (1997). I include this analysis both to ensure that the functional form of the vulnerability-at-length has been specified correctly and to compare how well the vulnerability function estimated using only the length-at-age data and the multinomial likelihood(s) does relative to the direct estimates of vulnerability computed from the tagging experiment. 3.3 Results For the simulated data with no fishing mortality K was overestimated and Loo underestimated using Fabens method (Fig. 3.1). These biases were small (0.20% for K and negligible for Loo). There was still the common bias of a large negative to parameter which was underestimated by a factor Chapter 3. Estimating Growth from Length At Age Data 66 of two. With no fishing models 1,2,3 and 4 were unbiased for the growth, vulnerability parameters but slightly over-estimated M and in the case of model 3 F. The parameter bias using Fabens, models 1 and 2 worsened with increas ing F. With the Fabens method the bias was large and negative for to, small for K and negligible for Loo (Fig. 3.1). Model 1 accounted for the fishing mortality by over-estimating the natural mortality (Fig. 3.2) but could not account for the selective mortality on higher L^ individuals caused by fish ing and so underestimated Loo- Although model 2 suffered from the same bias in growth parameter estimates as model 1 did, models 3 and 4 were unbiased. Biases in parameter estimates were much worse where F â€” 1.0 for all but models 3 and 4 (Fig. 3.3). The bias in K, Loo and tQ was less severe for models 1 and 2 but in the same direction as Fabens. When fishing mortality was low, the distortion in the sample caused by F was compensated for by high estimates' of M (Fig. 3.2). This was not the case with high F (Fig. 3.3). Fishing mortality distorted the sample so much that the few older fish left were the small Loo,i (slow growing) individuals. Models 3 and 4 correctly estimated the von Bertalanffy growth param eters (Fig. 1) at all levels of stable fishing mortality. Even with moderate recruitment anomalies used to simulate the data (CVr=0.5), F was over es timated. This was the case at low F (although it cannot been seen due to the scaling of Fig. 3.1 and 3.2) and much worse at higher F (Fig. 3.3). Chapter 3. Estimating Growth from Length At Age Data 67 (e) U K t0 h X2 Y lh m F Figure 3.1: Proportional error in parameter estimates for each likelihood for mulation with F = 0. (a) Fabens, (b) model 1, (c) model 2, (d) model 3, and (e) model 4, (circles represent outliers). Chapter 3. Estimating Growth from Length At Age Data 68 (e) 1 1 o o e O T o x I I I I I I I I I U K t0 h ^2 1 lh m F Figure 3.2: Proportional error in parameter estimates for each likelihood for mulation with F = K. (a) Fabens, (b) model 1, (c) model 2, (d) model 3, and (e) model 4, (circles represent outliers). Chapter 3. Estimating Growth from Length At Age Data, 69 I I I I I I I I I U K t0 h X2 J lh m F Figure 3.3: Proportional error in parameter estimates for each likelihood for mulation with F = 1. (a) Fabens, (b) model 1, (c) model 2, (d) model 3, and (e) model 4, (circles represent outliers). Chapter 3. Estimating Growth from Length At Age Data 70 The performance of models 3 and 4 suffered with variable fishing. All the parameters were estimated well with 5 years of increased fishing (Fig. 3.4 a,c,e). But with 10 years of increased fishing, model 5 (Fig.3.4 f) performed as poorly was Fabens (Fig. 3.4 b) and model 4 was only slightly better (Fig. 3.4 d). At all levels of fishing, the models 2 and 4 were less precise than models 1 and 3. Models 2 and 4 do not assume a stable age distribution and so admit that more parameter combinations can explain the data. The reduced likelihoods effectively estimated relative recruitment of each age a cohort Rt â€” a. This means a additional parameters are estimated. While there is loss in precision of the parameter estimates, models 2 and 4 allow a much more honest acknowledgement of the uncertainty caused by recruitment variation in cases where a stable age structure is doubtful or unknown. All the models are sensitive to low values of //,. A very slowly sloping vulnerability (7 = 0.05) function had the same effect. Distortion in the data of younger age classes relative to fully represented ones needs to be present in the data for it to be possible to resolve the vulnerability parameters. For example, with no fishing, using the same growth parameters listed in Table 3.2.6 but with lh is equal to 0.05 of L^,, the data do not contain any infor mation about the vulnerability parameters and the result is mean biases of 300% for lh and 500% for 7. M is confounded with the vulnerability param eters and it is under-estimated by 0.28. Fortunately the growth parameters K, Loo and to are well estimated with mean bias of less than 5% bias. As is Chapter 3. Estimating Growth from Length At Age Data 71 I I I I I I I I U K t0 h \2 Y lh m F I I I I I I I I I U K t0 h X2 Y lh m F Figure 3.4: Proportional error of Fabens (a,b), model 3 (c,d), model 4 (e,f), where F increases in increments of 0.1 to F = 0.5 (a,c,e) and to F â€” 1.0 (b,d,f). F over time was estimated but the proportional bias is not included here since the true F used to simulate the data changed annually. Chapter 3. Estimating Growth from Length At Age Data 72 expected where with little size selectivity, the Fabens method actually per forms as well as likelihoods presented here because there is not significant distortion in length-age samples from either fishing or gear-selectivity. With no fishing and parameters again set to those listed in Table 3.2.6 but making lh = 0.9, the problem is that there are no fully represented age-classes in the length-age sample. The parameters Loo , K, ^2 and lh are all well estimated with biases less than 8%, but to, 7 and m are biased by 35, 21 and -40% respectively. As long as lh is an intermediate value, then the model is robust to steeply sloping vi (7 = 0.9) The simulated estimates were robust to data simulated with faster grow ing (moderately high K = 0.5) and faster dying (higher M = 0.6) population. But in populations where K and M are greater than about 0.7, fractional ages (half or quarter year) ages need to be used or the model performs badly and either underestimates K or fails to converge at all. These models break down when the shape of the vulnerability curve is not specified correctly, if fishing mortality is too large or if M is size or age-dependent, and with smaller length at age samples. If the actual vul nerability function is dome-shaped but an asymptotic function is assumed in the analysis, F is confounded with decreasing vulnerability of older/larger fish and becomes biased upward. Very high F is very destructive to the age structure of the population and no parameters can be estimated well. Where M is size or age dependent (where M decreases over age for example), there is severe confounding of M and F with the parameters that describe vi. At Chapter 3. Estimating Growth from Length At Age Data. 73 low sample sizes it is possible to have no data by random chance from either the faster growing younger fish (that help resolve v{) or older fish (that re solve M and F). With 25 age classes these models worked very poorly with fewer than approximately 500 observations. 3.3.1 Northern pikeminnow growth parameter estimates The five model fits to the northern pikeminnow data are plotted in Fig. 3.5. Parameters estimates are very similar for all of the models used. As they should, the likelihood formulations that include fishing (models 3 and 4) actually estimate a small fishing mortality in this population. Models 3 and 4 have a tendency to over-estimate the fishing mortality, but a non-zero value for this parameter is not as unreasonable as it might seem. The population is exposed to a small scale fishery from local lodge owners that have in the past conducted annual trapping programs during the spring spawn. Parameter estimates-from all four models are very similar (Table 3.3.1). Since this population was subject to some fishing in the past by fishing lodge owners in the area and because how stable recruitment has been is uncertain, the best model choice is the reduced likelihood with fishing. The vulnerability curve estimated by model five (Fig.6) is very similar to that fit using the mark recapture data. Fitting with model 5 appears to over-estimate the vulnerability at length for smaller size classes (Fig. 3.6) Chapter 3. Estimating Growth from Length At Age Data 74 Figure 3.5: Growth curves fit to northern pikeminnow data using all 5 mod els: solid=fabens, dashed=full likelihood, dotted=reduced like lihood, dotdash=full likelihood with fishing, longdash=reduced likelihood with fishing. Chapter 3. Estimating Growth from Length At Age Data 75 Table 3.2: Estimated parameter values for each model Parameter Fabens Model # 1 2 3 4 LQO 179.61 162.06 179.77 166.46 188.10 K 0.12 0.19 0.14 0.18 0.14 to -1.95 -0.41 -0.00 -0.38 -0.00 Ai 13.90 13.18 16.16 13.20 15.96 A2 0.69 0.65 0.60 0.61 0.57 h - 0.45 0.49 0.44 0.47 r - 0.21 0.20 0.19 0.19 z - 0.38 - 0.26 -F - - - 0.18 0.15 but otherwise seems a reasonable approximation (note that the parameter estimates for the vulnerability parameters in table 3.3.1 were similar for all models). Note that the vulnerability at length for the larger size classes is not well defined due to small sample sizes of tagged animals in those size bins. 3.4 Discussion The estimated Loo of northern pikeminnow is small compared to other doc umented populations of this species.. While the von Bertalanffy growth pa rameter (K) for' this population of northern pikeminnow is similar to- those published in the literature, the is much smaller. Northern pikeminnow have been studied extensively due to their predation on juvenile salmonids in a variety of systems such as Cultus Lake British Columbia (Ricker, 1941; Steigenberger and Larkin, 1974) and they are presently managed in Chapter 3. Estimating Growth from Length At Age Data 76 Figure 3.6: Plot of vulnerability curve (solid line) for northern pikeminnow estimated using likelihood 3 and direct estimates of vulnerability using mark-recapture. Chapter 3. Estimating Growth from Length At Age Data 77 the Columbia basin to reduce their impact on juvenile salmon (Friesen and Ward, 1999). Typical LM for this species are in the order of 400-600 mm FL (Parker et al., 1995) in the Columbia river basin and in Idaho lakes the average reported size of a sexually mature female approximately 440 mm TL (20 inches) for female and 300 mm (15 inches) for males Jeppson (1959). These values are well above even the maximum sizes observed in the study area. The reasons for their small size are presently unknown and could be density or environmental effects, but I hypothesize that it is mainly due to the short growing season (three months or so) that these fish experience. The simulations shown here are not unusual in showing the biases in the von Bertalanffy growth parameters (and corresponding yield per recruit analyses) due to gear selectivity and size-selective mortality on the estimation of growth parameters. These problems are well known (Deriso et al., 1985; Parma and Deriso, 1990; Sinclair et al., 2002b). The methods I present are original in using simulation studies to show the biases in estimates of both the von Bertalanffy parameters, the parameters describing size-selectivity, natural and fishing mortality and in presenting likelihoods that model these effects. Unlike Parma and Deriso (1990) and Sinclair et al. (2002b), I make no effort to include environmental effects or in the case of Sinclair et al. (2002b), density dependent growth. Parma and Deriso (1990) show that increasing the contribution of environmental factors have little effect on the variance in size at age relative to size-selective harvesting, and that most fisheries data contain little information about such effects. Sinclair et al. Chapter 3. Estimating Growth from Length At Age Data 78 (2002b) also determined that by far the largest effect on mean predicted L^ was size-selective mortality. I have shown it possible under a restricted set of assumptions to esti mate the von Bertalanffy growth parameters, M, F and the vulnerability parameters from only size-at-age data when other data from a fishery are not available. I caution that estimates of the vulnerability and mortality pa rameters should be considered very uncertain. Unfortunately, the sensitivity of the models to stable fishing mortality and known vulnerability shape re stricts the applicability of these models. Recall that the models are robust to an increasing fishing rate as long as the fishing mortality has not grown too rapidly. While the Fabens method performed almost equally as well in the case of growing F it did not tell the researcher anything about M or the vulnerability function vi. Of particular concern is the breakdown of the models following a very rapid increase in F. Having accurate assessment of the true growth parameters of the stock is particularly needed in order to assess the rebuilding potential of the stock in such situations. Fortunately, in many cases the reason for estimating growth parameters in the first place is that it is part of a larger stock assessment where F (and sometimes vi as in virtual population analysis ) is already estimated. This method could be applied in more complex stock assessments where nia tables can be provided for a collection of sample years. For each such table, the stock assessment model provides additional information on time-varying re cruitments Rt-a and fishing mortality rates F and in some cases (like virtual 1 Chapter 3. Estimating Growth from Length At Age Data 79 population analysis) vi. Assuming the n^a data are collected independently each year, the log-likelihood term for each of these tables can simply be added to the overall log-likelihood for the assessment model. The accounting (sum or integration) calculations for each Zia (cumulative mortality by size and age) are would require calculating the survival of those individuals growing along each L^ trajectory, but may carry valuable information on changes over time in F. A potentially important advantage of this approach would be to correct the problem that has plagued some past length-based stock assessment methods of ignoring cumulative effects of fishing on length distri bution patterns. Mean length and variability of length at age are explicitly variable and dependent on Ft in method 3 only, due to variation in Z^a. 3.5 Acknowledgements This manuscript was greatly improved by thorough reviews by an anonymous reviewer and Ana Parma. I greatly appreciate the help of an excellent field crew in the collection of otoliths consisting of Shaun McGloughlin, Hannah Murphy, Lew Coggins, Mike Melnychuk, and Eric Parkinson. I couldn't have gotten started without the expert advice from the Department of Fisheries and Oceans ageing lab at the Pacific Biological Station in Nanaimo, B.C., or finished without Angela Danyluk who did the bulk of the ageing. Financial support was provided by an NSERC operating grant and Pew Fellowship to C. Walters and by a Habitat Conservation Trust Fund grant to Eric Parkin-Chapter 3. Estimating Growth from Length At Age Data 80 son. Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 81 Chapter 4 Estimating movement and growth parameters given size-dependent spatial ontogeny Abstract I developed a likelihood to simultaneously estimate growth, natural mor tality, and gear selectivity parameters using change in length from tagging data. I combined this likelihood with two others for mark-recapture and for length-age data to estimate the von Bertalanffy growth parameters, natural mortality, gear selectivity and in some cases length-dependent movement pa rameters. Using simulation studies I showed that if a stable recruitment can be assumed it is also possible to estimate tag loss but that the assumptions required to do so are very limiting. The combined likelihood was not robust to large recruitment variation, measurement or ageing error. The advantage of such an approach however is that it provides a framework to use all sources of data to measure population parameters. 4.1 Introduction There are many tools at the disposal of stock assessment scientists to mea sure growth and mortality parameters provided sampling is done represen tatively. But representative sampling may be difficult to acheive, especially if fish move a lot. Fish movement is invisible and can contaminate sam pling in a number of ways: the spatial distribution of the population may Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 82 be unknown and sampling done from only a portion of the true range, if sampling is based on an agency's jurisdiction rather than the distribution of the fish; or the spatial distribution may be dynamic (a function of the stock's size or oceanographic conditions). The number of examples where fish are distributed over larger area than previously thought is increasing in both aquatic (Anras et al., 1999; Arnekleiv and Kraabol, 1996) and marine systems (Haist et al, 1999; McHich et al, 2002; Rooker et al., 2003; Block et al., 2005). Such biased sampling will contaminate estimates of population parameters such as growth and mortality, particularly if the movement is size dependent and the age or size composition differs between areas, ff larger fish swim faster (and hence further) then sampling at the margins of a stock's distribution will be biased for faster growing fish, and sampling in the center of the distribution biased for slower growing fish. Finally, the center of a stock's distribution may also move as oceanographic conditions vary. Such dynamics are present for example in Pacific Hake (Benson et al., 2002). Even where sampling can be assumed representative in the spatial sense, Laslett et al. (2002) show growth parameters must be estimated simultaneously with natural mortality and measurement error for mark-recapture data, fn Chap ter 3, I showed using simulated length-age data that gear selectivity must also be considered. So in order to properly estimate growth parameters, in some cases it is also necessary to also estimate mortality, gear selectivity and in some cases movement must be included in the stock assessment. The format of most mark-recapture data is convenient for estimating sur-Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 83 vival parameters at fine time scale (that of the mark-recapture experiment) and when size information is included with observed recaptures then it is also convenient for estimating growth parameters. Growth analysis only re quires that the Is and Os typically used to denote observations of individually marked fish be replaced with size at time. Regardless of technique, estimates of growth and survival parameters rely heavily on assumptions that can rarely be met, or shown to be met, in practice. With length-age data the principal concern is age validation, that is, showing that annuli counted on a structure represent actual years. Beamish and McFarlane (1983) found that only 3.4% of 500 studies conducted before 1982 were successfully able to validate ages across the full age range. There has been little recent improvement in this ratio, with only 15% of studies doing so since then (Campana and Thorrold, 2001). Measurement error is often not even considered in assessments or worse, assumed to be zero and used to check the validity of ageing (Paragamian and Beamesderfer, 2003). Finally mark-recapture experiments rely on assumptions of no tag-loss, no tagging mortality and all tags being reported. Studies that estimate tag-loss are in vogue (Ebener and Copes, 1982; Pierce and Tomcko, 1993; Swanson and Schram, 1996; McGlennon and Partington, 1997; Julliard et al., 2001; Feldman et al., 2002; Rikardsen et al., 2002; Brattey and Cadigan, 2004) but it is practically very difficult to do dual tag studies and using internal tags is expensive and limited to relatively large fish. Even if a dual tagging study can be done, it cannot be used to determine tagging mortality. Furthermore, Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 84 dual tagging may actually increase the tagging mortality. It would be useful therefore to estimate a combined tag-loss, tag-mortality term without using such studies. This study consists of three parts. First I develop a likelihood analogous to that developed in Chapter 3 that can be used to estimate growth parame ters from mark-recapture data. Then I develop and explore the performance of combined likelihoods for length-age, change in length and mark-recapture data under two distinct situations, with and without length dependent move ment similar to that described in Chapter 2. Using simulation studies, I test the performance of each at estimating the von Bertalanffy growth param eters, movement parameters, mortality and tag-loss in a range of scenarios that include measurement error, ageing error and tag loss, f find the per formance of the combined likelihoods good but not robust to assumptions about stable historical recruitment, and measurement error. 4.2 Methods 4.2.1 Length-age likelihood The details of the likelihood for the length-age data are discussed in chapter 3 so will be only briefly reviewed here. I assume the data available for analysis consists of a matrix ri;a with elements of numbers of fish sampled at (discrete) lengths / and ages a, and that this is a random sample of the number of vulnerable fish of length I and age a available in the population to Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 85 be sampled. The general form of the likelihood for n;}Q given the parameter vector (9) is multinomial, and the log likelihood a product of the data n/itt and the log of the predicted proportions p^a at length I and age a: logL1(n|9) = ^^n(,aln(Ra) (4.1) ( a Pita is expressed as the product of three factors: a size dependent vulner ability to gear vi that depends on size (but not age), relative abundance Na of age a fish, and the conditional probability P(l\a) of being in a discrete length interval I given age a Pl = (42) Ka T,i EaviNaP(l\a)' [^Z) I assume vulnerability at length vi as,an increasing function of length "(0 = T, ?7"TTT- (4-3) (1 + e-TC-W) with parameters (//,) as the length at 50 % vulnerability and a shape param eter (7) that describes the slope of the curve through lh (Deriso et al., 1985). Assuming stable recruitment No, then relative numbers-at-age (Na) can be calculated using: Na = Noe-W'-V. â€˘ , (4.4) Equation 4.4 computes the exponential decay of older cohorts relative to A^o individuals. The natural mortality rate M is to be estimated along with the Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 86 growth and vulnerability parameters using Eq. 4.1. I assume variation in growth among individuals is caused variation in in dividual asymptotic lengths (Wang et al., 1995), so that the von Berta lanffy prediction for any individual i is L00ji/(a) where /(a) is shared by all individuals i. Using the von Bertalanffy growth model this shared effect is described by: f{o) = l-e{--K{a-tÂ°)\ (4.5) where K is the metabolic growth parameter and tQ is the theoretical time of zero length. Assuming that individuals with Loo,* present at the start of cohort life are drawn from a normal distribution with mean LM, and variance cr^,, an individual with a specific L^i will follow a growth trajectory determined by the Lco.i they were born with. This implies that the integral defining P(l\a) for each age a should be evaluated with mean la = Loaf(a) and variance in mean length at age CT2. 1 pl+d P(l\a) = 7= / exp where I is the length of the fish, d is half the length interval width, la is the mean length-at-age, and CT2 is the variance in length-at-age. In most fish species, the absolute value of CT2 increases with age (cr2 gets larger as a increases). To avoid estimating cr2 for each age, I assume that standard deviation at age oa can be expressed as a simple function of the (la - If 2<72 dl (4.6) Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 87 mean length at age la. This function can be /â€ž multiplied by some coefficient of variation (CV) which is assumed to be constant across all ages, or more complicated functions can be used such as that of Fournier and Sibert (1991) as described in Eq. 4.7. In this formulation p is the Brody growth coefficient (p = e^-7^), A, the number of ages, age a, Ai represents the magnitude of the standard devi ations at age a â€” 1 and A2 determines the length dependent trend in the standard deviations (if A2=0, the standard deviations are independent of length) (Fournier and Sibert, 1991). This formulation has the disadvantage of adding two parameters rather than one if a\ is expressed as CV * la. The rationale for using it however, is that it makes a less restrictive assumption about how aa changes as fish grow (rather than assuming a fixed coefficient multiplied by length at age). 4.2.2 Mark-Recapture Data I assume the data consist of marked cohorts R with individual fish of length I tagged and released at time t. Each individual % therefore has a capture history consisting of lengths litt at marking and subsequent recapture. The recapture history of the cohort Rt then is a matrix with elements lt if captured and 0 if not, rows of individual tag numbers and columns t when sampling (4.7) Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 88 Cohort tag tl *2 ts tk-1 tk Ri XXX k - k - - -xxx k k - k 4-1 â€” XXX k â€” - 4-i â€” XXX k - - - 4 R2 XXX k k - lk-1 -XXX k k - â€” â€” XXX k -' k . - . -XXX k â€” - 4-i â€” XXX k k k â€” Parameters - - â€˘ â€˘ capture probability Pt Pl Vi PA P5 survival 4>t fa 4>2 <t>3 <t>i <t>5 06 Table 4.1: Format of mark-recapture data by cohort R released and recap tured at times t and estimated parameters for survival <f>t and capture probability pt occurred (table 4.1). Two likelihoods are used for the mark-recapture data: the probability of the observed sizes at capture and recapture given the predicted age struc ture as well as the probability of the capture history given predicted survival over the mark-recapture time period. The first depends on the growth, re cruitment and vulnerability parameters that led to the size/age structure of observed marked and recaptured animals. The second depends only on mortality parameters over the course of the mark-recapture experiment. I discuss first the likelihood for growth and second that for survival. Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 89 4.2.3 Mark-Recapture Likelihood for Growth The general form of the likelihood for estimating growth parameters from mark-recapture data is an adaptation of Laslett et al. (2002)'s formulation to include the effects of gear selectivity. It is the product of two parts: the joint probability of being marked at length at time of first capture /c, pric and the joint probability h(lc,lr\a,l) of being measured to have lengths lc at time of marking and at recapture lr after some time increment 5t later. Using discrete lengths I and ages a the likelihood is: where the data niCiiT are the lengths at capture and recapture, h(lc, lr\a, I) is the joint density of lc and lr. I assumed the probabilities of observed length at capture and recapture to be independent and normally distributed with the true mean length at marking l\ and length at recapture l2 respectively logL2 = ^^"Wr^EHP^Mk.Ma.O] (4.8) lc , lr â€˘ la h(lc, lr\a, I) = e' (4.9) where o20 is the measurement error variance, lc and lr the measured lengths at marking and recapture. I assumed each marked fish follows an average growth trajectory described by some function /(ÂŁ), that allows for individual Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 90 variation in each fish i so that its true length l\ at time t and true age A is I assumed that individual variation in length at age comes from normal dis tribution of individual with mean u.^ and variance u2^ , A the age of fish and 9 a vector of growth parameters. Using the von Bertalanffy model, we expect the lengths of fish marked at t\ and recovered at t2 to be func tions fl and /2 (respectively) of the metabolic growth parameter (K) and the amount of time 5t after marking so that l2 is the predicted length at recapture computed as: Since the true age A was unknown, for each combination of age a and length I in Eq. 4.8 f computed the individual LXii that would have produced the observed length. I assumed this distribution was normal with the mean asymptotic length LM and variance a^,. Individual Look's were calculated for each length and age combination using /(a) (Eq. 4.5): (4.10) l2 = L00,:f(t,A + 6ud) (4.11) Loo, = I/f(a) (4.12) The predicted proportions at length and age for the mark-recapture sam-Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 91 Additional recaptures are simply added to the log-likelihood of that in dividual's growth trajectory. The vulnerability parameters that predict vi, the growth parameters that predict h(lc, lT\a, I) combined with M to predict priiC are estimated in the likelihood. I treated the observed lengths as coming from a distribution with a mean true length I and a measurement error term assumed normally distributed with mean zero and standard deviation o\. I assumed the distribution of measurement errors was the same for marking and recapture. For each ob served length at either marking or recapture, I compute a range of possible true lengths lrng = lc or lr Â± 2o0. This format does not permit estimating the measurement error. This must be assumed or done empirically where possible by querying the lengths of fish marked at short time intervals (say one day) apart and computing the mean difference between those two times. 4.2.4 Mark-Recapture Likelihood for Survival with no Movement I used the method reviewed in Lebreton et al. (1992) for estimating survival. The data and parameters used are of the form described in table 4.1 but instead of l's typically used to denote recaptured fish I use size observations pie have a similar form to the length-age data (Eq. 4.2): (4.13) Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 92 lt > 0 where fish were observed and lt = 0 where not. Calculating the likelihood of each individual i capture history involves three steps: determining the time when each fish was last observed alive r; computing the probability of each lt observation for time t < T given the fish was alive; and computing the probability the fish was not observed for time t > T. The probability of the data at all time points t < r is simply the product of survival 4>t and the capture probability pt if the fish was observed and if not, the product (frt and the compliment of the capture probability qt = l-pt: where pitt = vtpt. The computation is more complex for the probability of observations at time t > rt. Here the probability of each observation is the sum of the fish may not have been observed due to any combination of dying at any time t > T or not being detected even though alive. Fortunately these probabilities can be calculated by backwards recursion. If Xt is the probability of not being observed again given release alive at t = r and the last sampling time point t = k then Xk is by definition 1. According to Cormack (1968) Xi is calculated as: (4.14) probabilities that could have led to the fish not being observed. Individual 1 + Xi = M1 ~ Qi+iXi+i) (4.15) Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 93 The log-likelihood of each capture history is multinomial with the pre dicted probability equal to the product of the probabilities of all the time t observations. Suppose for example, an individual was marked at t = 1 at 120 mm, not observed at t = 2, measured again at t = 3 at 123 mm; then not observed again in two addition surveys conducted at times t = 4 and t = 5. Its capture history is: 120 0 123 0 0. The likelihood Li of individual i's capture history is the product of the probabilities of each of observation at time t: , Li-= <p2q2<f>3P3X3 - â€˘ (4-16) The total log-likelihood of all data then is the sum of the likelihoods of each individual of the individual capture histories i. log L3 = ]TL/ (4.17) i The capture probabilities pt may be estimated in the likelihood but are given by the conditional maximum likelihood estimate: Pt = (4.18) where rt is the recapture of individual i (either 1 or 0) v^i is the gear selectivity of individual i and N[ti is the predicted survivorship of that individual. Using the conditional maximum likelihood estimates of the capture probabilities is convenient particularly if the capture probabilities are low, and/or if many Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 94 animals are never observed again after marking (for such data there is very little information about the capture probabilities). Calculating vi requires predicting the length of each individual at time li.t and calculating its vulnerability v^i using Eq. 4.3. I predicted kit at Ai time after first marking tc, ltc+At as ktc+M = lc,i + (L00-lc,i)(l-e-K^) (4.19) using the von Bertalanffy growth parameters estimated with Eqs. 4.8 and/or 4.1. 4.2.5 Mark-Recapture Likelihood for estimating survival parameters and movement To estimate movement parameters I depart from the traditional mark-recapture method described above and instead adopt the state-space approach of De Valpine and Hastings (2002) to formulate a likelihood function. Here I suppose a time series consisting of length observations y\.y2, â€˘â€˘â€˘VT until some maximum time T. I denote all observations Y until time t as Yt. The likelihood is calculated recursively with the probability of all the data at time t given the parameters P(Yt) expressed as the product of the proba bility of the data through t â€” 1 and the probability of the latest observation Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 95 P(Yt) = PiY^PiytlY^) (4.20) P(yt\Yt-i) is expressed as: (4.21) St where St represents all possible fish states (alive in area 1, alive in area 2, etc. and dead). P(yt\st,Yt-i) is the probability of the observation given the state, or simply the capture probability. For example, if a fish is observed in area 1 at time t then the probability of that observation is simply the capture probability in that state pSjt. The probability of it being observed in any of the other states (alive in other areas, or dead) given it was captured in area 1 is therefore zero. P(st\Yt) is updated at each time step using Bayes theorem so P(st\Yt) is equal to the prior P(st\Yt-i) multiplied by the probability of the data given the state (the likelihood p(yt\st)) divided by the sum of all possible combinations of priors and likelihoods (the marginal). Where there is an observation in one of the location states, the posterior probability of being'in that state is simply 1. The priors at the subsequent step P(st+i\Yt) are the product of the posterior state probabilities P(st\Yt) and the state transition matrix MSliSl+1 which is a square matrix with rows P(st\Yt) = P(st\Yt_l)p(yt\st)lY.Pist\Yt-Myt\st) (4.22) Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 96 Area 1 (Nursery) Figure 4.1: Movement model used to simulate data. Fish enter the movement pool at the length-dependent movement rate p,i from the nursery area then divide into areas 2 and 3 with the proportion p2 going to area 2, l â€” p2 going to area 3, and 1 â€” staying in the nursery area. Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 97 St+i and columns St with elements survival rate 4> and movement probabilities ps. Taking P(st\Yt) as a column vector with rows for each state, P(st+1\Yt) = MatiSt+lP{st\Yt). (4.23) The transition probability of going from any location state to the dead state is simply 1 â€” 4>, and from the dead state to the dead state 1. 4.2.6 Movement Model There is considerable flexibility to model complicated movement patterns using the above methodology. Since the partial objective of this study was to simulate the estimation of growth and movement parameters for a stock with a spatial structure like that described in Chapter 2 and for simplicity, I simulate a stock with two life history types: a moving type which undergoes a single length-dependent movement from the nursery area, and a resident type that remains in the nursery area its entire life (Fig. 4.1). Fish are assumed not to return to nursery area after dispersing. For convenience I subscript each area according to Fig. 4.1. The proportion of fish at length I in site s is ipitS. I assume this probability to be the product of the total proportion at length leaving the nursery area piti and a length dependent movement probability function assumed to be normally distributed, with mean length at movement lyt and standard deviation o^ so that the predicted proportion at length in the nursery area is: Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 98 The proportion at length in site 2 is ipit2 = (1 â€” ipi,i)P2 and ipit3 â€” ipifii^- â€” P2) fÂ°r site 3. For example, with the total proportion moving pn set to 0.70 and n.2 set to 0.5 the predicted proportion at length in all areas is illustrated in Fig. 4.2. Because any length-dependent movement.will also affect the length-age structure in each site, ipitS terms for site must be included to the predicted proportions at length and age in Eq. -4.13 and Eq. 4.2. In the movement case, Eq. 4.13 becomes 2 ^M = (l-xxOCi - exp â€” dl) (4.24) (4.25) and Eq. 4.2 Pi,a,s --= ipi,sviNaP{l\a) (4.26) J2i EaEsipsviNaP(l\ay so that the likelihood L2 (Eq. 4.8) becomes logLm2 = ÂŁÂŁÂŁni<;S],i.Jo.g[ÂŁÂŁÂŁp^iSh(/C)S,/r^|a,/is)] (4.27) 5 lc,s lr,s ICS Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 99 Figure 4.2: Proportion of the population in each area as a function of length ipi, in area 2 (red, 1P2) and 3 (green ip3). Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 100 and L\ (Eq. 4.1) becomes log-Lmi(ni]Q]5|9) = J2J2J2ni;a,sm(Pi^) (4-28) ( a s 4.2.7 Combined Likelihoods The way movement is modeled here requires that growth, mortality and movement likelihoods be combined. With practical sample sizes, length-age or size-at-capture and recapture data do not contain enough information to estimate the parameters of the movement probability function (Eq. 4.24). Also, the survival likelihoods (with or without movement) require either as sumptions, or estimates of growth to estimate the capture probabilities using Eq. 4.18 (since ijj's are needed) and obviously the length-dependent move ment probability function (Eq. 4.24). These formulations have considerable flexibility with respect to how sur vival and mortality are modeled. The estimate of M in the growth likelihoods (Eqs. 4.1 and 4.8) assumes stable recruitment. I test how robust Eq. 4.8) is to this assumption below. Survival and movement may be modeled as time dependent (fit = e~MAt at fine scale (at each time step in the mark-recapture experiment), as distinct for the marked cohort, or assumed the same as the historical M that gave rise to the age structure represented in Eqs. 4.1 and 4.8. Since part of the purpose of this study was to explore if a combined tag-loss/tag-mortality parameter can be estimated without dual marking, I Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 101 assumed that the natural mortality experienced by the marking cohort(s) M was the same as the M that gave rise to the age structure so that the difference in the apparent mortality experienced by the marked cohort must be due to a combined tag-loss/tag-mortality term. 4.2.8 Simulation Stock-Assessment Using Combined Likelihoods with No Movement I tested the performance of the likelihoods using simulated data. The like lihood used for the length-age data (L\ Eq. 4.1) was tested extensively in chapter 3; L3 for survival data has also been used and tested extensively (re viewed in Lebreton et al. (1992)) and Eq. 4.20 likewise for animal movement (Jonsen et al., 2003, 2005) so their individual performance was not evalu ated here. I tested: the performance of the mark-recapture likelihood for growth increments (Eq. 4.8) across a range of recruitment and measurement error values; and the ability of the combined likelihoods (Eq. 4.1, 4.8, and 4.16) to capture tag-loss in simulated data with and without supplimentary length-age data. I explored the following scenarios: a) data generated with no tag loss and fit assuming no tag loss using only the growth increment likelihood L2 (Eq. 4.8) b) data generated with tag loss and fit assuming no tag loss using the growth increment L2 and tag survival likelihoods L3 (Eqs. 4.8 and 4.17) Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 102 c) data generated with tag loss and estimating this tag loss using the growth increment L2 and tag survival likelihoods L3 (Eqs. 4.8 and 4.17) d) data generated with tag loss and estimating this tag loss using length-age (Li), growth increment (L2) and tag survival likelihoods (L3) (Eqs. 4.8, 4.17 and 4.1). Table 4.2: Parameters used to generate fake data for combined likelihoods Parameter Value sample size NT 1000 log asymptotic length InLoo 5.5 mm von Bertalanffy growth parameter K 0.15 yr'1 natural mortality M 0.2 yr'1 fraction of at half vulnerability k 0.5 mm selectivity slope 7 0.1 standard deviation in length at age 1 Ar 16 mm age standard deviation scalar A2 0.5 tag loss U 0:3 yr-1 measurement error Om 5 mm . I ran three sets of simulations for the combined likelihoods with parameter values listed in table 4.2.8. For the first, recruitment variation was assumed to be 0, measurement and ageing error set to zero and tag loss set to 0.3. For the second set, I included variation in past recruitment anomalies as log-normal process error with a mean of zero and standard deviation of 1 multiplied by a coefficient of variation CVR of 0.2, and measurement error of 5 mm. For the final series, ageing error was included in the simulated length-age data (see below). Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 103 Ageing error may be either measurement error clue to structures showing different numbers of annuli (Beamish and McFarlane, 1983) or error arising from the subjective assignment of rings on structures to annuli. The former is generally not normally distributed, and instead tends to be negatively biased, resulting in under-ageing of older fish (Campana and Thorrold 2001, Shayne MacClellan Department of Fisheries and Oceans. Nanaimo. Canada, pers. comm.). This error structure occurs because the first spawn often appears as a check on the otolith when fish stop growing. Under-ageing is very common. Since the amount of tissue laid down-on each ear bone gets smaller with age, many annuli can be compressed together. If the otolith is sectioned along the short axis, these compressed rings may appear as a single ring. Furthermore, the preparation of otoliths for reading usually involves burning them so this same outer layer can be completely charred during this process. I modeled the simulated ageing error accordingly, assuming readers cor rectly estimated ages with a certain probability C of being correct where the correct age is estimated and otherwise making a normally distributed error with mean size a * a and standard deviation 0.1 * a. I modeled a as a sigmoidal function (Fig. 4.2.8) having a positive domain at ages under some inflection age a,- and a negative domain for older fish so that: (4.29) Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 104 o o o o m o Â°oooooooooooo o o o o o o o o r o T T I 25 5 10 15 20 age (years) 30 Figure 4.3: Plot of a used to simulate ageing error Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 105. and the estimated age a in the simulated data: a = N(aa,0.1o) (4.30) where a was a normally distributed random number with mean a * a and standard deviation 0.1 * a. For simulations C = 0.7 and a* = 8. I initially simulated data with 1000 length-age and mark-recapture sam ples. The capture probabilities at all time steps in the simulated data were set to 0.2. For subsequent simulations without varying annual recruitment (and hence estimates of growth and mortality), and with measurement and/or ageing error the simulated number of marked fish was 300. This was done to explore more realistic sample sizes, and also for computational efficiency. Calculating L2 is computationally intensive because of having to integrate across ages, lengths (Eq. 4.8) and measurement errors (<r0)(Eq. 4.9). This issue is not trivial, the number of function evaluations of Eq. 4.8 needed for each simulation trial is a multiple of the number of observations, ages, length-bins, and the range of measurement errors. 4.2.9 Simulation of growth parameter estimates with length-dependent movement Given the difficulty of marking small fish in mark-recapture programs, it is not practical to model, or even attempt to characterize any size-dependent movement process of juvenile fish. Nevertheless such movement will have an Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 106 effect on the size-age structure where sampling is limited to either nursery or outlying areas. I explored potential biases from using the length-age like lihood (Eq. 4.1) when each area is treated as an independent stock having its own growth and mortality parameters. The main purpose of these sim ulations was to determine whether or not it is necessary to model all of the movement dynamics in order to correctly estimate growth and mortality pa rameters. For computational efficiency I chose Eq. 4.1 for these simulations. 4.2.10 Effects of Gear Selectivity and Capture Probability on Mortality and Movement Parameters When there are mark-recapture data available, movement rates may be es timable. Two things are required to do so: fish must be captured and marked at sizes small enough that such movement can be detected (the ratio of the length at half selectivity to the gear to the mean length at which movement takes place lh/1^ small), and they must be recaptured in sufficient numbers (high capture probability). I therefore tested the performance of Eq. 4.20 across a range of capture probabilities and ratios of mean length at movement to the length at half selectivity to the gear lh (l^/lh)- For these simulations I set the reference model 1^ : lh to 0.16, 1.16 and 1.83 and capture probabili ties pt at all time steps equal to 0.05, 0.35 and 0.55. I ran 100 simulations of for each combination of pt and l^ : lh-Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 107 Growth parameters were estimated using Eq. 4.13 assuming no mea surement error and variation in past recruitment anomalies was included as log-normal process error with a mean of zero and standard deviation of 1 multiplied by a coefficient of variation CVR = 0.2. Each simulated dataset consisted of a single marked cohort of 1000 (the approximate total number marked in Dad's and Moose Pasture lakes over the summer of 2001) individ uals marked in the nursery area, with recapture sampling occurring every 2 months for two years. 4.3 Results 4.3.1 Estimation Trials with No Movement Estimates of growth parameters were unbiased and with low variance when large datasets (1000 growth increment observations) were simulated with no recruitment variability, no tag loss and neither measurement nor ageing error (Fig. 4.4 (a)). When data were generated with tag loss (ij), but it was not estimated, M was positively biased. The growth increment data predicted the correct M and the addition of the L$ term to the total likelihood dragged the estimate of M up by 15 % (Fig. 4.4 (b)). The models were not robust to violations in the assumption of stable re cruitment or to smaller mark-recapture cohorts. Even small annual variabil ity in recruitment (CVR = 0.2) caused high variance in growth and mortality Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 108 (a) iâ€”iâ€”iâ€”iâ€”r K h X2 y lh M tl (b) "iâ€”iâ€”iâ€”iâ€”iâ€”i i r U K h ^2 7 lh M tl (c) (d) ; f - -LT) _ O -* V , * -L. * + o in o -o ' i L, K ^1 ^2 7 lh M tl 1â€”Iâ€”Iâ€”Iâ€”Iâ€”Iâ€”Iâ€”T L. K ^1 h 7 lh M tl Figure 4.4: Boxplots of proportional bias ((true â€” estimate)/true) of 100 growth and mortality parameter estimates for scenarios a) data generated with no tag loss and fit assuming no tag loss using only the growth increment likelihood L2 (Eq. 4.8), b) data generated with tag loss and fit assuming no tag loss using the growth in crement 1/2 and tag survival likelihoods L3 (Eqs. 4.8 and 4.17), c) data generated with tag loss and estimating this tag loss using the growth increment L2 and tag survival likelihoods L3 (Eqs. 4.8 and 4.17), and d) data generated with tag loss and estimat ing this tag loss using length-age (la), growth increment (L2) and tag survival likelihoods (L3) (Eqs. 4.8, 4.17 and 4.1) with CVR â€” 0, no measurement or ageing error. Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 109 parameters when only the mark-recapture data were used (Fig. 4.5 panels a, b, and c). Due to high covariance of parameters, poor estimates of one resulted in poor estimates of the others. When tag loss was not fit (Fig. 4.4 (b)) but data generated with it, M was positively biased but the estimates of the growth parameters and K were also biased. This bias was reduced when tag loss was fit (Fig. 4.5 c), but only marginally. The addition of length-age data reduced the bias and the variance of parameter estimates considerably (Fig. 4.5 d) but only when ageing error was zero. The ability of the length-age data to compensate for measurement errors (in L2) in the combined likelihood was compromised when aging error was included. Because of the function that was used to generate the ageing error, (the tendency of young fish be over-aged and older fish to be under-aged) M was positively biased (there were few "observations" of old fish) and K negatively biased. The parameters used to describe the variance in length at age (A] and A2) were poorly estimated all scenarios except the first where there was no recruitment variation and large sample size. With few growth increment samples, there was little information about the distribution of lengths at each age. In general Ai and A2 were the most sensitive to data simulated with measurement error. There were also the most poorly behaved during fitting, often resulting in the models failing to converge. This was also the case for estimates of CV\a when oa was defined more simply as a product of length at Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 110 (a) "iâ€”iâ€”iâ€”i i i r L. K h h 1 lh M tl (b) "i i i i i i r U K h >-2 Y lh M tl (c) iâ€”iâ€”iâ€”iâ€”iâ€”iâ€”iâ€”r Iâ„˘ K h ^-2 J lh M tl (d) "iâ€”iâ€”iâ€”iâ€”iâ€”i i r L. K h h y lh M tl Figure 4.5: Boxplots of proportional bias ((true â€” estimate)/true) of 100 growth and mortality parameter estimates for scenarios a) data generated with no tag loss and fit assuming no tag loss using only the growth increment likelihood L2 (Eq. 4.8). b) data generated with tag loss and fit assuming no tag loss using the growth in crement 1/2 and tag survival likelihoods L3 (Eqs. 4.8 and 4.17), c) data generated with tag loss and estimating this tag loss using the growth increment L2 and tag survival likelihoods L3 (Eqs. 4.8 and 4.17), and d) data generated with tag loss and estimat ing this tag loss using length-age (Li), growth increment (L2) and tag survival likelihoods (L3) (Eqs. 4.8, 4.17 and 4.1) with CVR = 0.2, no ageing error, measurement error= 5mra. Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 111 (a) iâ€”iâ€”i i i i i r U K li ^2 T lh M tl (b) iâ€”mâ€”ÂĄâ€”iâ€”iâ€”iâ€”r L_ K h ^2 Y lh M tl (C) iâ„˘ K ^2 y ih M ti (d) nâ€”iâ€”iâ€”iâ€”iâ€”iâ€”iâ€”r U K h h y lh M ti Figure 4.6: Boxplots of proportional bias ((true â€” estimate)/true) of 100 growth and mortality parameter estimates for scenarios a) data generated with no tag loss and fit assuming no tag loss using only the growth increment likelihood L2 (Eq. 4.8), b) data generated with tag loss and fit assuming no tag loss using the growth in crement 1/2 and tag survival likelihoods L3 (Eqs. 4.8 and 4.17), c) data generated with tag loss and estimating this tag loss using the growth increment L2 and tag survival likelihoods L3 (Eqs. 4.8 and 4.17), and d) data generated with tag loss and estimat ing this tag loss using length-age (L\), growth increment (L2) and tag survival likelihoods (L3) (Eqs. 4.8, 4.17 and 4.1) with CVR = 0.2, ageing error, measurement error= 5mm. Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 112 age and a coefficient of variation in length at age (ZaCV/a). In some cases, the simulated data could best be explained by making the variance in length-at-age very large. Though fixing these parameters always improved the stability of the model it only improved, the bias in parameter estimates significantly for scenario d). (Fig. 4.7). 4.3.2 Simulation of growth parameter estimation with length-dependent movement When each area was treated as a separate stock while the simulated data came from a stock with ontogenetic movement from area 1 to area 2, the main effect was that growth parameters were unbiased but gear selectivity parameters (4 and 7), and M were biased (Fig. 4.8). In areas 2 and 3 the model 'saw' the failure to observe small fish as, a gear effect, so 42 and 43 had mean proportional biases of 200%. This was the 'correct' interpretation of gear selectivity in any case, since overall selectivity can be viewed as the product of both the gear effects and spatial distribution effects. The small fish did not appear vulnerable to the gear because they were not there. Movement out of area 1 (the nursery area) appears as a mean 50 % bias in estimates M. The von Bertalanffy growth parameters were unbiased across a range of smaller values but once became large, the bias in M grew large or the model often could not converge at all. In the nursery area, M was confounded Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 113 (a) ~\â€”iâ€”iâ€”i i i i r U K ^2 Y lh M ti (c) d iâ€”iâ€”iâ€”iâ€”Tâ€”n-1â€”r U K ^1 ^2 1 lh M tl (b) iâ€”iâ€”iâ€”iâ€”iâ€”iâ€”iâ€”r L. K h >-2 y lh M tl (d) "iâ€”iâ€”iâ€”râ€”iâ€”iâ€”iâ€”r L. K h h y lh M tl Figure 4.7: Boxplots of proportional bias ((true â€” estimate)/true) of 100 growth and mortality parameter estimates for scenarios a) data generated with no tag loss and fit assuming no tag loss using only the growth increment likelihood L2 (Eq. 4.8), b) data generated with tag loss and fit assuming no tag loss using the growth in crement L2 and tag survival likelihoods L3 (Eqs. 4.8 and 4.17), c) data generated with tag loss and estimating this tag loss using the growth increment L2 and tag survival likelihoods L3 (Eqs. 4.8 and 4.17), and d) data generated with tag loss and estimat ing this tag loss using length-age (Ia), growth increment (L2) and tag survival likelihoods (L3) (Eqs. 4.8, 4.17 and 4.1) with variance in length at age parameters (Ai and A2 fixed at their true values) Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 114 by an apparent dome-shaped gear selectivity process (clue to movement). M was over-estimated in the nursery area, where fish movement to outly ing areas increased the apparent mortality. This bias decreased as the total proportion remaining in the nursery area Lin increased and as the ratio of Ih/lfi increased. When the total proportion moving pi was high, the bias in the nursery M\ was also higher but it depended also on the ratio of lh to ZM and on <7M. If movement was complete at sizes smaller than the gear was ca pable of detecting (small ZM and CTm), then there was little bias in the samples taken from each area. When the simulated gear was able to capture smaller and smaller fish, the samples at young ages became increasingly distorted, and the bias in M grew proportionately larger in the nursery area. 4.3.3 Effects of Gear Selectivity and Capture Probability on Mortality and Movement Parameters Across a range of capture probabilities and gear selectivity values, M was well estimated (Fig. 4.9) for models that included movement. Variance in estimates of M increased as capture probability decreased, but the bias was negligible (1-3 %) and negative. However, the parameters that defined movement were only well estimated in those cases where capture probabilities were relatively high (greater the 30 %) and where Ih/lhn was approximately 1. Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 115 o co la "co c g ti o Q. o CM H I I I I I I I I I I I I I I I I I I I I I m1m2m;M-~J-"3Ki K2K3h,hfafafafa3\M lâ€ž2'h3 Yi Y2 Y3 Figure 4.8: Boxplots of proportional bias ((true â€” estimate)/true) of 100 growth (LQO, -K\ Ai, A2), mortality (M), length at half gear se lectivity (//(), and gear selectivity function slope (7) parameters when each area is assumed to be separate stock, while simulated data come from a stock with ontogenetic movement from area 1 to areas 2 and 3. Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 116 There are several important caveats. Even with relatively high capture probabilities, lk/l/Ht set to 0.16 and 1000 fish marked, the number of marked fish that actually move over a two year period is relatively small (approx imately 160) and those tagged fish are distributed between two areas. So, even with relatively high capture probabilities, the number of observations that can be used to define the movement parameters is small even when a large proportion of the population is leaving the nursery area (70%). When lh/lhn = 1-16, the number of marked fish that are actually observed moving is much smaller (approx. 15-20). In the case of high lh/hin = 1-83, p2 is not estimable at all, or correctly estimated to be small, because there should typ ically be no observations of fish going to that area. Additionally, here again I assumed the same M for the marked cohort and the historical age structure sample so the estimated value of M is robust to lower capture probabilities in ways it would not otherwise be had the only information about M been from the mark-recapture data. Finally, regardless of whether or not param eters defining length-dependent movement can be estimated, admitting the possibility of movement in the model makes a big difference to variance of the estimate of M, since many combinations of capture probability and natural mortality can explain the observed data. Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 117 Ihg/lhm = 0.16 "i 1 1 1 r M Ihm Om Mn M2 Ihg/lhm =1.16 ~i 1 1 1 r M Ihm Om Mn M2 Ihg/lhm - 1-83 i 1 1 1 r M Ihm Om Mn M2 M Ihm "rn ~iâ€”iâ€”iâ€”~iâ€”T M Ihm Om Mn M2 iâ€”iâ€”iâ€”r M Ihm Om Mn M2 M Ihm O, T I I i r M Ihm Om Mn M2 t t _i_ _i_ Â° M Ihm Om Mn M2 Figure 4.9: Boxplots of proportional bias ((true â€” estimate)/true) in 100 es timates of M and movement parameters with capture probability (rows) set to 0.05, 0.35, 0,55 and with ratio of length at half gear selectivity to the mean length at movement /^/^ set to 0.16, 1.16 and 1.83. Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 118 4.4 Discussion The suite of growth, survival and movement likelihoods I presented here per mit simultaneous analysis of several processes using data commonly collected in many applied ecology programs. This is particularly useful because these parameters are nearly always of interest in applied ecology but also because both biological and observation processes mean these parameters must be estimated together. Consistent with the observations of Eveson et al. (2004), different types of data contain more information about some processes than others. For example, only with very large sample sizes (greater than 100 000) could the length-age data be used to estimate movement rates using simulated data. The problem is that using practical sample sizes, estimating M using length-age data requires estimates of movement rates, and likewise, if movement rates are a function of size, then correct estimates of growth are also required. One potentially serious problem with combining all data together is that some data may bias parameter estimates due to improperly modeled effects (for example mark-recapture data with a lot of measurement error, assumed to have none). More data and more complicated likelihoods do not necessarily mean better parameter estimates, therefore the processes used to collect such data should be examined very carefully. Rather than assume small measurement and ageing errors as well as con venient distributions for such errors, I have tried to simulate the performance Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 119 of the likelihoods under the worst rather than best situations. The biases in parameter estimates shown here are therefore conservative, and worse than might be expected in many mark-recapture and/or ageing programs. Measurement error tends to bias growth parameter estimates dispropor tionately in smaller, slower growing fish, fn this analysis, measurement error was set at 5 mm because in the field large measurement errors occur when fish tails are damaged from spawning, or when larger rule increments are mis-read (fish length is recorded as 235 rather than 230 mm for example). It is instructive to think of the measurement error relative to the annual in crement of the fish. In the simulations performed here a 5 mm measurement error is larger than the annual increment of fish greater than age 12, less than half the maximum age. The magnitude and direction of the simulated ageing error was consider able. The choice of such a function to represent this error was based on the review of Campana (2001) who shows that very few ageing programs validate their ageing correctly or even at all. Much ageing can reasonably be assumed correct, or to have normally distributed error purely from counting. How ever, the reality of most stock assessment programs is that all these sources of error are present and there are systematic biases towards under-aging older fish. It is unreasonable to assume mark-recapture programs for size and fish survival are not subject to some violation of assumptions about constant recruitment, lack of measurement error, no tag-loss etc. Therefore, the choice Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 120 of methods for estimating growth parameters using mark-recapture is a choice between the least of evils. On one hand, traditional methods ignore natural mortality, gear selectivity and measurement error altogether. Methods such as Laslett et al. (2002) and Eveson et al. (2004) do not account for size-selectivity, so over-estimate K and of the total population, an issue that is irrelevant if the stock assessment scientist wishes only to describe the growth of the population being harvested. On the other, the method I developed here is data intensive, means tolerating at least a 5 â€” 10% bias in K and poorly estimated parameters describing the variance in length-at-age. However, the direction of the bias in K and M is the most conservative. Stock assessments using underestimates of K and M predict smaller than actual yield-per-recruit and current biomass. Further, the bias does not matter if the objective is simply to compare the growth of one stock to another. Combining length-age, growth increment and mark-recapture data can only be used to estimate of tag-loss when recruitment is reasonably constant over time. In cases where recruitment is variable, noise caused by the re cruitment variation makes M unstable, hence unreliable as a resource base for detecting tag-loss. Also, since the M of the population is what is of inter est in some cases, making such an assumption defeats the purpose of doing the mark-recapture in the first place. However there is a considerable litera ture developing for estimating tag-loss (Ebener and Copes, 1982; Pierce and Tomcko, 1993; Swanson and Schram, 1996; McGlennon and Partington, 1997; Julliard et al., 2001; Feldman et al., 2002; Rikardsen et al., 2002; Brattey and Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 121 Cadigan, 2004) so such information could be used to generate priors for the tag-loss. But none of this literatures addresses problems with long-term tag ging mortality or tag under-reporting. Admitting a range of possible tag-loss values is important for properly admitting uncertainty about mortality es timates since the trade-off between tag-loss and mortality is one-to-one and uncertainty about what the true tag-loss is propagates through the estimates of all the other parameters. Assuming that constant recruitment so tag-loss can be estimated is ob viously incorrect. Nevertheless with external tags it is better than making the still worse assumption of no tag-loss, no under-reporting, and no tag-mortality. This is particularly true when external tags are used. Where the magnitude of the tag-loss/tag-mortality is large, the bias in M (and the corresponding positive bias in estimates of the population size where appli cable) produced by such assumptions failing is considerable and also in the least conservative direction (over-estimating M and hence the population size). For example, tag-loss for dart tags has been reported by McGlennon and Partington (1997) at O.OOOGcT1 and for anchor tags at 10 - 20%yr~1 (Ebener and Copes, 1982). Even in the case of internal tags, passive induced transponder tag (PIT) failure has been reported in sharks as high as 12%yr_1 (Feldman et al., 2002). These biases are also in the least conservative direc tion with respect to exploitation rate predictions. Estimating higher that actual natural mortality means predicting higher than optimal exploitation rates. Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 122 The simulations were unrealistic in assigning fixed nursery and non-nursery boundaries. When stocks have such a spatial structure, fishing and survey sampling are likely to overlap each area to a certain extent. Nevertheless a number of fisheries are divided along similar lines with an onshore sector targeting younger fish and an offshore sector targeting different fishes, e.g. Pacific Hake or Yellowfin tuna. In such situations separate gear and spatial effects need to be considered for data coming from each fishing sector in any case (onshore, offshore etc.), because in addition to spatial effects, the gear used also differs. This is not the first paper to use the state-space methods like De Valpine and Hastings (2002) with mark-recapture data. Rivot et al. (2004) used this method and mark-recapture data to estimate upstream migration of adults and downstream migration of juveniles in Atlantic salmon. Clark et al. (2005) use a hierarchical Bayesian model to estimate maturation age, survivorship, and population growth in simulated and real data, and Jonsen et al. (2003) used state space approaches to combine information from multiple individual movement trajectories with missing data. Finally state space methods have been used to estimate growth parameters for physiologically based individ ual growth models with size trajectory data (Fujiwara et al., 2005). The method used in this study is not fully a state space formulation because of the predicted growth trajectories are modeled deterministically using the von Bertalanffy growth model, but it is the first to combine growth information with movement data to estimate a size-dependent movement function. Unfor-Chapter 4. Estimating movement and growth parameters given size-dependent spatial ontogeny 123 tunately the models presented here require a lot of data, (several 100 marked and recaptured fish, approximately 1000 length-age observations, and in the case of movement several marked fish observed to have moved) and are not robust to either measurement or ageing error. Since datasets used to measure growth and mortality may not contain enough information to estimate parameters such as gear selectivity and mor tality, integrating the information from all available data sources to estimate growth parameters should be expanded to the entire stock assessment process for many commercial fisheries. Stock assessments typically contain informa tion about the fishing mortality and gear selectivity and often have many years of length-age, or length-frequency or mark-recapture data. Several years of this data could be incorporated into multiple length-age and mark-recapture tables to track changes in natural mortality and growth over the time of a fishery. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 124 Chapter 5 Predicted and Observed Ecosystem Responses to Fishing Abstract I used a simple ecosystem model and compared the predictions to observed responses following experimental fishing in a two fish lake system with rain bow trout and northern pikeminnow. Consistent with the model's predic tions, growth and mortality of juvenile rainbow trout was higher relative to the control in lakes where northern pikeminnow were removed while adult rainbow trout survival remained unchanged. Visual survey indices of north ern pikeminnow fry indicated survival of 1+ fish worsened and 2+ improved following fishing. Consistent with the model's predictions no obvious mor tality or growth responses were observed in northern pikeminnow. While the agreement between the model and observations was encouraging, field testing such a hypothesis was fraught with difficulty. The probability distributions of the parameters of interest were very broad and the model predicts many of the important dynamics, in particular behavior mediated vulnerability ex change rates, to occur in fish size classes and groups of zooplankton that are difficult to observe. keywords: non-target species response to fishing, cultivation-depensation, northern pikeminnow, movement mortality estimation Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 125 5.1 Introduction Juvenile survival is usually assumed to improve at low stock size so as to make recruitment much more sensitive to stock size than would be the case if survival were constant. There is good evidence to support this assumption (Myers et al., 1999, 1995b). Given the failure of a number of overexploited stocks (Shelton and Harley, 1999) to recover following collapse, there has recently been considerable concern about whether or not recruitment de creases at low stock size (depensation). Myers et al. (1995b) concluded that only 3/128 stocks showed significant depensation. Nevertheless, considerable work followed their analysis with particular attention devoted to determining whether or not models parameterized with depensation fit the data better than those without it (Liermann and Hilborn, 1997, 2001) and if depensa tion could be detected at all in complexes of multiple 'sub-stocks', each with differing productivites (Frank and Brickman, 2000). In all these cases, the depensatory dynamics were assumed stationary in a statistical sense, where the parameters describing the relationship are assumed time-invariant. Changes in ecosystem productivity and the process of fishing itself likely alter recruitment dynamics of fish stocks over time, since they alter food and predation regimes. Foraging arena theory (Walters and Juanes, 1993; Walters and Korman, 1999) predicts that as the ratio of predation risk to food production changes over time, then so too will recruitment. Abrupt ecosystems state transitions have been observed in aquatic systems (Scheffer Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 126 et al., 2001b; Scheffer and Carpenter, 2003). Walters and Kitchell (2001) postulate a specific hypothesis termed "Cultivation-Depensation" explaining how such shifts might happen in response to fishing, and what observations should be observed in the field if they are. If their explanation is correct, the cultivation-depensation hypothesis is that if a dominant stock is reduced, there will be a reduction in the extent to which it "cultivates" more favor able conditions for its juveniles by reducing abundance of competitors and predators. Cultivation-depensation effects arise in Ecosim II (Walters et al., 2000) models though the following sequence of events (Walters and Kitchell, 2001). Fishing reduces the adult population size of a fish species and hence, the total number of juveniles in predation refuges. Juveniles reduce feeding time or time spent at body sizes small enough to be vulnerable to predation risk. Juvenile mortality then decreases so that the net number of recruits stays nearly constant even though fewer juveniles are being produced. However, if there is predation between the adult fish and a predator or competitor of the juveniles (a "forage" fish) then as adult density is reduced, the forage fish is released to increase in abundance. Then one or two negative effects can occur. If the forage fish prey directly on juveniles, then predation mortality is directly increased. If the forage fish and juveniles are competitors, increased forage fish abundance leads to reduced food density and hence, increased juvenile foraging time and general predation risk. These dynamics can be represented with a trophic triangle such as that in Fig. 1.1. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 127 I used field data collected in 2001-2003 to constructed a simple ecosystem model of small lakes in northern British Columbia Canada (see Section 2.2.1) using Ecopath with Ecosim (Walters and Christensen, 2004). These lakes had two predatory fish species, rainbow trout (Onchorhynchus mykiss) and stunted northern pikeminnow (Ptychocheilus oregonensis). The study system had the foraging arena structure described above with juvenile rainbow trout and northern pikeminnow (in all age classes) confined to the margins of the lake during the day (Section 5.2.2), whereas adult rainbow â€˘ trout were distributed mainly in the center of the lakes. I sampled in the system and measured the growth and survival response of the two fish communities to depletion fishing (where a large proportion of the population was fished in a short, series of fishing bouts) of both rainbow trout and northern pikeminnow. I found that consistent with model predictions, survival and growth of small rainbow trout decreased in lakes where northern pikeminnow were removed and that no changes in growth or survival for adult adult northern pikmeinnow could be detected and it was not possible to estimate growth and survival parameters due to low sample sizes for adult rainbow trout. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 128 5.2 Methods 5.2.1 Ecosim Model of Predicted Observations The details of the Ecopath-Ecosim modeling approach are discussed exten sively in Walters et al. (1997, 2000) and Walters and Christensen (2004) so will only be briefly discussed here. Ecopath is used to define the initial ecosys tem biomass state that is mass-balanced, i.e. where estimated total biomass loss rates Zi for each modeled biomass group i are partitioned among as sumed static predation rate components and unaccounted losses. In Ecosim models, these static flows are turned into dynamic, time-varying predictions by assuming that flows C from prey i to predator j groups are mediated by vulnerability exchange rates vitj between "vulnerable" and non-vulnerable prey pools (Walters et al., 2000): c >â€˘,.,<>,., (5. |) + i ,.j'iKjPj where a; is the effective search rate, of .predators, B the biomass and â€˘ the exchange rate from the vulnerable pool back to the non-vulnerable pool, assumed to be equal to vitj. The vulnerability exchange rates ^js's determine the rate at which prey enter either a vulnerable state j (which is available to be eaten by predators) from an invulnerable state i (assumed not to be vulnerable to predators). These dynamics are assumed to occur on a much faster time scale than other Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 129 population dynamics such as predation and mortality (Walters and Juanes, 1993; Abrams and Walters, 1996) and thus reach an equilibrium vulnerable pool of prey V that is available to predators (Walters et al., 1997). The behavioral interpretation of what Vifs are can best be thought of as any behavior (avoidance, fish schooling, habitat refuges etc.) that limits the access of the prey to the predators. Small Vij's mean that a lower proportion of the total prey population is in the vulnerable state at any given time, and vice versa. These rates therefore have a very large influence on the population dynamics predicted by Ecosim. Small vitj's imply a lot of foraging arena structure (Walters and Juanes, 1993), whereas large rates imply classical type II (Ffolling 1959) predation dynamics. Overall biomass was simulated for pelagic zooplankton, chaoborus larvae, benthos, phytoplankton and detritus since data to estimate these were un available. Simplification of the system into these groups was done to allow a focus on specific hypotheses about size-dependent predation and compe tition interactions involving the two fish species. Chaoborus larvae were singled out as a particularly important group because they are the main diet item of (70%) of pikeminnow but were virtually absent in rainbow trout stomach contents. Pikeminnow undergo daily offshore migrations that are concurrent with the nightly rise of chaoborus (Table 5.2.1, Dave O'Brien un published data). The diet matrix was parameterized using stomach content data collected over 2001 and 2002 (Dave Obrien unpublished data). I used the multi-stanza approach (Walters and Christensen, 2004) for Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 130 modeling fish species in the system, with parameters listed in Table 5.2.1. The multi-stanza version of Ecosim allows for the division of a species into age-size groups (stanzas) assumed to share similar mortality and diet com position. It assumes growth follows the von Bertalanffy (von Bertalanffy, 1934) growth curve. To initialize the population stanza age structure, it is assumed that recruitment and mortality have been stable for long enough for the population to be at a stable age distribution. Leading values for mor tality are needed for all stanzas, while annual consumption per unit biomass Q/B and biomass are needed for one leading group. The biomass and Q/B of the remaining groups are calculated using age-dependent weight wa and survivorship la. The initial population growth corrected proportion of a fish la is modeled in Ecopath as: where Z is this case is the instantaneous annual natural mortality (in years yr~l) The la for any given age is the sum of Zs is over all ages up to a, and BA/B term represents the effect on relative numbers at age of the population growth rate (Walters and Christensen, 2004). The relative biomass of other stanzas relative to the leading stanza is initialized using relative biomass proportions bs, where for any stanza s: 7 - p-l2aZa-aBA/B (5.2) a (5.3) Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 131 (Walters and Christensen, 2004). The relative weights at age wa are assumed to follow the von Bertalanffy prediction: wa = (l- eKaf. (5.4) where K is the von Bertalanffy growth parameter estimated for both fish species using the methods described in Section 5.2.6. Q/B estimates for non-leading stanzas are calculated with a similar approach, assuming that feeding rates vary with age as the 2/3 power of body weight (Walters and Christensen, 2004). Consumption per unit biomass ratios for oldest stanza's were assumed to be 1.5 for northern pikeminnow and 5 for rainbow trout. I divided northern pikeminnow (NPM) in age into 4 life-history stanzas denoted by the age a at which the stanza began. This stanza division was chosen since northern pikeminnow are markedly different in sizes for only the first four years. Rainbow trout (RBT) were divided into two stanzas, 0-1 and 2+ years. Rather than parameterize the fish groups in absolute biomass, they were parameterized relative to each other. Where the biomass of the 4+ northern pikeminnow and the 2+ rainbow trout were assumed equal they were both set to 1. Ecopath was used to calculate invertebrate biomasses needed support the base estimated consumption rates caused by these relative biomasses, assuming reasonable ecotrophic efficiencies (Table 5.2.1, ecotrophic efficiency is proportion of Zi explained by modeled predation). Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 132 Start Relative Instantaneous Natural Consumption per Age yr~l Biomass Mortality (Z yr~l) unit biomass yr~l Northern pikeminnow 1 0.002 3 13.033 2 0.009 0.5 5.362 3 0.022 0.3 3.5 4+ 1 0.2 1.5 Rainbow trout 0 0.061 3 16.491 2 1 0.7 5 Table 5.1: Parameters for multi-stanza representation of northern pikeminnow and rainbow trout populations I predicted changes in mortality, body growth, population size and feed ing time following a very short pulse of intense 'depletion' fishing F = 1 applied for one year. I explored the sensitivity of the model to a range of vulnerability exchange rates (vij) for the fish and zooplankton groups. I explored how differences in relative fish biomass and vulnerability exchange rates the model would or would not produce Cultivation-Depensation effects, and in particular two equilibria with only one fish group dominant at each. In search for parameter combinations that would produce multiple equilibria, the two fish biomasses were set to 1.0, so as to represent a potentially un stable equilibrium point between the two stable equilibria. When two stable states exist, any fishing disturbance tends over time to one of the biomasses being dominant. Table 5.2: Diet composition matrix for Ecopath model. Each column is the diet composition of a particular predator, as a proportion of total annual biomass food intake Zoo Phyto Det. Prey Pred RBT 2+ RBT 1 NPM 4+ NPM 3 NPM 2 NPM 1 Chaob Ben RBT 2+ RBT 1 0.049 0.02 0.091 NPM 4 0.00001 NPM 3 0.00005 NPM 2 0.0001 0.00049 NPM 1 0.0005 0.009 Chaob 0.665 0.686 0.27 Ben 0.909 .0.1 0.19 0.196 0.27 0.1 Zoo 0.091 0.9 0,095 0.098 0.36 0.9 1 Phyto 0.05 Det. 0.95 Table 5.3: Basic parameter inputs for Ecopath Model Biomass Production per unit biomass yr~l Consumption per unit biomass yr~ 1 Ecotrophic efficiency Unassimilated Consumption RBT 2+ 1 0.7 5 0.2 RBT 1 0.0613 3 16.491 0.2 NPM 4 1 0.2 1.5 0.2 NPM 3 0.0219 0.3 3.5 0.2 NPM 2 0.00865 0.5 5.362 0.2 NPM 1 0.0019 3 13.033 0.2 Chaob 2 6 0.8 0.2 Ben 3 15 0.3 0.2 Zoo 5 20 0.8 0.2 Phyto 30 0.4 Det. 100 Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 135 5.2.2 Experimental fishing In the summer of 2001 1 depletion fished two lakes called Mom's and Cheryl (see Fig. 2.1) in two separate drainages on the Bonaparte Plateau north of Kamloops in south central British Columbia. I set one lake in each drainage aside as a control (Dad's and Moose Pasture). Early observations showed northern pikeminnow are confined to the shoreline during the day but per form crepuscular migrations offshore from nearshore hiding spots. This be havior was used to selectively remove them by setting gillnets along the entire shoreline of the experimental lakes. This same behaviour was used to selec tively deplete rainbow trout in Wilderness and Nestor lakes in 2001 and 2002, by setting gillnets mid-lake rather than parallel to shore (O'Brien unpublished data). During June and July of 2001 northern pikeminnow depletions were con ducted in two or three bouts of several (3-5) consecutive nights fishing. Dur ing each bout, the length of gillnet used was sufficient to completely surround Mom's Lake and about 80% of the perimeter of Cheryl Lake, f rotated net panels with different bar meshes around each evening to ensure each area was exposed to all meshes. Summaries of the depletion effort by date and bar mesh are compiled in Table 5.4 for Cheryl Lake and in Table 5.2.2 with a plot of the proportion of mesh sizes used in figure 5.1. I measured the fork-length (FL) of every fish captured and sacrificed 285 from Cheryl lake and 264 from Mom's Lake for ageing. Given the nursery structure discussed in Chapter 2, I determined after Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 136 Table 5.4: Total length and proportions by bar length (cm) Cheryl Lake Proportion of bar mesh by cm Date Total (m) 1.25 1.5 1.9 2.5 3.1 3.75 26-Jun-01 1200 0.06 0.06 0.08 0.57 0.11 0.11 27-Jun-01 1200 0.06 0.06 0.08 0.57 0.11 0.11 28-Jun-01 1200 0.06 0.06 0.08 0.57 0.11 0.11 2-Jul-01 1300 0.06 0.06 0.10 0.57 0.10 0.10 3-Jul-01 1300 0.06 0.06 0.10 0.57 0.10 0.10 15-Jul-01 1300 0.06 0.06 0.10 0.57 0.10 0.10 16-Jul-01 1300 0.06 0.06 0.10 0.57 0.10 0.10 17-Jul-01 1300 0.06 0.06 0.10 0.57 0.10 0.10 Table 5.5: Total length and proportions by bar length (cm) Mom's Lake Proportion of bar mesh by cm Date Total (m) 1.25 1.5 1.9 2.5 3.1 3.75 18-Jun-01 1150 0.06 0.06 0.08 0.57 0.11 0.11 19-Jun-01 1150 0.06 0.06 0.08 0.57 0.11 0.11 20-Jun-01 1150 0.06 0.06 0.08 0.57 0.11 0.11 9-Jul-01 1135 0.06 0.06 0.10 0.57 0.10 0.10 10-Jul-01 1135 0.06 0.06 0.10 0.57 0.10 0.10 ll-Jul-01 1135 0.06 0.06 0.10 0.57 0.10 0.10 Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 137 1.25 1.56 1.87 2.5 3.12 3.75 mesh size (cm) Figure 5.1: Proportion of gillnet meshes used on all depletions. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 138 carrying out the Cheryl and Mom's Lake depletions that in order to observe a northern pikeminnow recruitment response, a nursery lake had to be ma nipulated as well. In late August and early September of 2002 I fished the eastern drainage nursery lake called Moose Pasture (Fig. 2.1). Fish were captured during 6 bouts of daily fishing using 4 hoop nets. Three of these nets consisted of 6 x 1 m fiberglass hoops covered in 1 cm mesh, 24 m center lead, and 15 m side leads. The other consisted of 6 x 0.7 m steel hoops cov ered in 0.5 cm mesh, 15 m center lead, and 10 m side leads. Lapilli otoliths were taken from each northern pikeminnow and 945 of these were aged of 3682 fish caught in Moose Pasture. Using the same gear, an additional 1082 northern pikeminnow were captured and aged from Dad's Lake in September 2003. Additional depletion fishing of rainbow trout was conducted in Wilderness Lake in 2001 and Nestor Lake in the summer of 2002 (David O'brien unpub lished data. A map showing the lakes, and what removals (either northern pikeminnow or rainbow trout) is shown in Fig. 5.2. 5.2.3 Fish ageing To age the fish I cut Lapilli otoliths along the ventral/dorsal axis using an Isomet Bueller slow speed saw, burned and counted annuli. Otoliths too small to cut were burned and counted directly. For fish older than 5 years, failing to cut otoliths along the long axis resulted in significant under-ageing. Mom's Lake (NPM depletion Nestor Lake (RBT depletion 2002) Moose Pasture Lake (NPM Depletion 2002) Iderness Lake^^ Wilderness (RBT Depletion 2001) Cheryl Lake (NPM depletion 2001) Figure 5.2: Map of experimental lakes showing the location of rainbow trout density reductions (RBT depletion), and northern pikeminnow density reductions (NPM depletion). 9 CD CD CL o CD i CL ft .8 ft) o o tr 3' Crq 00 Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 140 5.2.4 Depletion Experiments Population sizes and percent removal were estimated using the method out lined in Schnute (1983). The analysis consists of a population model describ ing the numbers remaining (Nt) and an observation model describing the predicted number caught Ct. Ct was predicted as proportion of the popula tion removed by the fishing gear each night (q) and the numbers remaining alive at time t (Nt): Nt = N0-ÂŁct t=0 (5.5) Ct = qNt The observed catches at time t in length bin I were fit to the predicted catches in Eq. 5.5 using a Poisson log likelihood. Ignoring all constants that do not depend on the estimated parameters, the poisson log probability of the data (Ct) given the estimated parameters (q,N0) is: P(Ct\Noh m) c< Ct,i In (qiNu) - qiNtJ. (5.6) The parameter qt was evaluated at its conditional maximum likelihood esti mate: q=^. (5.7) t I used 10 mm length bins. Since there were tagged animals in Moose Pasture Lake when depletions were conducted it was possible to use these data to estimate depletion also. I Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 141 used fish marked in the two weeks preceding removals to obtain a population estimate (assuming no tag loss or mortality in that time interval). The log likelihood was calculated as: L = Ri \og(Pn) + Utlog(l - Pn) (5.8) where Ri is the number of recaptures at length, Ui the number of marked animals and Pri the predicted probability of capturing a marked animal. Pri was the ratio of tagged recaptures to the number of tagged fish at risk to capture (or the ratio of total captures (MiUi) to total N at risk, N0j). It is typical in depletion experiments for each bout of several days fishing to result in an underestimate of N, clue to some fish not being vulnerable during any short-term bout. I hopefully corrected for this effect by using more than one bout on each lake, and the daily catches over all bouts (Fig. 5.11) support this hope. 5.2.5 Visual Surveys I conducted visual fry surveys in all study and control lakes in 2002 to confirm the presence or absence of fry and to generate a quantitative index of fry abundance. A second series of visual observations was on approximately the same dates in 2003. Due to a nearby forest fire only one set of observations was possible in 2003. The surveys were conducted on sunny days between 9 : 00 A.M. and 3 : 00 P.M. by either walking or rowing as close as possible Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 142 along the shoreline. Where fry were present (in Moose Pasture and Dad's lake) I recorded estimates of the number of 0+ fry, age 1+, and age 2+ northern pikeminnow observed along with the GPS positions of each school spotted. I calculated crude survival rates by calculating the ratio of the 2+ index in 2003 to the 1+ index in the previous year, and likewise the 1+ index in 2003 to the 0+ index in 2002. These survival estimates are plotted for the manipulated lake (Moose Pasture) and the unmanipulated lake (Dad's) in Fig. 5.15. 5.2.6 Estimation of Survival and Growth Parameters For northern pikeminnow growth, I used mark-recapture methods to mea sure the growth and survival responses following manipulations. At approx imately weekly intervals, I surveyed all the lakes using the gear described in Section 5.2.2, recorded the fork length of all marked and unmarked ani mals, and marked new animals. Since the overwhelming majority of north ern pikeminnow marked were greater than 90 mmFL (or approximately 4+), they are treated as a single adult "stanza" and assumed to be subject to same natural mortality. I divided marked rainbow trout into two groups: those greater or smaller than 200 mm. All data used for this analysis come from fish captured in fyke nets and marked following experimental depletions in each lake. I estimated northern pikeminnow survival and movement parameters in the eastern and western drainage lakes using the combined likelihoods de-Table 5.6: Total number of marked and recaptured northern pikeminnow by drainage, lake and treatment. NPM=northern pikeminnow, RBT=rainbow trout and dep=depletion Number of Total number Total recaptures from Treatment Drainage Lake marked cohorts marked all cohorts/times Moose 7 343 153 NPM dep East Cheryl 10 613 216 NPM dep Wilderness 7 580 143 RBT dep Dad's 11 2024 667 Control West Mom's 11 597 428 NPM dep Nestor 9 629 155 RBT dep Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 144 T3 a 3 o IS I o _Q fl 'S -n i-i fl DH 03 â€˘ O CD i-1 3 *â€˘< S v. g â€˘ 6-5 in $ O TT X ri o ao p CN Â« b ^ Â« r~ 12 ; Is E! Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 145 scribed in Section 4.2.5 (Eqs. 4.20, 4.27 and 4.28). Fish marked following experimental manipulations were marked and recaptured in approximately weekly intervals, with the number of marked cohorts (groups of animals marked in any particular sampling bout), the number of fish marked in each cohort and the total number of recaptures from all cohorts at all times in each lake summarized in tables 5.2.6 and 5.2.6. I did not assume a normal distribution of mean length at movement (Eq. 4.24) since it is restrictive about the shape of movement probability density. Instead, I represented the cumulative probability of moving at length I as the product of the maximum proportion moving from the nursery area U\ and an incomplete beta distribution. The length dependent cumulative movement probability function became: where a. and (3 are the shape parameters and pn the maximum proportion moving. I set a lower bound on the parameter a of 2 for fitting since at values approaching 1 it was possible for the curve to predict 100 % of fish moved before 50 mm FL. Gear selectivity parameters (Eq. 4.3) were fixed with 4 = 0.45 and 7 = 0.2 for all areas and both fish since they were not estimable. The assumed gear selectivity parameters are basically the same as those estimated by the length-age likelihood (Chapter 3 Table 3.3.1). (5.9) o Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 146 For rainbow trout, I assumed no structured ontogenetic movement and estimated the rainbow trout growth and survival parameters using the com bined likelihoods described in Section 4.2.4. It was not possible to estimate the historical natural mortality for rainbow trout < 200 mm so I fixed these values at the mean value of the prior for natural mortality for juvenile rain bow trout where M â€” 1.78 (see Section 5.2.7 below). 5.2.7 Prior Distributions In all estimation procedures for both fish species I used Bayesian priors for all mortality, growth and tag-loss parameters. In the case of rainbow trout, the tag loss was a hyper-parameter and assumed shared across all the study lakes. Analysis of the northern pikeminnow data was too memory-intensive to allow parameter estimates for all six study lakes to be run at once. The analysis was done instead by drainage where tag-loss was assumed equal across the drainage. The prior on northern pikeminnow natural mortality M and the mortality of the tagged cohorts by lake Mt was normal N~(p = 0.30, a = 0.19) and built from 7 estimates of natural mortality in the Columbia River (Rieman and Beamesderfer, 1990). Growth parameter priors come from 2 observations in Montana lakes and streams (Carlander, 1969; Peters, 1964) and from Rieman and Beamesderfer (1990). For log^^) the prior was N~(p = 6.23, cr = 0.1) and for the von Bertalanffy K parameter N~(p = 0.14,CT = 0.08). The prior for age 1 rainbow trout natural mortality come from Post et al. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 147 (1999)'s 47 observations of age 1 rainbow trout survival across a range of rainbow trout densities. This prior was normal N ~ (fi = 1.78, cr = 1.95). Priors for the rainbow trout von Bertalanffy growth parameters and for adult mortality come from 7 estimates in (Ruiz-Campos et al., 1997; Pidgeon, 1981; Kwain, 1981). For K this prior was N~ (LI = 0.53, a = 0.1), for it was N ~ (p, = 6.0, o = 0.2) lacking information on M, the prior for M was set to the same as for K. The prior for anchor tag loss for both species comes from studies that estimated the tag-loss rates for fish of comparable sizes using Floy type an chor tags (Ebener and Copes, 1982; Ebener, 1982; Muoneke, 1992; Pierce and Tomcko, 1993; Swanson and Schram, 1996; McGlennon and Partington, 1997; Julliard et al, 2001; Rikardsen et al., 2002; Brattey and Cadigan, 2004). This prior was again assumed to be normally distributed N~(p = 0.33, a = 0.27) 5.2.8 Markov Chain Monte Carlo Sampling for parameter uncertainty I expressed parameter uncertainty by sampling the posterior probability dis tributions of each estimated parameter using the MCMC algorithm built into AD Model Builder (a C++ software, Otter Research Ltd. Sidney, B.C., Canada), which allows fast maximization of the likelihoods of complex mod els because analytic derivatives are automatically calculated. Four Markov chains were run for each analysis (adult northern pikeminnow, rainbow trout Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 148 smaller than 200 mm) until the multivariate potential scale reduction factor (Gelman et al., 1995) was smaller than 1.05. 30 000 samples of the posterior were taken from each chain following convergence. Convergence diagnostics were performed using the CODA with the R statistical software package (http://www.r-project.org). 5.3 Results 5.3.1 Predicted responses to experimental fishing of using Ecosim The model showed that it is possible to produce cultivation-depensation ef fects in the experimental system and that it was possible to produce a flip from either a rainbow trout dominated system to a northern pikeminnow dominated one and vice-versa (Figs. 5.4 through 5.10). These predictions were very sensitive to changes in the vulnerability exchange rates. Flips were not predicted when all vulnerability exchange rates between prey and preda tors were set to 2 (implying a maximum mortality rate on prey at very high predator abundance of 2x the Ecopath base rate) for all groups. In order to produce flips by northern pikeminnow depletion fishing, the vulnerability ex change rates between zooplankton and their predators, as well as chaoborus and 2+, 3+, 4+ northern pikeminnow had to be 3 or greater and the vul nerability exchange rate between zooplankton and chaoborus greater than Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 149 10. When vulnerable exchange rates were high enough to produce flips, the main predicted changes in the system following northern pikeminnow biomass reduction (Fig. 5.4) operated through the chaoborus and zooplankton dy namics. As 4+ northern pikeminnow declined, chaoborus was released from predation. While its total predation mortality declined (Fig. 5.4), the biomass of chaoborus did not increase (Fig. 5.3) significantly since at the same time its own food supply, zooplankton, was decreasing because of in creases in rainbow trout 2+ density and large increases in growth by the remaining 2, 3, and 4+ northern pikeminnow and 2+ rainbow trout (Fig. 5.5). Because of decreased zooplankton density, predicted relative feeding time of both the juvenile rainbow trout and northern pikeminnow increased. Interestingly, the predicted response of the rainbow trout population was for the total biomass to increase and be comprised of fewer, but larger fish. While the mortality of the juveniles increased, the adults were larger (Fig. 5.5) and so the predicted biomass of rainbow trout higher. Producing flips by rainbow trout depletion fishing occurred only when vulnerability exchange rates between 2+,3+ and 4+ northern pikeminnow and 2+ rainbow trout were 5 (Figs. 5.8 to 5.10) or greater. As was the case in producing flips with northern pikeminnow depletions above, the vulnerability exchange rates of zooplankton to chaoborus needed also had to be greater than 10 in order to produce flips. The models were relatively insensitive to changes in the relative fish start-Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 150 ing biomasses and would still produce a flip from one dominated state to another in both cases where rainbow trout biomass is half the northern pikeminnow biomass and vice-versa. In general, you could move the un stable starting point around a lot, without eliminating the two stable points where alternate equilibria exist at all. 5.3.2 Estimated Depletion The depletion estimates here are those of the vulnerable (active) population. The depletion estimates in Fig. 5.12 and the upper panel of Fig. 5.13 are very high, i.e. are optimistic about the impact of the removal fishing. Gill nets are passive gear and so fish must be active in order to be captured in them. Furthermore, incomplete depletions in a particular gear type may be due to learned gear avoidance (after an unsuccessful capture encounter). The depletion estimates based on the tagged animals (Fig.5.13) showed the deple tion to be on average 70% across size classes rather than the 100% estimated using Eq. 5.6. Bycatch mortality of rainbow trout was negligible during depletions in Moose Pasture (since trap gear was used) and Mom's Lake. However, there was considerable bycatch in Cheryl Lake of rainbow trout where 1257 mainly small (< 200 mm) were captured. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 151 Rbt2+ Rbt 1 '8 **Â»*Â«*Â»Â» *Â»Â»Â»Â»Â»B**Â«iS*Â»B?Â»9S>i NPM 4+ NPM 3 NPM 2 Chaoborus NPM 1 Zoo Figure 5.3: Predicted relative biomass (B) changes after depletion fishing of 4+ northern pikeminnow. The biomass of 2+ RBT and 4+ NPM have been arbitarily set to 1 and the other groups scaled accordingly. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 152 Rbt 2+ NPM 4+ NPM 2 Chaoborus Rbt1 NPM 3 NPM 1 Zoo Figure 5.4: Predicted changes in M after simulated depletion fishing of 4+ northern pikeminnow. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 153 Rbt 2+ Rbt1 NPM 4+ NPM 3 NPM 2 NPM 1 Chaoborus Zoo year Figure 5.5: Predicted body weight changes (kg) after 4+ northern pikeminnow depletion fishing. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 154 Rbt2+ NPM 4+ Rbt 1 NPM 3 NPM 2 NPM 1 Chaoborus Zoo Figure 5.6: Predicted changes in relative feeding time after 4+ northern mikeminnow depletion fishing. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 155 Rbt 2+ Rbt 1 NPM 4 NPM 3 NPM 2 Chaoborus NPM 1 Zoo Figure 5.7: Predicted relative changes in biomass B following 2+ rainbow trout depletion fishing. The biomass of 2+ RBT and 4+ NPM have been arbitarily set to 1 and the other groups scaled accord ingly. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 156 Rbt 2+ Rbt1 NPM 4 10 20 NPM 2 Chaoborus NPM 3 NPM 1 Zoo Figure 5.8: Predicted changes in M following 2+ rainbow trout depletion fishing. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 157 Rbt 2+ NPM 4 NPM 2 10 20 30 year 40 50 Chaoborus Rbt1 NPM 3 NPM 1 20 30 Zoo Figure 5.9: Predicted changes in weight (in kg) after rainbow trout depletion fishing. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 158 Rbt 2+ Rbt 1 NPM 4 NPM 3 NPM 2 I 1 r-20 30 40 Chaoborus NPM 1 Zoo Figure 5.10: Predicted relative changes in feeding time after rainbow trout depletion fishing. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 159 Cheryl Lake 2001 o Â° _i u â€” ra _ O o -o -CM Jun 27 Jul 02 1 Jul 07 Date 1 Jul 12 Jul 17 Mom's Lake 2001 Jun 22 Jun 27 Jul 02 Jul 07 Jul 12 Date Moose Pasture Lake 2002 o Sep 09 Sep 10 Sep 11 Sep 12 Sep 13 Sep 14 Sep 15 Sep 16 Date Figure 5.11: Depletion catches of northern pikeminnow(in numbers) by date for Cheryl lake in 2001 (top), Mom's lake in 2001 (middle) and Moose Pasture lake in 2002 (bottom). Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 160 Cherl Lake o CN Mom's Lake o o c o oj -o o o o 50 "i r 100 150 200 o "S3 CP "D CO O o o o "i r 50 100 150 200 FL (mm) FL (mm) Figure 5.12: Estimated northern pikeminnow vulnerable numbers (iV) and percent depletion estimates by length for Cheryl and Mom's lake. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 161 Depletion Estimates 50 100 150 200 FL (mm) Mark-recapture Estimates FL (mm) Q-"D co o -3-o CM O FL (mm) FL (mm) Figure 5.13: Northern pikeminnow population and percent depletion esti mates by length, V represent 95 percent CI. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 162 50 100 150 200 FL(mm) Figure 5.14: Fit of proportion northern pikeminnow leaving the nursery area function by length for each drainage. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 163 5.3.3 Visual Surveys The change in the visual survey index shows that survival of fish from 0+ to 1+ was better in the unfished lake than the fished one (0.06 in Dad's lake but only 0.03 in Moose Pasture) following experimental fishing (Fig. 5.15). In contrast, the survival rate from 1+ to 2+ was much improved following fishing of adults in Moose Pasture relative to the unfished lake (Fig. 5.15). A serious problem with interpreting these result however, is that they come from a single pair of observations so are not reliable. 5.3.4 Northern pikeminnow growth, mortality and movement parameter estimates The northern pikeminnow in each drainage have approximately the same growth curves (Fig. 5.16). In both drainages, the observed lengths at age in the non-nursery lakes tended to be higher than the nursery lakes suggesting either that larger fish move upstream to the head-end lakes, or that growth is better in these lakes. Northern pikeminnow movement differed between the eastern and western drainages in two ways. In the eastern drainage, there was a tendency for fish to migrate into the headwater lakes at smaller sizes (Fig. 5.14). For example, age 2+ NPM were absent from the western drainage (Fig. 5.16 upper panel) but present in the eastern drainage (Fig. 5.16 lower panel). This observation was also consistent with the population estimates (Fig. 2.3) showing the Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 164 Figure 5.15: Percent change in visual survey index in Dad's (blue) and Moose Pasture (red). Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 165 Figure 5.16: Fit of von Bertalanffy growth curve through length-age data in western (top) and eastern (bottom) data. Jitter added to better see overlay. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 166 presence of 1 and 2+ fish in Cheryl lake, but not in Mom's or Nestor lakes. Also, the total proportion moving from the nursery area pn appeared to be lower in eastern drainage than in the western (Fig. 5.18). The broad posterior probability distributions meant there were no clear differences in growth or survival parameters in northern pikeminnow greater than 90 mm between the eastern and western drainage(Fig. 5.17). 5.3.5 Rainbow trout growth and mortality estimates It was not possible to estimate growth parameters for rainbow trout > 200 mm. There were very few data, so the growth likelihood would not converge and only Mt was estimable using only Eq. 4.17. In addition, no fish marked following the experimental manipulations in Nestor Lake were recaptured so it was not possible to estimate Mt in that lake at all. There did appear to be some effect of the rainbow trout depletion fishing in Wilderness lake and to the combined northern pikeminnow (and acciden tal) rainbow trout depletion in Cheryl lake (Fig. 5.20). However, while the posterior modes of these distributions are a different, the posteriors are too broad to confidently argue a difference was observed. The estimated von Bertalanffy K for juvenile rainbow trout was the same between all treated and untreated lakes. There were differences in the Zog(Loo) between treated and untreated lakes, (Fig. 5.21), with fish appear ing to be stunted in those lakes where northern pikeminnow were removed (Moose Pasture, Cheryl and Mom's). Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 167 5.10 5.15 5.20 5.25 5.30 5.35 5.10 5.15 5.20 5.25 5.30 5.35 log(L_) log(L_) 1.0 1.5 2.0 2.5 3.0 1.0 1.5 2.0 2.5 3.0 Figure 5.17: Posterior samples of growth parameters (/oc/(L00), K), historical natural motality M, and tag loss tl for unfished western (left column) and fished eastern drainage (right column). Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 168 J 10 15 20 -r-25 -1 30 iâ€”i 10 . iJlTrriT-E*. I 1 1 1 15 20 25 30 Figure 5.18: Posterior samples of movement parameters (maximum propor tion leaving the nursery area p,n, proportion of the moving pool going to lake 2 p2 (Cheryl and Mom's), and the beta distri bution parameter (3 for the unfished western (left column) and fished eastern drainage. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 169 Dad 0.0 0.2 0.4 0.6 0.8 1.0 1.2 r Moose tun ~i 1 r 1 0.0 0.2 0.4 0.6 0.8 1.0 1.2 mil Mom Cheryl s i "i 1 1 r ~\ 1 0.0 0.2 0.4 0.6 0.8 1.0 1.2 I 1 1 1 1 1 1 0.0 0.2 0.4 0.6 0.8 1.0 1.2 mt2 m,2 Nestor o 0.0 0.2 0.4 0.6 0.8 1.0 1.2 mt3 Wilderness o o o 0.0 0.2 0.4 0.6 0.8 1.0 1.2 mt3 Figure 5.19: Posterior samples of northern squawfish tagged cohort mortality Mt by lake. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 170 Figure 5.20: Posterior samples of Mt for rainbow trout greater than 200 mm by lake. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 171 Moose Dad's T 1 1 4.5 5.0 5.5 6.0 6.5 log(U) Iâ€”-â€”I 1 1 1 4.5 5.0 5.5 6.0 6.5 log(U) Cheryl Mom's I 1 1 1 1 4.5 5.0 5.5 6.0 6.5 log(U) I 1 1 1 1 4.5 5.0 5.5 6.0 6.5 log(U) Wilderness Nestor g- N -I c <D O 3. Â° cr o a) o T 1 1 1 4.5 5.0 5.5 6.0 6.5 I 1 1 1 1 4.5 5.0 5.5 6.0 6.5 log(U) log(L-) Figure 5.21: Posterior samples of the log asymptotic length /Joc>(Loo for rain bow trout smaller than 200 mm by lake. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 172 Figure 5.22: Posterior samples of the von Bertalanffy K for rainbow trout smaller than 200 mm by lake. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 173 In spite of the very large posterior probability intervals, Mt for the rain bow trout was higher in those lakes where" northern pikeminnow we're fished (Moose Pasture, Cheryl, and Mom's Fig. 5.23). The lowest mortality was observed in Dad's lake, where there was .very high northern pikeminnow den sity. 5.4 Discussion I cannot say whether or not the experimental manipulations of either rainbow trout or northern pikeminnow will eventually result in alternate stable states. There is some agreement between the observed results and from model predic tions with parameter combinations implying strong cultivation-depensation effects. But, to make a case that the experimental fishing produced an al ternate stable state through cultivation-depensation effects would require a) observed changes in relative feeding time of 1+ northern pikeminnow and 1+ rainbow trout; b) observed changes in zooplankton and chaoborus densities; and c) a long series of observations following the manipulations showing that any recruitment responses were not transitory. Even in the case of mortal ity and particularly growth of 1+ rainbow trout, the posterior probability distributions for growth and mortality parameters showed the data can be explained by a large range of parameter combinations, including some con trary that would not imply strong cultivation-depensation effects according to Ecosim. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 174 Figure 5.23: Posterior samples of the instantaneous annual mortality of tagged fish by lake for rainbow trout smaller than 200 mm. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 175 Measuring the northern pikeminnow response to experimental removal to either rainbow trout or northern pikeminnow was much more problematic than simply wide probability distributions for response parameters. Because of dispersal among lakes of northern pikeminnow in the study system, the experimental unit was effectively a drainage. Therefore, the only relevant comparison for northern pikeminnow responses to northern pikeminnow fish ing were between the fished and unfished nursery lakes (Moose Pasture and Dad's respectively). Even ignoring the problem that sample size for the manipulations, was one lake, the flow of fry from lakes above the treated (Moose Pasture) and control lake (Dad's) could have been affected by fishing conducted in those upstream lakes. Fortunately, the manipulations in lakes above Dad's and Moose Pasture were identical, offering the possibility of long term comparisons. In the case of measuring the effects of rainbow trout removal, no 1+ and 2+ northern pikeminnow parameters could have been measured, since there are no fish of those size classes in those lakes. The non-nursery lakes were probably reasonable experimental units insofar as measuring the response of rainbow trout to fishing of northern pikeminnow since little interaction between 1 and 2+ northern pikeminnow and rainbow trout recruits was either predicted in the model here or observed in the field. There was a trade-off between northern pikeminnow density and rain bow trout growth and mortality (Figs. 5.23 and 5.21 (Post et al., 1999). In Ecosim, this trade-off operates through the effects of northern pikeminnow on Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 176 chaoborus which in turn affects the density of rainbow trout food supply (the zooplankton and benthos Figs 5.21, 5.22, and 5.5). However, since rainbow-trout were not marked until they were at least 100 mm, changes occurring in growth and survival of these fish before that point were invisible. Where northern pikeminnow were fished, juvenile rainbow trout density could have increased for example if northern pikeminnow predation was reduced result ing in slower growth and higher mortality similar to the pattern observed by Post et al. (1999). Distinguishing between the two hypothesis is simply a matter of observing the system over a few more years. The important thing to measure is how recruitment (in biomass) has changed before and since the manipulations. Ontogenetic movement of northern pikeminnow severely confounds any measurement of mortality and growth response. Implicit in the analysis shown here was a large and unlikely assumption that movement rates re mained constant over time. Recall in chapter 4.3.3 that I combined the length-age and tagging data to simultaneously estimate growth and move ment parameters. This approach implicitly assumes that the historical move ment rates leading to the observed length-age structure (in this case collected before any manipulations) was the same following experimental removals. This was necessary in order to accurately estimate the growth parameters in the nursery lakes needed to predict growth trajectories of the marked fish (used in turn to predict the probability of movement). This assumption would be violated in the likely case that movement being density-dependent. Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 177 The very high effective densities of northern pikeminnow in the nursery lakes (chapter 2, Fig. 2.5) suggest these lakes are very crowded. If the cue for fish to move upstream is very high density in the nursery area, then density reductions in the nursery area would result in less migration and possibly no change in mortality rates. An additional problem is that movement of northern pikeminnow could have occurred to lakes where no sampling could have detected. In the eastern lakes, fish could leave Moose Pasture lake by the outflow creek, and in the case of Dad's, to both Tasha lake above it and the outflow creek below it (Fig. 2.1). The estimates of any movement parameters could be grossly incorrect. The simulation studies in chapter 4.3.3 show that in cases with low capture probabilities and where movement occurs at sizes smaller than the selectivity of the gear (low Ih/hpi), the total proportion of the population leaving the nursery area (pi) is over-estimated. While the movement .probability function used in the analysis of the field data was different, the estimated movement functions show that movement likely occurs in size classes too small to be captured with standard hoop nets, meaning we should expect a positive bias in estimates of the total proportion leaving the nursery area p\. However, these same simulation studies showed that the estimate of mortality of the tagged cohort Mt was still unbiased. Ontogenetic movement does present an interesting opportunity for north ern pikeminnow control in this system. By preventing northern pikeminnow from returning to head-end lakes using dams, populations in those lakes Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 178 would eventually decline. Since the jumping ability of rainbow trout is much greater than northern pikeminnow, such barriers need not prevent their ac cess to headwater lakes. Only a single construction event would be needed to build these barriers with regular maintenance to prevent streams cutting around the stream banks around them. This would be considerably less ef fort than large-scale predator removal. Unfortunately, the effect of the clams might take several years to be felt since northern pikeminnow are relatively long lived, and have been known to spawn in the margins of lakes (Jeppson, 1959). On the other hand, efforts to eradicate northern pikeminnow in any lake lower in the drainage will be almost entirely fruitless since there will be a constant flow of fry from lakes upstream. Comparing measured and predicted experimental responses of ecosystem to fishing has several advantages. First, it gets away from attempting to intuit ecosystem responses to fishing.. There is little dispute that fishing will have community wide effects and that the interactions effects are not likely simple. It is optimistic to think any "expected" (as discussed by Sih et al. (1985)) effects of such removals could come from anything other than an ecosystem model. Ecosystem responses to fishing may occur in several different species, at several different trophic levels and have dynamics mediated by change in prey behavior (vulnerability exchanges rates). In addition, some of the expected response variables such as juvenile rainbow trout survival respond are likely to change in highly counter intuitive ways (survival decreasing but overall biomass of adult rainbow trout increasing over time). That said, the Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 179 Ecosim model I used here might require a more detailed description of the population dynamics (more groups to describe zooplankton for example) to realistically describe population dynamics. My results were similar to those of Vander Zanden et al. (2005) in iden tifying the potential importance of the benthic-zooplankton linkage in pre dicting the outcome of predator removal from lakes. The modeling approach used here is significantly different in that I assumed the dynamics were mit igated by behavior (vulnerability exchange processes) and, that model pre dictions were very sensitive to assumptions about those dynamics. Even though simple predator prey models are known to produce paradoxical be havior (Abrams and Walters, 1996), larger scale ecosystem models with the same flaws are still being produced (Vander Zanden et al., 2005; Mangel and Levin, 2005) with apparent disregard to the problems of the simple models. This study identifies some daunting practical challenges with measuring how ecosystems might respond to fishing (experimentally or otherwise). The major problems were firstly the spatial organization of the stock and secondly, that dynamics predicted to be the most important to the response to fishing are those occurring in size classes too small to measure. In the case of marine fisheries these difficulties are likely to be worse. Spatial dynamics in marine systems are arguably much more complex, and more poorly understood than lakes. Many marine systems are also likely to by already affected by fishing (Fisher and Frank, 2004), and data on non-target species at any size or trophic level are even more limited for most marine ecosystems. The model Chapter 5. Predicted and Observed Ecosystem Responses to Fishing 180 predictions and the field experience shows the most important dynamics are those that occur in precisely those young age groups and/or small size classes for which there is very poor information even for the target species of most fisheries. Chapter 6. General Conclusions 181 Chapter 6 General Conclusions 6.1 The difficulty of properly estimating growth and mortality parameters Growth and mortality should be relatively simple parameters to measure in response to harvesting but I have shown here that it is not easy to estimate these parameters correctly even with likelihoods that correctly account for the sampling process. This is a serious concern since growth parameters are used in virtually every stock assessment to predict size at age, yield per recruit, and often even as proxies for natural mortality itself (Pauly, 1980; Jensen, 1997). Traditional methods, such as the Fabens method are biased in the worst possible direction (over-estimating the metabolic growth parameter K and natural mortality M). This bias will lead to over-estimating the. optimal exploitation rate. The biases in traditional method for estimating growth parameters have been known for some time (Parma and Deriso, 1990) but solving the problem has proven very difficult even with techniques developed in this thesis and Chapter 6. General Conclusions 182 elsewhere Laslett et al. (2002); Eveson et al. (2004). The likelihoods devel oped here (Chapters 4 and 3) are not very robust to their assumptions and could not be used in many fisheries. Consider for example that the length-age likelihood fails to estimate parameters correctly when the historical fishing rate has been variable (chap. 3, Fig. 3.4) meaning that these methods could only be applied in a very restricted number of cases. Of particular concern is that growth parameters bias is worst in the common situation where exploita tion rate increases rapidly before a collapse. Unfortunately, this is when it is most important to be able to estimate the correct target exploitation rate, and to correctly project the biomass for rebuilding. Estimating growth parameters needs to be included in the stock assess ment itself, rather than treating growth parameters as 'known' values exter nal to the models, their estimation could be included with parameters (such as productivity, etc.) that are usually estimated in such models. Natural mortality, gear selectivity and fishing mortality are often already modeled in most stock assessment models so predicting a matrix of vulnerable numbers at length and age (pi, a Eq. 4.6) for every year would be relatively simple. When there are time series of length-age data, mark-recapture data many years of such tables could be included as time series to estimate the effects of fishing on the size and age structure of the stock. Many such tables could potentially provide information about time-varying growth and recruitment. Chapter 6. General Conclusions 183 6.2 Evaluating Ecosystem Impacts of Fishing The dynamics Ecosim predicted to have the greatest effect on an ecosystem's response to fishing are also those most challenging to study: the vulnerability exchange rates, and juvenile fish survival. Methods to estimate survival at least exist but there are considerable difficulties catching small fish and mark ing them once captured. The vulnerability exchange rates have the greatest effect on predicted direction and magnitude of the response to fishing. Es timating vulnerability exchange rates is typically done in Ecosim by fitting time series; analysis of change in prey mortality with changes in predator abundance; examination of long-term changes in predator abundance and calculations based on movement/exchange-rate data (Walters and Martell, 2004). Since I did not have multiple years of data only direct calculation of movement and exchange rate data would have been possible. Since the most important dynamics occur in small fish, the challenge here is to develop methods measure this exchange rate directly or indirectly in juvenile fish. If this study is carried forward for several years it will be possible to estimate the recruitment in the years that following depletion fishing once those recruits become fully vulnerable to fishing year using a standard stock-assessment model. However, without observations of changes in the vulnera bility exchange rates (or some proxy of foraging time) it will not be possible to say anything about whether Cultivation-Depensation effects were pro-Chapter 6. General Conclusions 184 duced. While agreement between observed and predicted response variables were encouraging, the true test of whether or not cultivation-depensation was produced will be to actually observe an alternate stable state with lower recruitment over several years and the changes in foraging behavior that produced that state. While Mangel and Levin (2005) may be right saying we have no excuse for not shifting to a community paradigm in fisheries, the data requirements to practically do so may be considerable. Consider the study system. To monitor and manage the community effects of fishing in this case f had to consider the dynamics of one species with two life-history types; one with large-scale density dependent spatial dynamics (northern pikeminnow) and rainbow trout on a more localized scale. Considering the relatively closed nature of this system and the iarge quantity of data - measuring growth and mortality responses should have been relatively simple. In many (especially marine) fisheries the data are poorer; the spatial dynamics are more complex; and the dynamics are further complicated by fast changing variables such as fishing effort. My study shows that simple growth and mortality variables may respond to fishing in very counter-intuitive directions. Consider for example, our modeling and field results showed that juvenile rainbow trout mortality was actually higher following northern pikeminnow removals. The model predicts this response but at the same time predicts an overall increase in rainbow biomass related to improved growth. The number of juvenile rainbow trout Chapter 6. General Conclusions 185 surviving might have indeed been lower in numbers, but the fewer remaining rainbow trout could have grown better, lived longer and produce more re cruits that many smaller fishes would have. Without considering such effects, the data from other predator control programs might be ambiguous. Bibliography 186 Bibliography Abrams, P. A. and Walters, C. (1996). Invulnerable prey and the paradox of enrichment. Ecology, 77:1125-1133. Anras, M. L. B., Cooley, P. M., Bodaly, R. A., Anras, L., and Fudge, R. J. P. (1999). Movement and habitat use by lake whitefish during spawning in a boreal lake: Integrating acoustic telemetry and geographic information systems. Transactions of the American Fisheries Society, 128:939-952. Arnekleiv, J. V. and Kraabol, M. (1996). Migratory behaviour of adult fast-growing brown trout (Salmo trutta, L) in relation to water flow in a regulated norwegian river. Regulated Rivers Research and Management, 12:39-49. Bainbridge, R. (1958). The speed of swimming as related to size and to the frequency and amplitude of the tail beat. Journal of Experimental Biology, 35:109-133. Barfoot, C. A., Gadomski, D. M., and Wertheimer, R. H. (1999). Growth and mortality of age-0 northern squawfish, Ptychocheilus oregonensis, rear ing in shoreline habitats of a Columbia River reservoir. Environmental Biology of Fishes, 54:107-115. Beamesderfer, R. (1992a). Reproduction and early life history of northern squawfish, Ptychocheilus oregonensis, in Idaho's St. Joe River. Environmen tal Biology of Fishes, 35:231-241. Beamesderfer, R. C. (1992b). Implementation ofâ€˘ the northern squawfish sport-reward fishery on the Columbia and snake rivers. Northwest Science, 66. Beamish, R. J. and McFarlane, G. A. (1983). The forgotten requirement for age validation in fisheries biology. Transactions of the. American Fisheries Society, 112:735-743. Bibliography 187 Benson, A. J., McFarlane, G., Allen, S. E., and Dower, J. (2002). Changes in pacific hake (Merluccius productus) migration patterns and juvenile growth related to the 1989 regime shift. Canadian Journal of Fisheries and Aquatic Sciences, 59:1969- 1979. Beverton, R. and lies, T. (1992). Mortality rates of 0-group plaice (Platessa platessa L. ), dab (Limanda limanda L. ) and turbot (Scophthalmus max-imus L. ) in european waters, density-dependence of mortality rates and some demographic implications. Netherlands Journal of Sea Research, 29:61-79. Biro, P. A., Post, J. R., and Abrahams, M. V. (2005). Ontogeny of en ergy allocation reveals selective pressure promoting risk-taking behaviour in young fish cohorts. Proceedings of the Royal Society of London - Series B: Biological Sciences, 272:1443-1448. Block, B. A., Teo, S. L. H., Walli, A., Boustany, A., Stokesbury, M. J. W., Farwell, C. J., Weng, K. C, Dewar, H., and Williams, T. D. (2005). Elec tronic tagging and population structure of Atlantic bluefin tuna. Nature, 434:1121-1127. Brattey, J. and Cadigan, N. (2004). Estimation of short-term tagging mor tality of adult atlantic cod (Gadus morhua). Fisheries Research, 66:223-233. Burr, P. and Doksum, K. (1980). Inferring the distribution of the parame ters of the von bertalanffy growth model from length moments. Canadian Journal of Fisheries and Aquatic Sciences, 45:1179-1788. Campana, S. (2001). Accuracy, precision and quality control in age determi nation, including a review of the use and abuse of age validation methods. Journal of fish biology, 59:197-242. Campana, S. E. and Thorrold, S. R. (2001). Otoliths, increments, and ele ments: keys to a comprehensive understanding of fish populations? Cana dian Journal of Fisheries and Aquatic Sciences, 58:30-38. Carlander, K. (1969). Handbook of freshwater fishery biology, volume 1. The Iowa State University Press, Ames. Iowa. Bibliography 188 Childs, M. and Clarkson, R. (1996). Temperature effects on swimming per formance of larval and juvenile Colorado squawfish: implications for sur vival and species recovery. Transactions of the American Fisheries Society, 125:940-947. Clark, J. S., Ferraz, G. A., Oguge, N., Hays, H., and DiCostanzo, J. (2005). Hierarchical bayes for structured, variable populations: from recapture data to life-history prediction. Ecology, 86:2232-2244. Cormack, R. M. (1968). Estimates of survival from sighting of marked animals. Biometrika, 51:429-438. Craig, J.. and Kipling, C. (1983).. Reproductive effort versus the environ ment: case histories of Winclemere perch, Perca fluviatilis L. and pike, Esox lucius. Journal of Fish Biology, 22:713-727. de Roos, A. M., Leonardsson, K., Persson, L., and Mittelbach, G. G. (2002). Ontogenetic niche shifts and flexible behavior in size-structured populations. Ecological Monographs, 72:271-292. De Valpine, P. and Hastings, A. (2002). Fitting population models incorpo rating process noise and observation error. Ecological Monographs, 72:57-76. Deriso, R., Quinn, T.J., I., and Neal, P. (1985). Catch-age analysis with auxiliary information. Canadian Journal of Fisheries a,nd Aquatic Sciences, 42:815-824. Ebener, M. (1982). Loss of floy anchor tags from lake whitefish. North American Journal of Fisheries Management, 2:90-93. . Ebener, M. and Copes, F. (1982). Loss of floy anchor tags from lake white-fish. North American Journal of Fisheries Management, 2:90-93. Eveson, J., Laslett, G., and Polachek, T. (2004). An integrated model for growth incorporating tagrecapture, lengthfrequency, and direct aging data. Canadian Journal of Fisheries and Aquatic Sciences, 61:292-304. Fabens, A. (1965). Properties and fitting of the von bertalanffy growth curve. Growth, 29:265-289. Bibliography 189 Feldman, K. A., Gruber, S., De Marignac, J., and Ashley, M. (2002). Ge netic tagging to determine passive integrated transponder tag loss in lemon sharks. Journal of Fish Biology, 61:13091313. Fisher, J. A. D. and Frank, K. T. (2004). Abundance-distribution relation ships and conservation of exploited marine fishes. Marine Ecology-Progress Series, 279:201-213. Fournier, D. A. and Sibert, J. R. (1991). Analysis of length frequency sam ples with relative abundance data for the gulf of maine northern shrimp (Pandalus borealis) by the MULTIFAN method. Canadian Journal of Fish eries and Aquatic Sciences, 48:591-598. Frank, K. and JSrickman, D. (2000). Allee effects and compensatory pop ulation dynamics within a stock complex. Canadian Journal of Fisheries and Aquatic Sciences, 57:513-517. Friesen, T. A. and Ward, D. L. (1999). Management of northern pikeminnow and implications for juvenile salmonid survival in the lower Columbia and Snake Rivers. North American Journal of Fisheries Management, 19:406-420. Fujiwara, M., Kendall, B. E., Nisbet, R. M., and Bennett, W. A. (2005). Analysis of size trajectory data using an energetic-based growth model. Ecology, 86:1441-1451. Funakoshi, S. (1994). Relationship between stock levels and the population structure of the Japanese anchovy. Marine Behavior and Physiology, 21:1â€” 84. Gadomski, D. M., Barfoot, C. A., Bayer, J. M., and Poe, T. (2001). Early life history of the northern pikeminnow in the lower Columbia River basin. Transactions of the American Fisheries Society, 130:250-262. Gelman, A., Carlin, J., Stern, H., and Rubin, D. (1995). Bayesian Data Analysis. Texts in Statistical Science. Chapman and Hall, Boca Raton, first edition. Gerking (1959). The restricted movement of fish populations. Biological Review, 34:221-242. Bibliography 190 Gomi, T., Sidle, R. C., and Richardson, J. (2002). Understanding processes and downstream linkages of headwater systems. Bioscience, 52:905-916. Gowen, C., Young, M. K., Fausch, K. D., and Riley, S. C. (1994). Restricted movement in resident stream salmonids: A paradigm lost? Canadian Jour nal of Fisheries and Aquatic Sciences, 51:2626-2637. Haist, V., Fournier, D. A., and Saunders, M. (1999). Reconstruction of B.C. sablefish stocks, 1966-1998, and catch projections for 1999, using an integrated catch-age mark-recapture model with area and depth movement. Canadian Stock Assessment Secretariate Research, Doc.:99/79. Hanson, J. and Chouinard, G. (1992). Evidence that size-selective mortality affects growth of Atlantic cod (Gadus morhua L.) in the southern Gulf of St. Lawrence. Journal of Fish Biology, 41:31-41. Healey, M. (1980). Growth and recruitment in experimentally exploited lake whitefish (Coregonus clupeaformis) populations. Canadian Journal of Fisheries and Aquatic Sciences, 37:255-267. Holling, C. (1959). The components of predation as revealed by the study of small mammal predation on the european pine sawfly. The Canadian Entomologist, 91:293-320. James, I. (1991). Estimation of von Bertalanffy growth parameters from recapture data. Biometrics, 47:1519-1530. Jensen, A. (1997). Origin of the relation between k and Linf and synthesis of relations among life history parameters. Canadian Journal of Fisheries and Aquatic Sciences, 54:987-989. Jeppson, P. W. (1959). Ecology and control of the Columbia squawfish in northern idaho lakes. ' Transactions of the American Fisheries Society, 88:197-202. Jonsen, I. D., Mills Flemming, J., and Myers, R. A. (2005). Robust state-space modelling of animal movement. Ecology, 86:2874-2880. Jonsen, I. D., Myers, R. A., and Flemming, J. M. (2003). Meta-analysis of animal movement using state-space models. Ecology, 84:3055-3063. Bibliography 191 Julliard, R., Stenseth, N. C, Gjosaeter, J., Lekve, K., Fromentin, J. M., and Danielssen, D. S. (2001). Natural mortality and fishing mortality in a coastal cod population: A release-recapture experiment. Ecological Applications, 11:540-558. Kerr, S. (1971). Analysis of laboratory experiments on growth efficiency of fishes. Journal of the fisheries research board of Canada, 28:801808. Kitchell, J., Stewart, D., and Weininger, D. (1977). Applications of a bioen ergetics model to yellow perch [Perca flavescens) and walleye (Stizoste-dion vitreum vitreum). Journal of the Fisheries Research Board of Canada, 34:19221935. Koslow, J. (1992). Fecundity and the stock-recruitment relationship. Cana dian Journal of Fisheries and Aquatic Sciences, 49:210-217. Koslow, J., Bell, J., Virtue, P., and Smith, D. (1995). Fecundity and its variability in orange roughy: effects of population density, condition, egg size and senescence. Journal of Fish Biology, 47:1063-1080. Kristiansen, T. and Svasand, T. (1998). Effects of size-selective mortality on growth of coastal cod illustrated by tagging data and an individual-based growth and mortality model. Journal of fish biology, 52:688-705. Kwain, W. (1981). Population dynamics and exploitation of rainbow trout in stokely creek, eastern lake superior. Transactions of the American Fish eries Society, 110:210-215. Laslett, G., Eveson, J., and Polachek, T. (2002). A flexible maximum like lihood approach for fitting growth curves to tag-recapture data. Canadian Journal of Fisheries and Aquatic Sciences, 59:976-986. Lebreton, J.. Burnham, K., Clobert, J., and Anderson, D. (1992). Modelling survival and testing biological hypotheses using marked animals: a unified approach using case studies. Ecological Monographs, 62:67-118. Lee, R. M. (1912). An investigation into the methods of growth determina tion in fishes. Conseil Permanent International Sur L 'Exploration du Mer, 63:35. Bibliography 192 Liermann, M. and Hilborn, R. (1997). Depensation in fish stocks. Canadian Journal of Fisheries and Aquatic Sciences, 54:1976-1984. Liermann, M. and Hilborn, R. (2001). Depensation: evidence, models a,nd implications. Fish and Fisheries, 2:33-58. Mangel, M. and Levin, P. S. (2005). Regime, phase and paradigm shifts: making community ecology the basic science for fisheries. Philosophical Transactions of the Royal Society B-Biological Sciences, 360:95-105. Marshall, C. and Frank, K. (1999). The effect of interannual variation in growth and condition of haddock recruitment. Canadian Journal of Fish eries and Aquatic Sciences, 56:356-363. McGlennon, D. and Partington, D. (1997). Mortality and tag loss in dart and loop-tagged captive snapper, Pagrus auratus (sparidae), with compar isons to relative recapture rates from a field study. New Zealand Journal of Marine and Freshwater Research, 31:39-49. McHich, R., Auger, P. M., de la Parra, R. B., and Raissi, N. (2002). Dynam ics of a fishery on two fishing zones with fish stock dependent migrations: aggregation and control. Ecological Modelling, 158:51-62. Munch, S. and Conover, D. (2002). Accounting for local physiological adap tation in bioenergetic models: testing hypotheses for growth rate evolu tion by virtual transplant experiments. Canadian Journal of Fisheries and Aquatic Sciences, 59:393403. Muoneke, M. (1992). Loss of-floy anchor tags from white bass. North American Journal of Fisheries Management, 12:819-824. Myers, R., Bridson, J., and Barrowman, N. (1995a). Summary of worldwide spawner and recruitment data. Canadian Technical Reports of Fisheries and Aquatic Sciences, 2024. Myers, R. and Hoenig, J. (1997). Direct estimates of gear selectivity from multiple tagging experiments. Canadian Journal of Fisheries and Aquatic Sciences, 54:1-9. Myers, R. A., Barrowman, N. J., Hutchings, J. A., and Rosenberg, A. A. (1995b). Population dynamics of exploited fish stocks at low population levels. Science, 269:1106-1108. Bibliography 193 Myers, R. A., Bowen, K. G., and Barrowman, N. J. (1999). Maximum repro ductive rate of fish at low population sizes. Canadian Journal of Fisheries and Aquatic Sciences, 56:2404-2419. Myers, R. A. and Cadigan, N. G. (1993). Density-dependent juvenile mor tality in marine demersal fish. Canadian Journal of Fisheries and Aquatic Sciences, 50:1576-1590. Naslund, I. (1990). The development of regular seasonal habitat shifts in a landlocked arctic charr Salvelinus-Alpinus L. population. Journal of Fish Biology, 36:401-414. Olson, M. H. (1996). Ontogenetic niche shifts in largemouth bass: Variabil ity and consequences for first-year growth. Ecology, 77:179-190. . Olsson, I. C. arid Greenberg, L. A. (2004). Partial migration in a landlocked brown trout population. Journal of Fish Biology, 65:106-121. Osenberg, C. W., Olson, M. H., and Mittelbach, G. G. (1994). Stage struc ture in fishes: Resource productivity and competition gradients. University of South Carolina. Belle W. Baruch Library in Marine Science and Coastal Research Collected Papers, 18:151â€”170. Palmer, M., Phillips, B., and Smith, G. (1991). Application of nonlinear models with random coefficients to growth data. Biometrics, 47:623-635. Paragamian, V. and Beamesderfer, R. (2003). Growth estimates from tagged white sturgeon suggest that ages from fin rays underestimate true age in the Kootenai River, USA and Canada. Transactions of the American Fisheries Society, 132:895-903. Parker, R. M., Zimmerman, M. P., and Ward, D. L. (1995). Variability in biological characteristics of northern squawfish in the lower Columbia and Snake Rivers. Transactions of the American Fisheries Society, 124:335-346. Parma, A. M. and Deriso, R. (1990). Dynamics of age and size composition in a population subject to size-selective mortality: effects of phenotypic variability in growth. Canadian Journal of Fisheries and Aquatic Sciences, 47:274-289. Bibliography 194 Pauly, D. (1980). On the interrelationships between natural mortality, growth-parameters, and mean environmental temperature in 175 fish stocks. Journal Du Conseil Permanent Sur I'Explotation de Mer, 39:175-192. Pauly, D. (1990). Length converted catch curves and the seasonal growth of fishes. ICLARM Fishbyte, 8:33 - 38. Persson, L. and Eklov, P. (1995). Prey refuges affecting interactions between piscivorous perch and juvenile perch and roach. Ecology, 76:70-81. Persson, L. and Greenberg, L. A. (1990). Optimal foraging and habitat shift in perch (Perca fhiviatilis) in a resource gradient. Ecology, 71:1699-1713. Peters, J. (1964). Summary of calculated growth data on Montana fishes, 1948-61. Montana Fish and Game Dept. Fisheries Division. Petersen,.J. H. and DeAngelis, D. L. (1992). Predation by northern squaw fish on live and dead juvenile chinook salmon. Transactions of the American Fisheries Society, 121. Petersen, J. H. and Ward, D. L. (1999). Development and corroboration of a bioenergetics model for northern pikeminnow feeding on juvenile salmonids in the Columbia River. Transactions of the American Fisheries Society, 128:784-801. Pidgeon, R. (1981). Diet and growth of rainbow trout, salmo gairdneri richardson in two streams on the new england tableland, new south wales. Australian Journal of Marine Freshwater Research, 32:967-974. Pierce, R. and Tomcko, C. M. (1993). Tag loss and handling mortality for northern pike marked with plastic anchor tags. North American Journal of Fisheries Management, 13:613-615. Post, J. (1990). Metabolic allometry of larval and juveniles yellow perch (perca flavescens): in situ estimates and bioenergetics models.. Canadian Journal of Fisheries and Aquatic Sciences, 47:554-560. Post, J., Parkinson, E., and Johnston, N. (1999). Density-dependent pro cesses in structured fish populations: interaction strengths in whole-lake experiments. Ecological Monographs, 69:155-175. Bibliography 195 Post, J. R. and Parkinson, E. A. (2001). Energy allocation strategy in young fish: allometry and survival. Ecology, 82:1040-1051. Power, M. and van den Ffeuvel, M. (1999). Age-0 yellow perch growth and its relationship to temperature. Transactions of the American Fisheries Society, 128:687-700. Ricker, W. (1941). The consumption of young sockeye salmon by predaceous salmon by predaceous fish. Journal of the Fisheries Research Board of Canada, 5:293-313. Ricker, W. (1969). Effects of size-selective mortality and sampling bias on estimates of growth, mortality, production and yield. Journal of the Fisheries Research Board of Canada, 26:479-541. Rieman, B. E. and Beamesderfer, R. C. (1990). Dynamics of a north ern squawfish population and the potential to reduce predation on juvenile salmonids in a Columbia River reservoir. North American Journal of Fish eries Management, pages 228-241. Rikardsen, A. H., Woodgate, M., and Thompson, D. A. (2002). A compar ison of floy and soft vlalpha tags on hatchery Arctic charr, with emphasis on tag retention, growth and survival. Environmental Biology of Fishes, 64:269-273. Rivot, E., Prevost, E., Parent, E., and Bagliniere, J. L. (2004). A bayesian state-space modelling framework for fitting a salmon stage-structured pop ulation dynamic model to multiple time series of field data. Ecological Modelling, 179:463-485. Rooker, J. R., H., S. D., Zdanowicz, V. S., De Metro, G., and Orsi Relini, L. (2003). Identification of Atlantic bluefin tuna (Thunnus thynnus) stocks from putative nurseries using otolith chemistry. Fisheries Oceanography, 12:75-84. Rose, K. A., Cowan, J. H., Winemiller, K. O., Myers, R. A., and Hilborn, R. (2001). Compensatory density dependence in fish populations: importance, controversy, understanding and prognosis.' Fish and Fisheries, 2:293-327. Bibliography 196 Rothchild, B., Osborn, T., Dickey, T., and Farmer, D. (1989). The physical basis for recruitment variability in fish populations. Journal du Conseil International pour L'Exploration du Mer, 45:136-145. Ruiz-Campos, G., Pister, E., and Compean-Jimenez, G. (1997). Age and growth of nelson's trout, oncorhynchus mykiss nelsoni from arroyo san rafael, sierra san pedro martir, baja caffiornia, mexico. Southwest Natu ralist, 42:74-85. Sainsbury, K. (1980). Effect of individual variability on the von Berta lanffy growth equation. Canadian Journal of Fisheries and Aquatic Sci ences, 37:241-247. Scheffer, M., Carpenter, S., Foley, J. A., Folke, C, and Walker, B. (2001a). Catastrophic shifts in ecosystems. Nature, 413:591-596. Scheffer, M., Carpenter, S., Foley, J. A., Folke, C, and Walker, B. (2001b). Catastrophic shifts in ecosystems. Nature, 413:591-596. Scheffer, M. and Carpenter, S. R. (2003). Catastrophic regime shifts in ecosystems: linking theory to observation. Trends in Ecology and Evolution, 18:648-656. Schnute (1983). A new approach to estimating populations by the removal method. Canadian Journal of Fisheries and Aquatic Sciences, 40:2153-2169. Schuter, B. and Post, J. (1990). Climate, population viability and the zoogeography of fishes. Transactions of the American Fisheries Society, 119:314-336. Shelton, P. A. and Harley, B. P. (1999). Should depensation be dismissed as a possible explanation for the lack of recovery of the northern cod (Gadus m.orhua) stock? Canadian Journal of Fisheries and Aquatic Sciences, 56:1521-1524. Sih, A., Crawley, P., McPeek, M., Petranka, J., and Strohmeier, K. (1985). Predation, competition and prey communities: a review of field experi ments. Annual reviews in ecology and'systematics, 16:269-311. Bibliography 197 Sinclair, A., Swain, D., and Hanson, J. (2002a). Disentangling the effects of size selective mortality, density and temperature on length at age. Canadian Journal of Fisheries and Aquatic Sciences, 59:372-382. Sinclair, A., Swain, D., and Hanson, J. (2002b). Measuring changes in the direction and magnitude of size-selective mortality in a commercial fishery. Canadian Journal of Fisheries and Aquatic Sciences, 59:361-371. Steigenberger, L. W. and Larkin, P. (1974). Feeding activity rates of di gestion of northern squawfish (Ptychocheilus oregonensis). Journal of the Fisheries Research Board of Canada, 31:411-420. Swanson, B. and Schram, S. (1996). Comparison of three nonlinear mod els to describe long-term tag shedding by lake trout. Transactions of the American Fisheries Society, 125:264-273. Tonn, W., Holopainen, I. J., and Paszkowski, C. (1994). Density dependent effects and the regulation of crucial carp populations in single-species ponds. Ecology, 75:824-834. Tonn, W. and Paszkowski, C. (1992). Piscivory and recruitment: mecha nisms structuring prey populations in small lakes. Ecology, 79:951-958. Vander Zanden, M. J., Essington, T. E., and Vadeboncoeur, Y. (2005). Is pelagic top-down control in lakes augmented by benthic energy pathways? Canadian Journal of Fisheries and Aquatic Sciences, 62:1422-1431. von Bertalanffy, L. (1934). A quantitative theory of organic growth. Human Biology, 10:181-213. Walters, C. and Christensen, V. (2004). Ecopath with Ecosim: methods, capabilities and limitations. Ecological Modelling, 172:109-139. Walters, C, Christensen, V., and Pauly, D. (1997). Structuring dynamic models of exploited ecosystems from trophic mass-balance assessments. Re views in Fish Biology and Fisheries, 7:139-172. Walters, C. and Juanes, F. (1993). Recruitment limitation as a consequence of natural selection for use of restricted feeding habitats and predation risk taking by juvenile fishes. Canadian Journal of Fisheries and Aquatic Sci ences, 50:2058-2070. Bibliography 198 Walters, C. and Kitchell, J. (2001). Cultivation/depensation effects on juve nile survival and recruitment: implications for the theory of fishing. Cana dian Journal of Fisheries and Aquatic Sciences, 58:39-50. Walters, C. and Korman, J. (1999). Linking recruitment to trophic fac tors: revisiting the Beverton-Holt recruitment model from a life history and multispecies perspective. Reviews in Fish Biology and Fisheries, 9:187-202. Walters, C. and Martell, S. J. (2004). Fisheries Ecology and Management. Princeton University Press. Walters, C, Pauly, D., Christensen, V., and Kitchell, J. (2000). . Repre senting density dependent consequences of life history strategies in aquatic ecosystems: Ecosim II. Ecosystems, 3:70-83. Walters, C. and Post, J. R. (1993). Density-dependent growth and compet itive asymmetries in size-structured fish populations: a theoretical model and recommendations for field experiments. Transactions of the American Fisheries Society, 122:34-45. Wang, Y. G., Thomas, M., and Somers, I. (1995). A maximum likelihood approach for estimating growth from tagrecapture. Canadian Journal of Fisheries and Aquatic Sciences, 52:252 259. Werner, E. E. and Gilliam, J. F. (1984). The ontogenetic niche and species interactions in size-structured populations. Annual Review of Ecology and Systematics, 15:393-425.
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Growth and survival responses to experimental fishing : models, experiments and lessons from the Northern.. Taylor, Nathan Gabriel 2006-12-31
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Title | Growth and survival responses to experimental fishing : models, experiments and lessons from the Northern pikeminnow of South Central British Columbia |
Creator |
Taylor, Nathan Gabriel |
Date | 2006 |
Date Issued | 2010-01-18T20:46:43Z |
Description | The objective of this was study was to determine if species specific fishing could produce "cultivation-depensation effects" in an aquatic ecosystem with two predatory, competing fish species. I identified a unique stock of northern pikeminnow living in series of connected lakes that has obligatory rearing in specific nursery lakes; developed two novel likelihoods to measure the growth, movement and mortality responses; developed an ecosystem model to predict how the system would respond to fishing, and finally, compared the ecosystem modeling predictions to observed responses. My research showed northern pikeminnow in South Central B.C. have obligatory rearing in specific nursery lakes then disperse to other lakes as adults. I argue that this large scale spatial ontogeny can be solely explained by temperature cues to spawn and that the distribution of adults is determined by density-dependent dispersal that equalize very large productivity and effective density differences between lakes. I showed that in spite of being included in many stock assessments, and being used as proxies for natural mortality estimates and for exploitation rate targets, von Bertalanffy growth parameters are not generally estimated correctly. The data used to do so are virtually always biased due to: size-selective gears, populations subjected to fishing and natural mortality and in some cases, size-dependent movement. I developed two new likelihoods to simultaneously estimate growth and mortality parameters: one for length-age data, and another for mark-recapture data. The first performs well across a range of recruitment anomalies and steady state fishing mortalities but fails when fishing rates have been variable (especially increasing) and when gear selectivity is dome-shaped. The second likelihood works well with simulated data but is not robust to assumptions of constant recruitment and measurement error being violated. I combined length-age and mark-recapture data to show using simulated sampling that it is possible to simultaneously estimate growth, mortality, and movement parameters where sufficient numbers of fish are observed moving. The assumptions required for these models to perform well are very restrictive. I used a simple ecosystem model and compared the predictions to observed responses following depletion fishing in two-fish lake systems with rainbow trout and northern pikeminnow. Consistent with model predictions, growth was slower and mortality of juvenile rainbow trout higher relative to the control in lakes where northern pikeminnow were removed, while adult rainbow trout survival remained unchanged. Visual survey indices of northern pikeminnow fry indicated survival of 1+ fish worsened and 2+ improved following fishing. Consistent with model predictions, no obvious mortality or growth responses were observed in adult fish in either rainbow trout or northern pikeminnow removals. While the agreement between the model and observations was encouraging, field testing such complex predictions was fraught with difficulty. The probability distributions of the parameters of interest were very broad. Also, the model predicts that survival and behavioral dynamics producing the greatest differences in direction and magnitude of ecosystem response occur in size classes of fish and groups of zooplankton that are difficult to observe. It was not possible to conclude whether an alternate state was produced through cultivation-depensation effects. To do so would require longer term data on recruitment responses, vulnerability exchange processes and survival data of young age classes of fish. This study identifies several shortcomings in our ability to predict and detect how ecosystems will respond to fishing. First, our ability to measure even simple response variables such as growth and mortality is not good. Secondly, even if we could, the direction and magnitude of these responses can be highly counter-intuitive. Finally, those processes with the most violent effects on our predictions are those for which we have very little information, namely dynamics determining the spatial distribution of the stock, the dynamics of young fish and behaviorally mediated predation rates. |
Genre |
Thesis/Dissertation |
Type |
Text |
Language | eng |
Collection |
Retrospective Theses and Dissertations, 1919-2007 |
Series | UBC Retrospective Theses Digitization Project |
Date Available | 2010-01-18 |
Provider | Vancouver : University of British Columbia Library |
Rights | For non-commercial purposes only, such as research, private study and education. Additional conditions apply, see Terms of Use https://open.library.ubc.ca/terms_of_use. |
DOI | 10.14288/1.0074899 |
URI | http://hdl.handle.net/2429/18585 |
Degree |
Doctor of Philosophy - PhD |
Program |
Zoology |
Affiliation |
Science, Faculty of Zoology, Department of |
Degree Grantor | University of British Columbia |
Campus |
UBCV |
Scholarly Level | Graduate |
Aggregated Source Repository | DSpace |
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