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Short-term responses of songbirds to alternate harvesting methods in a high elevation forest Leupin, Ernest E. 2002

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S H O R T - T E R M RESPONSES O F S O N G B I R D S T O A L T E R N A T E H A R V E S T I N G M E T H O D S I N A H I G H E L E V A T I O N FOREST  by Ernest. E. Leupin B.Sc, The University o f B r i t i s h C o l u m b i a , 1992  A THESIS SUBMITTED IN P A R T I A L F U L F I L L M E N T OF THE REQUIREMENTS FOR T H E D E G R E E OF M A S T E R OF SCIENCE in  THE F A C U L T Y OF G R A D U A T E STUDIES THE F A C U L T Y OF FORESTRY Department of Forest Sciences Centre for Applied Conservation Research  We accept this thesis as conforming to the required standards  THE UNIVERSITY OF BRITISH C O L U M B I A July, 2002 ©Ernest E. Leupin, 2002  In  presenting  degree freely  at  this  the  available  copying  of  department publication  of  in  partial  fulfilment  of  the  University  of  British  Columbia,  I  agree  for  this or  thesis  reference  thesis by  this  for  his thesis  and  scholarly  or  her  for  Date  DE-6  (2/88)  ftUgn  Columbia  '2JQOZ ^  I further  purposes  gain  that  agree  may  be  It  is  representatives.  financial  permission.  T h e U n i v e r s i t y o f British Vancouver, Canada  study.  requirements  shall  not  that  the  Library  an  granted  by  allowed  advanced  shall  permission  understood be  for  the that  without  for head  make  it  extensive of  my  copying  or  my  written  ABSTRACT  Silvicultural alternatives to clearcutting have been promoted in forests of British Columbia to attempt to simulate short-term natural disturbances typical of certain forest types as these cuts are hypothesized to mitigate negative impacts on wildlife dependent on forests. However, the potential effects of these harvesting activities have not been studied enough to evaluate their success in mitigating wildlife impacts. I examined the response of songbirds breeding in high elevation, Engelmann spruce-subalpine fir forests (Sicamous Creek Research Forest) to alternative forms of forest harvesting using the variable circular method of point counting to determine relative abundance. The experimental harvesting treatments at Sicamous created openings (perforations) in the original forest that ranged in size from lOha clearcuts to small gaps (0.01 ha) resulting from the harvest of selected trees. The community of songbirds that breed in the Sicamous Creek Research Forest was monitored over a five-year period that included both pre- and post-harvest conditions. The original songbird community remained relatively unchanged after harvest and among the various treatments. Few new species colonized the newly created habitats (openings) and did so in very small numbers. Golden-crowned kinglet declined significantly post-harvest in harvested areas with the most pronounced declines in selection and 10 ha treatments. Conversely, dark-eyed junco responded positively to the harvesting and increased in abundance in all harvested treatments. In general, the creation of a variety of habitats through alternative harvesting methods appears to lessen impacts and allow much of the songbird community to persist in high elevation forests. This persistence may be related to an evolutionary adaptation  of songbirds to small-scale disturbances typical of high elevation forests that alternative harvesting methods simulate. Future research should focus on long-term monitoring to determine reproductive success in the various harvesting techniques.  T A B L E OF CONTENTS  ABSTRACT  ii  LIST OF T A B L E S . . .  vi  LIST OF FIGURES  vii  ACKNOWLEDGEMENTS  viii  INTRODUCTION  1  Evidence of Landscape effects  1  Issues of Incipient Fragmentation  2  Forestry Impacts on High Elevation Forest Ecosystems and Songbird Communities  4  OBJECTIVES  6  METHODS  9  Study Site  9  Bird Sampling  13  Sampling Design  14  Entire Study Area Sampling  ....14  Individual Treatment sampling  15  Data Analysis  16  Songbird Community Measures  17  Individual Species Abundance Study Area Comparisons Treatment Comparisons  18 19 20  RESULTS  21  Community Structure of Songbirds Inhabiting the Sicamous Creek Research Forest... 21 Changes in Abundance of Individual Species  27 iv  DISCUSSION  34  CONCLUSIONS  40  L I T E R A T U R E CITED  43  A P P E N D I X I. Sample data sheet for songbird sampling at Sicamous Creek  50  v  LIST OF TABLES  Table 1. Characteristics of experimental treatments. For each treatment approximately one third of the wood volume was removed 11  Table 2. Effective detection distances for seven common species at Sicamous Creek  19  Table 3. Proportional abundance of all songbird species detected in 100m radius census points (n=77) before and after harvest in the Sicamous Creek study area. 22  Table 4. Comparison of community parameters for uncut and treatment sites before and after harvest 24  Table 5. Comparison of community parameters (mean and (SE)) for individual treatment units 1 and 2 years postharvest 25  Table 6. Mean abundance (SE) of old and non old-growth species detected per census points in uncut and harvested treatments prior to and after harvest  26  Table 7. Mean (SE) detections per 3 point count stations of old and non old-growth species at treatment units 28  Table 8. Mean (1 SE) number of detections per census point of "core" songbird species in uncut and treatment areas prior to and after harvest. Number of detections was averaged for 2 years pre-harvest and 2 years post-harvest 31  Table 9. Mean detections (SE) per 3 point count stations of core species at individual treatment units  32  LIST OF FIGURES  Figure 1. Relative Location of the Sicamous Creek Research Forest  10  Figure 2. Experimental layout and treatments. Dashed line indicates the sampling extension of one uncut reserve  12  Figure 3. Aerial view (south-west) of the resulting forest matrix after harvest....;  13  Figure 4. Sampling strategies and point layout for: A . study area; and B experimental treatment units and controls 16  Figure 5. Example of two species that showed opposing responses to harvesting when examined prior to and after harvest, and at the individual treatment levels following harvest  33  ACKNOWLEDGEMENTS  I would like to thank everyone that was involved (directly or indirectly) with the completion of this thesis. To my committee members, Tom Dickinson, Kathy Martin, and Sue Glenn, all of who were extremely patient and put me "back on track" on several occasions. I also thank them for all the constructive comments that helped this thesis become what it is today. To Michael Murphy, Sean Bennett, and Dave Pehl, for the countless hours of field work. Their positive attitude and sense of humor made for great field seasons. I would also like to thank the research team at the Sicamous Creek experimental forest, in particular Alan Vyse, and Walt Klenner. Finally, I would like to thank my wife, Reena, and daughters Jennika (Tatoo), and Brittaney (Brinty), for their encouragement and the patience they demonstrated throughout this very long process.  Funding for this project was provided by Ministry of Forest, Silviculture Branch in Victoria, and Forest Renewal B C . Project administration was provided by the British Columbia Conservation foundation.  I dedicate this thesis to my parents, who never stopped believing in me.  viii  INTRODUCTION Declines of Neotropical songbird species have been attributed, for the most part, to destruction and degradation of natural habitats (Fahrig 1997, Finch and Stangel 1994). In forested areas, these anthropogenic activities usually result in fragmented landscapes that lower abundances of forest-dependent songbird species (Robinson 1992). Factors associated with the declines include songbird responses to the insularization phenomenon as related to the theory of island biogeography (Mac Arthur and Wilson 1967, Hunter 1990) and other factors that result from the concomitant creation of edges, including increased predation rates (Yahner and Scott 1988, Hartley and Hunter 1998), competition (Faaborg et al 1995), and brood parasitism (Robinson et al 1995, Brittingham and Temple 1983).  Evidence of Landscape effects  Nearly all of the evidence that support landscape explanations of bird declines stem from studies carried out in large-scale fragmented landscapes surrounded by matrices of agricultural, suburban, or urban landscapes and, in most cases, in areas where fragmentation had taken place decades prior to the study (Sallabanks et al 2000; e.g. Askins et al 1987, Robbins et al 1989). In contrast, similar studies in forest-dominated landscapes have reported mixed responses by various taxa (including songbirds) to the hypothesized effects (Debinski and Holt 2000). Schmiegelow (1997) reported a resiliency of the boreal songbird community to various levels of fragmentation in a boreal forest in Alberta. Similarly, Schieck et al (1995) found only weak evidence to support relationships between songbird species richness/abundance and patch size in coastal montane forest fragments of British  Columbia. Others however, have found supporting evidence of the fragmentation paradigm in primarily forested landscapes. Enoksson et al (1995) found that certain songbird species responded negatively to isolated patches of deciduous forests embedded in a coniferous forest matrix in south central Sweden. Similarly, Norton and Hannon (1997) found that 39% of species declined after logging in a boreal mixedwood forest in Alberta. Martin and Eadie (1999) found a strong and positive response of cavity nesting bird communities to forest edges and degree of natural fragmentation in interior Douglas fir forest ecosystems in B C . Thus, there is no clear agreement in terms of how fragmentation affects songbird species in forest-dominated landscapes.  Issues of Incipient Fragmentation  Despite the number of habitat fragmentation studies conducted, few have documented the responses of songbirds in extensively forested landscapes where fragmentation is incipient (Robinson and Robinson 1999, Hagan et al 1996, Buford and Capen 1999). The process of habitat fragmentation typically begins with the creation of small openings into otherwise continuous forest tracts through a process termed perforation (Hunter 1996). Timber harvesting, and in particular selective and group selection logging are two harvesting systems that create small openings in otherwise continuous forest tracts (Chambers et al 1999).  Multiple openings potentially have negative consequences for the original songbird community. Although fragmentation per se has not occurred, the perforation process can result in negative impacts resulting from habitat loss and the creation of edges. The creation  2  of multiple openings maximizes the ratio of edge to opening area and may represent a worse case scenario for forest-interior bird populations (Robinson and Robinson 1999, Thompson 1993). Furthermore, these openings represent a net loss in forest habitat available. Recent studies have concluded that habitat loss may play a much more important role in songbird declines than spatial configuration of habitats (e.g. Schmiegelow and Monkkonen 2002). A model examining the relative impacts of fragmentation and habitat loss on organisms also suggests that habitat loss has a much larger impact on population extinctions than habitat fragmentation (Fahrig 1997). Thus both the configuration and magnitude of forest retention may be important in determining the impacts of these harvesting methods in predominantly intact forest ecosystems (Drolet et al. 1999).  In contrast, multiple openings (gaps) may have potentially little effect on forestdependent songbirds if they are created in such a way that they simulate natural disturbance processes (Robinson and Robinson 1999). For example, if the openings created resemble those typically created by treefall or localized insect outbreaks, then some species, or the entire assemblage of species inhabiting that area may be evolutionarily adapted to accommodate such changes (Steventon et al 1998, Rudickny and Hunter 1993). In addition, nest predation, brood parasitism, and competition by colonizing species in forested landscapes may be mitigated because of the remoteness of an area; species responsible for these impacts, which are usually associated with human developments (e.g. corvids, brownheaded cowbirds) may be unable to colonize the newly created habitats and thus interact with the original songbird community.  3  Recent studies investigating the responses of the creation of small openings via these silvicultural methods have concluded that this practice has little effect on the songbird community. In continuous hardwood forests, Robinson and Robinson (1999) reported that the removal of 15-50% of the wood volume using a combination of selective harvest and group selection harvest (0.02-0.4 ha) in a hardwood forest had little effect on most bird species that typically occupy mature closed-canopy forests. Germaine et al (1997) also reported similar results, where 20-36% of the forested area was removed using 0.04 ha openings. In conifer-dominated landscapes, Chambers et al (1999), found that species composition was similar in uncut and small patch cut (0.02 ha) treatment stands where 30% of the wood volume was removed. Similarly, Steventon et al (1998) concluded that combinations of selection cut and small opening cuts 0.1 to 0.5 ha in size at two wood removal intensities (30% and 60%) supported songbird communities similar to those found in undisturbed mature forests in the first two years after harvest, although species composition in the heavier removal treatment showed some shift towards species typical of clearcuts.  Forestry Impacts on High Elevation Forest Ecosystems and Songbird Communities  High elevation forests are characterized by short growing seasons, extreme temperatures, and a comparatively simpler resource spectrum (Sabo 1980). As a result, songbird communities occupying high elevation forests are relatively simple and comprised of a few species that are able to tolerate extreme conditions (Sabo 1980, Sabo and Holmes 1983). High elevation forests are among the most undisturbed habitats remaining on the Pacific Northwest and as such are of important conservation concern (Martin 2001). As  4  lower elevation forests are degraded, mature forest-dependent songbird species that occur in a broad range of elevations may ultimately become restricted to these high elevation forests. However, in recent years high elevation forests have been subjected to increased harvesting pressures, which may be changing the overall characteristics of these forest, and the songbird communities that inhabit them. Songbird communities inhabiting high elevation forests are faced with severe environmental constraints that result in high energetic costs for living and breeding, delayed breeding schedules, reproductive stochasticity, and fewer broods per season (Martin 2001). Therefore, harvesting activities may present an additive effect to the existing environmental constraints, which may impact songbird communities of high elevation forests negatively. Despite the increased focus on high elevation forest harvesting, our knowledge of the impacts of these activities on the ecology of these forests is limited (Martin 2001, Thomas 1987).  In British Columbia, high-elevation forests comprise 14% of the landbase (Lloyd et al 1990). Since the early 1970's, an increasing proportion of the annual allowable cut (AAC) in B.C. has come from this biogeoclimatic zone (Yano 1991). In 1991, the harvesting rate was 10,000 ha/yr., approximately one third of the total area harvested annually in the region (Yano 1991) and has without a doubt increased since (D. Lloyd,pers. comm.). Clearcutting has been the preferred harvesting method. However, this large-scale disturbance is not consistent with natural disturbances typical of these forests. The factors mostly responsible for the structural make-up of these forests are guided by small-scale disturbances such as insect outbreaks and windfall (Parish et al 1999).  5  In recent years, the Forest Practices Code of British Columbia has encouraged the use of alternative silviculture practices to clearcutting including selection and group harvest methods. The underlying assumption was that by implementing these harvesting methods, it would promote the development, retention, or creation of late successional features, and mimic presettlement disturbance regimes and thus mitigate impacts on forest interior dependent species. However, literature pertaining to impacts of these alternative silviculture methods in these forests is limited (Raphael 1987, Scott et al 1982). Therefore, i f objectives are to manage for forest dependent species, we need a clearer understanding of how well various alternative silviculture methods perform in maintaining them.  OBJECTIVES  In 1991 the Forest Science section of the Kamloops Forest Region began a study of high-elevation silviculture systems. The study's broad objective has been to provide forest managers and interested groups with ecological information regarding high elevation forests in B C ' s Southern Interior and their responses to various levels and styles of harvesting. More specifically, the goal was to examine the manner in which different silvicultural methods affect a variety of forest ecosystem components, including microclimate, hydrology, wildlife, soil, nutrient cycling, and tree regeneration. This larger initiative involved the experimental harvesting of one 500 ha forest tract using clearcut, group selection, and selection harvest methods and provided the opportunity to determine how these alternative silviculture methods affect songbird populations.  6  In this thesis I examine the responses of the breeding songbird community in a high elevation forest to various sizes of canopy opening size with a constant (30%) wood volume removal at two levels of resolution. First I examine the responses of songbirds to the resulting harvesting matrix at the study area level and here I include available data I collected for the entirety of the study area and compare the two years pre-harvest with the two years post harvest. Secondly, I examine the short-term responses (two and three years after harvest) of the original songbird community to the five treatments.  I predicted that the songbird community would not be affected by the harvesting activities. Recent studies of forest perforation have shown that the removal of approximately 30% of the wood volume via selective and group harvesting methods had little or no effect on the original songbird community for a period of 1 and 2 years post harvest (e.g. Moorman and Guynn 2001, Robinson and Robinson 1999, Chambers et al 1999).  Changes in species richness and abundance are usually the result of a reorganization of the entire species assemblage in the newly harvested areas following clearcut harvest (Spies et al 1990). However, selection and group harvesting methods may not be detrimental to the original songbird community for a number of reasons. First, the creation of small openings may mimic natural disturbance patterns typical of the area and the songbird community could be evolutionarily adapted to cope with these changes (Schmiegelow et al 1997, Schieck et al 1995). Second, the openings created may not be large enough and could be unsuitable for colonizing species (Robinson and Robinson 1999). Finally, population densities of songbirds in high elevation forests are typically lower than those found in low  7  elevation forests (Martin 2001). Therefore, if actual densities are below the carrying capacity (low density), it implies large spatial scale for territories. Therefore small cuts (loss of habitat) would represent only a small proportion of the territory and more likely to represent a natural gap to high elevation songbird species.  At the individual species level, I predicted that species associated with mature forests would either exhibit declines proportional to the habitat lost, or decrease at levels inversely proportional to increasing canopy opening size and that the changes observed would be related to the amount of edge created by the various harvesting treatments. That is, abundance would be lowest in those treatments with the most edge. Conversely, I predicted the opposite for species that have higher habitat plasticity (e.g. species that can be found in a variety of habitats and are commonly associated with disturbances).  Although the sampling layout was different than that of the individual treatments, I opted to examine the responses of songbirds to the resulting forest matrix created by all treatments to take advantage of available pre-treatment data and to validate the results observed at the treatment-level. A discrepancy of results between both levels of analysis would in some cases suggest that small effects not evident at the forest stand level may become significant i f examined at a larger scale (McGarigal and McComb 1995; Boulinier et al 2001).  8  METHODS  Study Site  The Sicamous Creek Research Forest is located approximately 15 km south of the town of Sicamous in the southern interior of British Columbia (Fig 1). The area is estimated to receive 1,000 mm of precipitation annually (Feller 1997). The mean annual temperature is 1°C, and the continuous frost-free period is no more than 40 days, mainly accumulated in the months of July and August (Lloyd and Inselberg 1997). The study area, prior to treatments, consisted of approximately 500 ha of continuous mature forest in the Engelmann sprucesubalpine fir wet-cold (ESSFwc2) biogeoclimatic variant. The site was classified as a homogeneous old-growth stand, age classes 8 and 9 (250-400yrs), with a northeastern aspect and average slope gradients ranging between 20-40% (Puttonen et al. 1997). Subalpine fir (Abies lasiocarpa) (90%) and Engelmann spruce (Picea engelmanii) (10%) were the two codominant tree species (Parish 1997). The understorey was dominated by white rhododendron (Rhododendron albiflorum), oval-leaved blueberry (Vaccinium ovalifolium), and black huckleberry (Vaccinium membranaceum). False azalea (Menziesia ferruginea), and black twinberry (Lonicera involucrata) occurred scattered throughout the site. The herb layer consisted mainly of sitka valerian (Valeriana sitkensis), mountain arnica (Arnica latifolia), oak fern (Gymnocarpium dryopteris), one-leaved foamflower (Tiarella unifoliata), and rosy twisted stalk (Streptopus amplexifolius; Lloyd and Inselberg 1997).  9  Experimental treatments at the Sicamous Creek Research Forest  The experimental design of the Sicamous Creek Research Forest involved five treatments. The main treatment effect was canopy opening size (Table 1, Fig. 2). B y design, one-third of the wood volume was removed across all treatments except, of course, in the uncut reserves.  Table 1. Characteristics of experimental treatments. For each treatment approximately one third of the wood volume was removed. Treatment  Description  Uncut reserve:  no removal  single tree selection:  uniform removal across the block  0.1 1.0 10  ha:  sixty 0.1 ha openings evenly spaced across the blocks  ha:  ten 100 x 100m openings evenly spaced;  ha:  single 320 x 320m opening within the block  Each treatment unit was approximately 30 ha. in size. One hundred metre wide buffer strips were left at adjoining borders between single-tree selection treatment units and 0.1 ha treatment units to minimize confounding effects. Each treatment was replicated three times in a complete randomized block design; however, one stream crossed through the center of one 10 ha treatment the logical location (center of the treatment), therefore, the ten hectare opening had to be placed on one side of the treatment so that it encroached on one uncut reserve, as a result this uncut reserve was smaller than expected. To overcome this  11  logistical problem and retain a third uncut unit, I sampled beyond the boundaries of this unit outside of the boundaries of the existing design (see Fig 2).  N  I  A / I  Roads I Openings  —  Stream  2 Kilometers  Figure 2. Experimental layout and treatments at the Sicamous Creek Experimental Forest. A - Uncut Reserves, B - 0.1 ha openings, C- Selection Cut, D - 1 0 ha opening, E - lha openings . Each Treatment was replicated three times. Dashed line indicates the sampling extension of one uncut reserve.  The study area was harvested in the winter of 1994/95 according to the experimental design (Fig 3). To comply with Workers Compensation Board (WCB) regulations standing dead trees were removed from all treatment units except in the uncut reserves in June and April of 1995 and 1996 respectively. Because removal activities were conducted after 0900 hours the noise created by chain saws did not affect songbird data collection.  12  Figure 3. Aerial view (south-west) of the resulting forest matrix after harvest.  Bird  Sampling  I sampled the songbird community using the variable circular plot method (Reynolds et al 1980). To ensure independence between plots, all points were positioned at least 250m apart (Fig. 4). In each year, point count stations were sampled twice during the breeding season (June and mid July). A l l surveys were conducted between 0500-and 0900 in the morning to coincide with peak singing activity (Ralph et al 1993). Each census was conducted for fifteen minutes preceded by a one-minute rest period to allow for birds nearby to resume their activities after arriving at the census point. Surveys were not conducted on  13  rainy days because singing activity is reduced and less detectable (Robbins 1981). I conducted all surveys in 1993 and 1994 along with a second individual that acted as a recorder. In subsequent years (1995-1997) an additional experienced observer/recorder team participated in the census. In these years, observer variation was standardized across all stations by rotating observers among the point count stations. Aural and visual detections of individual birds were recorded at each point (Appendix I). Locations of birds that were recorded were plotted onto a Cardinal plane to monitor bird movements and thus avoid counting individuals more than once. Method of detection (i.e. song, call, visual) and horizontal distance from the bird to the observer was also recorded.  Sampling Design  Entire Study Area Sampling  The entire study area was sampled 2 years prior to (1993-94) and two years postharvest (1995,1996). Seventy permanent point count stations were established along ten parallel transects placed 250 metres apart (Fig. 4). Each transect contained seven permanent plots placed at equal intervals of 250 metres. Based on the size of territories of the songbirds sampled, this distance was considered appropriate to avoid counting individual birds more than once (see also Delasalla et al, 1996). The systematic arrangement of transects and plots, was chosen because at the time of placement, the actual locations of the future experimental treatments were unknown. Each point was identified using a submetric Global Positioning System (GPS) and incorporated into a digital map of the study area. After treatment  14  application, sixty-nine (15 in uncut reserves units; 54 in treatment units) of the seventy points fell within the experimental study area, and were used for pre and post harvest comparisons. (Fig. 4). Because the number of uncut forest point count stations was anticipated to be low, an additional permanent transect with seven points located in uncut forest had been placed 500 m away from but adjacent to the study site, which increased the number of point count stations for uncut forest to 22.  Individual Treatment sampling  Individual treatments were sampled using a different strategy following harvest in 1996 and 1997. Each replicate treatment unit contained three sampling points strategically placed in each treatment unit for a total of 45 point count stations. Each point was positioned so that its center would lay at least 100 m away from the edges of a treatment and at least 250 m away other point count stations. Point count stations were selected so that each would sample approximately an area that was two-thirds forested, which approximated the amount of forest that remained in each treatment after harvest (Fig 4).  15  A . Sample points for the overall study area pre- and post-harvest  Figure 4. Sampling strategies and point count layout for sampling songbirds at the Sicamous Creek Research Forest  16  Data Analysis  Songbird Community Measures  Species richness (total number of species), total abundance (number of detections of all species), diversity indices, and proportional similarity, were used to describe and compare avian community structure among treatments and years. Species richness values were calculated by averaging observations of all species recorded during census for both census periods in each year. Total relative abundance was determined by averaging all detections made within a 100-meter radius of the observer for the first census period in a given year because numbers of core songbird species detected during the second census period were very low. Shannon diversity H ' = ( - ^ pi log pi) and evenness  H'  i/max,  indices were used  to describe community diversity (Hunter 1990). Community similarity indices were derived using the Renkonen Index (Renkonen 1938 in Krebs 1999), an index value that reflects the relative abundance of each species and the species difference at treatments relative to the uncut reserves. Renkonen index values can range from 100, where both communities support exactly the same species in the same relative abundance, to 0, where none of the species are the same.  For certain community measures (richness and abundance) I grouped species into mature forest associates and others. The criteria for placing a species into either category  17  were based primarily on consistent species-habitat associations as identified by Harris (1984), Delasalla (1996), and others.  Individual Species Abundance  Because species-specific songs have effective detectability distances that vary considerably from species to species (Wolf et al 1995), I determined the effective detection distances (EDD's) for common species (>5% of the total detections) following methods developed by Reynolds et al (1980, Table 2). The EDD's for each species were derived by plotting the number of individuals detected in 10 metre concentric rings away from the observer. The distance where calculated densities declined by more than 50% (a rough estimate of the inflection point) between concentric rings was then considered the effective detection distance (the maximum distance at which individuals of a given species could be heard reliably). The E D D for each species was then used to calculate the area effectively sampled for each species at every census point. Relative abundance was calculated by averaging the number of detections within the EDD of singing males for both census periods.  Because the data under analyses consisted of counts, and followed a Poisson distribution, square root transformations in the form of X ' =  +  were performed on the  data to stabilize the variances around the means and thus better conform to the assumptions of normality where X is the observed relative abundance mean and X ' is the transformed mean (Sokal and Rohlf, 1995). A l l statistical tests were performed on the transformed data,  18  but tabulated values are presented in their original form as mean detections of singing males /census point (± SE).  Table 2. Effective detection distances for seven common species at Sicamous Creek.  Common Name  Effective Detection Distance (m)  Red-breasted Nuthatch  90  Winter Wren  90  Golden-crowned Kinglet  50  Hermit Thrush  70  Varied Thrush  100  Yellow-rumped Warbler  70  Dark-eyed Junco  80  Study Area Comparisons  I used a split-plot A N O V A procedure (SPSS 1992) to test for overall differences in community indices and relative abundance of common species among point count stations falling within harvested and unharvested forest patches, regardless of harvesting type applied. The data for the two conditions (harvested vs. unharvested) was pooled for the two years of pre (1993-94)- and post-harvest (1995-96) (A. Kozak pers. comm.). Because unharvested plots within the study site were relatively few (n=15), point count stations in uncut forest from the transect placed adjacent to the study area were included in the analyses to provide a larger sample size (n=22). I tested for significant year by treatment interaction  19  effects where a significant value would indicate either positive or negative responses by songbirds and changes in the songbird communities to the harvesting activities (Zar 1999).  Treatment Comparisons  Avian community indices and relative abundance for each common species (defined as one that made up at least 5% of the total songbird detections) were compared among treatments and between years using a repeated measures A N O V A (Zar 1999). I used a repeated measures analysis of variance because each census point and treatment was sampled repeatedly over the duration of the study (Kuehl 1994). Species richness was calculated by pooling the numbers of species detected for all three point count stations in a treatment unit. Likewise, relative abundance of a particular species was calculated by pooling the number of detections of singing males for all three point count stations in a treatment unit in a given year.  When significant year and year-by-treatment interactions were detected, treatment effects were evaluated using a separate two-way A N O V A for each year. Where no differences between the two years following harvest were detected, both samples (mean for the two years) were included in a single two-way A N O V A to test for treatment effects. In instances where A N O V A procedures identified significant treatment effects for community indices, abundance of mature forest associates, and individual bird abundance, Tukey's HSD was used as the a posteriori test to identify differences among treatments (Zar 1999).  20  When species showed significant year effects before and after harvest at the level of the entire study area, I consulted regional trends (estimating equations method) obtained by the Breeding Bird Survey to help determine if the trends observed were consistent with regional trends (Sauer et al 2001).  RESULTS  Community Structure of Songbirds Inhabiting the Sicamous Creek Research Forest  The songbird community at the study area was relatively simple. Based on the sampling conducted at the study area level, a total of 21 songbird species were detected at the study site prior to harvest. Eight species comprised 90% of the observations (n= 1,559). Varied thrush was the most abundant species followed by golden-crowned kinglet, winter wren, hermit thrush, pine siskin, dark-eyed junco, red-breasted nuthatch and yellow-rumped warbler. Twelve additional species accounted for the remaining 10% of the breeding songbird community detections. Following harvest the species richness across the entire area increased to 26 species. However, the core species remained the same, albeit at slightly different ranks, and comprised 84% of the total observations (n=l,590; Table 3). Winter wren became the most abundant species, followed by varied thrush, dark-eyed junco, hermit thrush, pine siskin, golden-crowned kinglet, yellow-rumped warbler, and red-breasted nuthatch. Seven songbird species were recorded for the first time during the 2 years postharvest. Some however consisted of single detections and likely transients through the study area (Table 3).  21  Table 3. Proportional abundance of all songbird species detected at point count stations (n=77) before and after harvest in the Sicamous Creek study area. Species Varied Thrush Hermit Thrush Golden-crowned Kinglet Winter Wren Pine Siskin Dark-eyed Junco Red-breasted Nuthatch Yellow-rumped Warbler Gray Jay Pine Grosbeak Boreal Chickadee Mountain Chickadee Brown Creeper Wilson's Warbler American Robin Chipping Sparrow Fox Sparrow Olive-sided Flycatcher Swainson's Thrush Townsend's Warbler Vesper Sparrow Clark's Nutcracker Evening Grosbeak Lincoln's Sparrow Ruby-crowned Kinglet Red Crossbill Townsend's Solitaire White-crowned Sparrow Total species  Treatment Pre-Treatment 0.141 0.117 0.116 0.114 0.109 0.106 0.080 0.073 0.045 0.037 0.031 0.009 0.008 0.005 0.0006 0.0006 0.0006 0.0006 0.0006 0.0006 0.0006  Post-treatment 0.132 0.119 0.079 0.143 0.091 0.128 0. 068 0. 078 0.024 0.034 0.026  —  ~  0.0006 0.001 0.002 0.006 0.001 0.002 0.001  21  26  ~  — ~  — —  —  0.004 0.014 0.014 0.010 0.007 0.0006 0.001 0.004 ~  22  Across the entire study area, the total number of species detected (species richness) was not significantly different between points in the uncut and harvested points before and after harvest (treatment by year interaction: F=0.36; df=l,75; p=0.55, Table 4). During the two years post harvest, at individual treatment level, there was a significant year effect (F=15.43; df=l,10; p=0.003) but no treatment or interaction effects (treatment F=2.19; df=4,10; p=0.143; treatment by year interaction: F=1.83; df=4,10; p=0.20).  When years were analyzed separately, year one post-harvest also showed nonsignificant results for treatments (F=1.16, df=4,14; p=0.38). However, in year two, there was a significant treatment effect (F=3.61; df=4,14; p=0.04;Table 5), although differences among the treatments could not be discerned by multiple comparison tests. Qualitatively, it appeared that species richness was higher in the 1.0 ha treatments followed by lOha, 0.1 ha, selection, and uncut treatments.  The number of songbirds detected (species abundance) per census point across the study area at uncut and harvested plots prior to and after harvest was marginally significant (year by treatment interaction F=3.85; df=l,75; p=0.053) with numbers of individuals detected decreasing in uncut reserves and increasing in the harvested plots (Table 4). However, when the individual treatments were examined separately, total relative abundance was not significantly different between years (F=0.74; df=l,10; p=0.41) or among the different treatments (F=1.92; df=4,10; p=0.18).  23  Shannon diversity and evenness indices were not significantly different in the uncut and harvested treatments prior to- or after treatment application (Shannon treatment by year interaction: F=0.75; df= 1,75; p=0.39; Evenness treatment by year interaction: F=0.91; df=l,75; p=0.34). Results were also similar for comparisons among the individual treatments: Shannon diversity, and evenness community indices were not significantly different among uncut and any other treatment (F=0.36; df=4,10; p=0.83 and F=0.50; df=4,10; p=0.73).  Table 4. Community parameters for uncut and treatment sites before and after harvest. Uncut reserves n=22  Treatments n=55  Pre-treatment  Post-treatment  Pre-treatment  Post-treatment  Shannon diversity  0.91  0.90  0.91  0.93  Evenness J= H/Hmax  0.95  0.93  0.94  0.94  Community parameter  Similarity  0.63 (0.02)  0.64 (0.01)  Species richness  9.22 (0.29)  9.40 (0.36)  9.49 (0.23)  9.98 (0.26)  Total relative abundance  9.88 (0.39)  9.31 (0.46)  10.07 (0.23)  10.70 (0.32)  Community similarity indices between uncut and harvested plots did not differ (F=0.04; df=l,75; p=0.84). At the individual treatment level, similarity indices ranged between 41% and 69% although there were no significant differences among the treatments (Year 1: F=3.83; df=3,6; p=0.07; and Year 2: F=1.22; df=3,6; p=0.37). Qualitatively, in year 1 the 0.1 ha treatment was most similar to uncut reserves followed by 1.0, selection and 10 ha. In the second year, selection cut was most similar to uncut reserves followed by 1.0, 0.1, and 10 ha treatments. 24  ll  ON  ON  CN ON  ©  o  ©  00 00 d  in d o o <fr  in 1-1  ON  ON  d  d  a  S ©  CU  o  |3  OO 00 d  ©  OO  O  ON  ON  d  d  d  ON  NO ON  d  O ON d  ON  ON  d  d  CN Os d  cn  ON  d  "fr co CO in  NO NO d CO CO in  CO  o o CO in "fr  .33 (1.  T -H ©m ©  NO  ra <u  >*  CN S-. ccj CU  CN  ra  I-j 3 cu  >*  ><  cu  Yea  -St  o CN NO NO CO  oo  00 <d CO CO -fr  CO CO ©, NO  NO r~; CN NO NO NO m 00  ON  t o— *H ' o NO NO  o o in ON  NO  NO d— ' NO NO d ocT OO ©, CO CO  CN S (U  00 NO ^ CO CO CO NO  00 CO oo  ON  CN CN O o d CO  "frN  s~ ON © 00 CO NO o NO CO ON CO •<fr  NO ©  o in NO "fr  ON  t-H NO CO o o ON CO  m  NO O m d in  CO in CN CO  < <  in oo CO o NO CO CO  S  CU  CN a <D ><  u 3 <u  O  T3  C  c/>  CO CU  I•c <u  •*H  CU >  S  CO  o  CU  CH  00  CU  O  PH  ON  NO NO d "fr  o Os CS NO NO in CO /—v  NO  o © CN rCO CO CO ON  CN CN 3  > > CU  co co cu  CO NO Tr' NO NO CO CO  CU >  •1-1  1 "ra  •*H  O  H  CU  in CN  Subsets of species in the community (species associated with mature forest and others) were examined separately for treatment effects. Based on Harris (1984) and Delasalla (1996) and others the following species were considered mature forest species: Varied Thrush, Townsend's Warbler, Red Crossbill, Pine Siskin, Red-breasted Nuthatch, Brown Creeper, Winter Wren, and Golden-crowned Kinglet. Other species were: Gray Jay, Olivesided Flycatcher, Swainson's Thrush, Hermit Thrush, American Robin, Wilson's Warbler, Lincoln's Sparrow, Mountain Chickadee, Vesper Sparrow, White-crowned Sparrow, Yellowrumped Warbler and Dark-eyed Junco. Mean mature forest species detections per census point were not significantly different between treatments and uncut plots prior to and after harvest (treatment by year interaction: F=0.10; df= 1,75; p=0.74; Table 6). For other species there were significant year (F=4.10; df=l,75; p=0.03), treatment (F=4.10; df=l,75; p=0.04) and treatment by year interaction effects (F=6.20, df=l,75; p=0.01). Other species became more abundant in harvested areas after harvest.  Table 6. Mean abundance (SE) of mature forest associates and other species detected per point count stations in uncut and harvested treatments prior to- and after harvest. Uncut reserves n=22 Treatments n=55 Pre-treatment  Post-treatment  Pre-treatment  Post-treatment  Mature Forest associates  12.86 (0.67)  11.77 (0.59)  12.98 (0.36)  12.25 (0.44)  Others  7.04(0.34)  8.77(0.68)  7.4(0.39)  12.54(0.45)  26  At the individual treatment level, abundance of both mature forest and other species were not significantly different between harvested and uncut treatments one year post-harvest (mature forest spp. F=2.05; df= 4,8; p=0.17, and others F=1.09; df= 4,8; p=0.42) (Table 8). In the second year after harvest abundance of mature forest associates was also not significantly different between treatments. However, it is worth noting that both selection and the 10 ha treatment supported fewer mature forest associates than any other treatment for both years. Conversely, other species did show significant responses among treatments in the second year after harvest. Abundance was lowest in uncut (mean= 9.80), followed by selection and 0.1 ha treatments (means=15.70, and 16.10), and then 1.0 ha and 10 ha. treatments (means= 24.22, and 28.07). However, significant differences were only detected between the uncut and the ten ha treatments (Tukey's HSD).  Changes in Abundance of Individual Species  Only eight species occurred at sufficiently high densities to conduct analysis on changes in relative abundance (Table 8.): Dark-eyed Junco, Golden-crowned Kinglet, Hermit Thrush, Pine Siskin, Red-breasted Nuthatch, Varied Thrush, Winter Wren and Yellowrumped Warbler. However, I did not conduct analyses on Pine Siskin because, although common, this species was most commonly detected flying over the study area during the bird census.  27  ,o o l) «  o  CN o o  o\  ro"  CN  vo CN  fe  fe  fe  CN  oo  Os  o  II  a c tp g  II  p.  PH  o" o  Os*  II  bo £  O O  II  d> II  II  OH  ITS  II  fe  PQ  CN  O 00 CN  00 CN  VO VO CN  VO  vo vq  od CN  oo  <3  »*5  T-H  o o  O o  od  VO  o  00 CN  ro ro CN ro VO  Os  ro ro CN  13  oo  ITS  —<  CN  ro  O 00  oo  oo  •rt  in CN ro ro Os  Os  a  00 CN * — '  ro ro vd  H§  i l  o p  cu I-  H  'a  ro  5  oo  CN rO  00  O o CN  ro ro  o, WD  |3  vd  vo  ro ro vd  'I -*-»  13 GO  co O VO  S  IS  ci  CN  O 00 CN  VO  ro co VO  VO ro  O CN  O  § CN rro 00 0\  U  H—» H—»  GO  00  p  " oo O Co  VO Os Os  r--  Os Os  ta  -$£  ^  vo Os  0\  rOv  Two of seven species showed significant responses to harvesting and among the individual treatments (Tables 8 and 9). Prior to harvest, relative abundance of goldencrowned kinglet appeared to be higher at treatment than in control sites although the differences were not statistically significant (F=2.42; df=l,75; p=0.12). However, after harvest, detections of golden-crowned kinglet declined significantly by more than two times at harvested plots (treatment by year interaction F=10.30; df= 1, 74; p=0.002). At the level of individual treatments, golden-crowned kinglet detections were significantly different between treatments (F=6.54; df=4,10; p=0.007). Golden crowned kinglet were significantly more abundant in uncut plots compared to the lOha and selection harvest treatments (Tukey's HSD ct=0.05) (Table 9, Fig. 5).  Dark-eyed junco detections were not significantly different between treatment and uncut plots prior to harvest (Table 8). After harvest the number of detections in harvested plots increased significantly (treatment by year interaction: F=7.23; df=l,74; p=0.009), suggesting a positive response as a result of harvest. When detections were compared among individual treatments, there were significant year (F=24.84; df=l,10; p=0.001) and treatment (F=6.70; df=4,10; p=0.007) effects. Dark-eyed junco detections were significantly lower in uncut reserves than in any treatment (Tukey's HSD a=0.05).  Although not significant, there were qualitative trends for some of the remaining species. Red-breasted nuthatch declined throughout the study area after harvest. At the individual treatment level, abundance was highest in the 1.0 ha opening treatments and lowest in the selection cut treatment. Hermit thrush increased in both uncut and harvested  29  areas after harvest but was least abundant in the uncut reserves. Conversely, varied thrush declined in abundance in both uncut and harvested plots after harvest. At the individual treatment level, varied thrush was most abundant in uncut treatments than in other treatments. Winter wren showed little change in abundance in all areas after the harvest, although they were most abundant in all treatments other than the uncut reserves. Finally, yellow-rumped warbler showed a response to harvesting similar than that of dark-eyed junco. After harvest, yellow-rumped warbler abundance declined in the uncut reserves and increased in the harvested areas. Among the individual treatments, yellow-rumped warbler was most abundant in the 10 ha treatment and least abundant in the selection cut treatment.  30  «  CU  u a  w SS  •a  53  ON  o o  d II  PH  rn o II  ll  Pi  a  d II II  OH  cn fN c^ II  M  PH  "t rn oo d II II  PH  r-  o oo d II II  PH  "t  VO O  d itII  d ll II fe  O  PH  +  c +  VO  o  00  d  CU  H  'I  as o o  CO 00  O  r-H  00  rr-H  o It II  m  d itII  o llII  r-H  PH  • vo ||  II  PH  PH VO  r-H  d || II fe  PH  00  VO  ON II II  +  ON  o  d  p d  d  O d  m vo  in  o  VO  Ov  ON VO  d  r-H  "t oo d  d  r—I  d  d  oo  vo  vo  VO  p d  o d  O  ON  o d  c-  o d  CU  S -«-»  ecu a  vo  O d  CN  oo  o d  vo 1-1  <N  '1!  o d  o d  vo  00  T-H  o d  IT)  00  r-H  d  d  m  o  ON  CN d  O d  d  d  d  d  o,  o d  00 00  oo oo  CN O  OO  vo  ON  d  d  T-H  d  d  o  o  ON O  CN i-H  ON O  d  d  d  d  OO p  CN  d T-H  o p  r-  m "fr  O  r-H  d  Os p  VO  in  u a  H  O  w  —  d  p  d ON  d  d  O  H3  1  T3 U  •+H  *3 cu a  "8  1/1 C3 U  T3  Pi  CN ro  PQ PQ VD  o  in  VO  ©  ro ro  vd  oo  in  00  VO  vo  ©  ©  ©  m  m r^  oo CN ro C N © © in  ON CN CN CN* CN CN CO  •sr  CD  Q oo  >,  CD  H PQ  PQ  ro  ro  CN ©  ©  00  00  ©  CN  in in  •st-  p  ©  VO  © in  CN  •sT  C N •sr  in i>  CN  •sr •si© in r•sr  © ro  > O  O ON  C/l CD  S3 00  ca CD  s  PQ  PQ  CN  00  ©  ©  ©  ©  VO VO  VO  oo  vd  CN  CD  in  o  o  Os  in ©  ro ro •sr  © m  ©  CN  vo"  •<t  ©  ©  © in in  in  •8 CD  OH  CN CD  PQ  |3  ro ro ©  CN  'I)  PQ •*r  vo  ©  ©  ©  VO  © in ro  ON  vo in  ON  CN  vq  © ro ©  CN •sr C N oq © ©  ro ro  vo  ro  oq ©  O  fl  -a s  < ©  C N © ON  S  © ro ©  m ro  ON VO  m  ©  vo  "sT  ©  ©  ©  ©  O  in  VO  in  © in  VO  OO  t-CN CN CN CN i n CN CO  in  •s CS CD  bO fl o  *e3  oo  ti CD  CD  43  1 •fl  CD fl  P  .2  CD  2 "3  O  o  o o 43  •fl u  oo  Q  43 cn -*-»  CD  X  "S  >  4 -— >  CD  OH  s  I  "8 a  CD  i  31  T3  13 I*  CD fl  fl -a CD GO  (fl  CD U. 43  i  GO  60 fl  "S 43  oo ^ fl ^ /  S  o  ,2 o  ro ro  cn a> = E  s)U|od snsueo £ jed saiew 6u|6u!s jo suoipaiap ueay\|  siuiod snsuao g jad saieui 6u]6u|s jo suoipajap ueajM  CQ  £ .3 CQ  0) tz>  }inod snsuao jad sa|Biu 6u|6uis jo suojpaiap uea^  )U|od snsuao jad saieui 6ui6uis jo suojpajap uean  .1  PH 43  DISCUSSION  The original songbird community inhabiting the Sicamous Creek Study area consisted of a relatively small number of dominant species and several rare ones. This pattern, and the community that inhabits these forests appears to be very similar to other conifer-dominated high elevation forests when compared to lower elevation forests (Sabo 1980). In British Columbia, Dickinson et al (unpubl. report), and Dickinson and Leupin (unpubl. report) reported similar community compositions in two studies within subalpine forests near Barriere, B.C. and Avola, B.C. respectively. Similarly, Davies et al (1999) identified similar songbird species composition within the ESSF biogeoclimatic zone in southern Cariboo region of British Columbia. Elsewhere in the Pacific Northwest, Wiens (1989) estimated that the average number of species inhabiting high elevation Rocky Mountain forests was 14. Similarly, Raphael (1987) in a review of studies conducted in high elevation forests in Colorado identified 14 species as being commonly reported in subalpine forests in the Central Rocky Mountains. In his paper, all species listed, with the exception of 1 species (Cassin's Finch) were also the species found at the Sicamous Creek Study site.  The responses of the songbird community to the various levels of perforation were subtle suggesting that the original songbird community inhabiting the Sicamous Creek research forest may have some resilience to the harvesting activities as has been observed in other experimental studies in the boreal forests of Alberta (Schmiegelow et al 1997). Dominant species that were originally present maintained dominance, although their representation changed in terms of rank. At Sicamous Creek, new species appeared in 34  relatively low numbers despite the presence of extensive clearcuts so that they did not play, at least in the two years following harvest, a large role in shaping the original songbird community. In similar studies in hardwood forests, Robinson and Robinson (1999), and Annand and Thompson (1997) attributed the lack of colonization by early serai stageassociated species in gapped forests to the small size (and consequently, unsuitability) of the new habitats created.  There are three plausible reasons for the observed results. In subalpine forests, largescale disturbances (typically created by fires) normally are of a stand-replacing nature and result in dramatic changes to the songbird community, but these occur at infrequent («400 year) intervals (Veblen 1986). In high-elevation and subalpine forests, the factors mostly responsible for the structural make-up of these forests are guided by small-scale disturbances such as insect outbreaks and windfall (Parish et al 1999). It is thus possible that the original songbird community may be able to accommodate such disturbances without appreciable changes in the songbird community. Similar results have been obtained in other areas in the Pacific Northwest and boreal forests in Alberta (Chambers et al 1999, Steventon et al 1998, Schieck et al 1995, Schmiegelow et al 1997). These authors hypothesized that the lack of response by mature forest-associated songbirds in their areas was the result of the harvesting methods used which resembled the usual natural disturbance events of the area.  A second possible reason for the low level of response may be that the removal of 30% of the habitat was not sufficient to affect the original songbird community negatively  35  because the original forest may have been supporting populations below carrying capacity. Martin (2001) noted that high elevation habitats tend to support lower densities of organisms (including birds) than lower elevation habitats (see also Sabo and Holmes 1983). Therefore, i f songbirds occurred at densities lower than the carrying capacity, the "displaced" individuals could occupy vacant territories within the remaining forest. Several studies have reported crowding effects in uncut forests after the surrounding forest had been harvested. In boreal forests of Alberta, Schmiegelow et al (1997) reported that bird abundance increased significantly in isolated fragments relative to controls one year after harvest suggesting such an accommodation or "crowding effect" may have occurred. However, species associated with mature forest at Sicamous Creek did not appear to show this "crowding effect". The lack of "crowding" may imply a shortage of one or more critical resources in high elevation forests that maintain densities at lower levels than those observed at lower elevations.  Finally, the influx of species into the study area after harvest was negligible. The ten ha opening treatments supported a higher abundance of non-old growth species when compared to the uncut treatments. However there was a non-significant tendency for higher numbers of non-old growth species in larger canopy openings in the second year postharvest. This could be accounted for by increases in species with broad habitat plasticity (i.e. species that can be found in a variety of habitat types) that were already present in the original forest. New species were detected at very low levels after harvest so that they did not play an important role in the reshaping the songbird community after harvest. In other studies, influx of new species has been documented following clearcut harvesting practices  36  and in forest remnants embedded in non-forest habitat (Thompson and Capen 1988, Rice et al 1984, Germaine et al 1997).  Increased abundance of predators and brood parasites has been implicated in impacting forest-dwelling songbirds negatively after harvesting (Robinson and Robinson 1999, Andren and Angelstram 1988). Gray Jay, the only predatory species in the area occurred at low densities and utilized areas that overlapped treatment units and showed no apparent response to the harvesting activities, suggesting that impacts of predation rates on the original songbird community by this species were probably similar to those that would occur at pre-harvest levels. Brown-headed cowbirds are common in lower elevations where agricultural lands make up a significant portion of the landscape. However, they were never detected within the study area or in extensive clearcuts adjacent to the site (T. Dickinson, unpubl. data).  Open country species, which were present in adjacent clearcuts did not colonize the newly created habitats (openings). After harvest, there was a dramatic decline in the original shrub and herb cover as a result of the harvest (Lloyd et al 1997). Secondary succession also did not occur within the first two years after harvest so that the openings may have been unsuitable for colonizing species. Robinson and Robinson (1999), and Annand and Thompson (1997) conducted similar studies addressing openings and their effects on forest interior birds. Both studies obtained similar results and attributed the lack of colonization of  37  early serai stage-associated species in forest gaps to the small size (and consequently, unsuitability) of the new habitat created.  Despite a lack of significant response by the community as a whole, the abundance of several species did respond negatively to the harvesting activities. The responses of these species can thus have serious implications in forest management practices where the objective is to retain the original species at similar abundances typical of the original forest. I predicted decreases in abundance of species commonly associated with mature- and oldgrowth forest interior. Four of the seven species common at the study site decreased in abundance. Golden-crowned kinglet, a species associated with high canopy closures (Galati 1991, Mannan and Meslow 1984), decreased in abundance at treatment areas after harvest. This result is consistent with studies elsewhere and in other forest types where consistent negative responses by this species to harvesting activities have been observed (i.e. Wetmore et al 1983; Delasalla et al 1996, Hutto et al 1993). More importantly and of potential management concern, abundance of this species decreased by a degree greater than the amount of wood removal suggesting that the remaining forest in harvested sites are unable to support densities typical of the undisturbed forest.  Other species like the dark-eyed junco responded positively to the harvesting activities. This species can be found in habitat types that range, from old-growth forests to open habitats (Titterington et al 1979). Similar results were obtained by Wetmore et al (1985), where this species was more abundant in disturbed sites than in control areas  38  following harvest. In addition, the results also suggest that Dark-eyed junco were attracted by and crowded into the newly created habitats.  Finally, other species showed significant results at the study site level between years but not between treatments. Red-breasted nuthatch a secondary cavity nester, showed a significant decline while hermit thrush showed a increase after harvest. I consulted regional Breeding Bird Surveys for the two species that exhibited the year effects to determine i f the results observed were likely the result of regional temporal declines or whether the observed responses were the result of harvesting pressures. The results of the BBS suggested that redbreasted nuthatch detections in the period of 1993-1997 declined (BC Trend -6.80, p=0.01, n=50; Sauer et al 2001), suggesting that the observed declines may have been associated with regional changes rather that the harvesting activities at the study area. However, because this species is a year-round resident in British Columbia, the regional trends may in fact be a reflection of harvesting throughout the province. At Sicamous Creek, this species forages in family units over large tracts of forests and may have expanded territory sizes to accommodate the loss of foraging/nesting habitat available to them and thus excluded other families from the surrounding area. Given the fact that standing dead trees (nesting sites) were removed to comply with W C B regulations strengthens this assumption.  Hermit thrush showed a significant increase in both treatment and control areas. When compared to regional BBS trends, the species shows declining trends throughout British Columbia over the period of 1993-1997 (Trend estimate -6.57; p=0.005, n=31, Sauer  39  et al 2001), which suggests that increases observed at the study area were likely the result of changes in habitats at a local level that favored this species.  CONCLUSIONS  Overall, the removal of 30% of wood volume removal by various means of forest perforation had little short-term effects on the original songbird community at Sicamous Creek. Although we observed some significant negative and positive effects for some species and groups of species, the magnitude of these effects were comparatively small. In general, it appears that songbirds inhabiting high-elevation appeared to accommodate the openings created by alternative silvicultural treatments perhaps because these mimicked natural disturbances typically experienced in this ecosystem. However, when interpreting the generality of these results it is important to consider several points.  First, this study investigated only the short-term (1-2 yrs) effects of the first cutting cycle in this forest. The trends that lacked statistical significance in this study could accumulate for some of the species and become significant over time. In the intervening five if eight years post-treatment (1998-2002), observations on the same sites, 4 new species associated with open habitats have been observed at treatment sites (T. Dickinson, pers. comm.). Second, we used the number of detections of singing birds as the treatment response variable as opposed to more direct measures of bird productivity, such as pairing and nesting success. Abundance or density estimates can be misleading indicators of habitat quality  40  because the harvested forests may have been sub-optimal habitats supporting non-breeding males (Van Home 1983). In such instances, presence of singing males could have been maintained through a "rescue" effect from adjacent undisturbed forests (Brawn and Robinson 1996). Easton and Martin (1998) investigated the effects of removal of deciduous vegetation in managed Interior Cedar-Hemlock forests near the Sicamous Creek study area and reported higher abundance of common species but lower nesting success. Third, the experimental treatments measured only one degree (30%) of tree volume removal. Conventional forestry practices in turn remove 80-90% of the tree volume (Easton and Martin 1998, Schmiegelow et al 1997). A n increased amount of habitat removal may in fact incrementally reduce the value of the remaining forests and make them less suitable for forest interior species. Steventon et al (1998) concluded that although removal of 30% and 60% of the wood volume in forests near Hazelton, B C , using a combination of selection harvest and 0.1-0.5 ha openings provided some habitat for mature forest songbird species, the heavy removal began to show a shift to species typical of clearcuts. As a result, subsequent entries into high elevation forests harvested using alternative silvicultural methods to clearcutting may be highly detrimental to songbirds associated with mature forest and should be reconsidered.  Finally, the effects of forest perforation on the songbird community must be interpreted within the context of the surrounding landscape. Instances of increased brood parasitism and predation have been linked to the amount of regional forest cover (Robinson et al 1995). The Sicamous Creek Research Forest was located in a predominantly forested landscape, however, as the forest area is reduced, the creation of gaps can increase the risks  41  to forest interior birds to parasitism and predation. Nevertheless, i f the management objectives of mature forest species are to be met, the first cutting cycle of alternative silvicultural treatments at low removal levels can provide for both timber extraction and the retention of structural characteristics important to songbirds inhabiting these forests.  42  LITERATURE CITED  Andren, H., and P. Angelstram. 1988. Elevated predation rates as an edge effect in habitat islands. Ecology 69: 544-547 Annand, E. M . , and F. R. Thompson III. 1997. Forest bird response to regeneration practices in central hardwood forests. Journal of Wildlife Management 61: 159-171. Askins, R., D. M.J. Philbrick, and D. S. Sugeno. 1987. Relationship between the regional abundance of forest and the composition of forest bird communities. Biological Conservation 39:129-152. Boulinier, T., J. D. Nichols, J. E. Hines, J. R. Sauer, C. H. Flather, and K . H . Pollock. 2001. Forest fragmentation and bird community dynamics. Ecology 82:1159-1169. Brawn, J. D., and S. K . Robinson. 1996. Source sink Populations dynamics may complicate interpretation of long-term data census. Ecology 77:3-12. Brittingham, M . C , and S. A . Temple. 1983. How cowbirds have caused forest songbirds to decline. Bioscience 33:31-35. Buford, E. W., and D. E. Capen. 1999. Abundance and productivity of forest songbirds in a managed, unfragmented landscape in Vermont. Journal of Wildlife Management 63:180-188. Chambers, C. L., W.C. McComb, and J.C. Tappeiner II. 1999. Breeding bird responses to three silvicultural treatments in the Oregon Coast Range. Ecological Applications 91:171-185. Davies, L . R., M . J. Waterhouse, and H . M . Armleder. 1999. A comparison of breeding bird communities in serai stages of the Engelmann spruce—sub-alpine fir zone in eastcentral British Columbia. Working Paper 39/99 Research Branch, B.C. Ministry of Forests: Victoria, B.C. Debinski, D. M . , and R. D. Holt. 2000. A survey overview of habitat fragmentation experiments. Conservation Biology 14:342-355. Delasalla, D. A., J. C. Hagar, K. A . Engel, W. C. McComb, R. L. Fairbanks, and E. G . Campbell. 1996. Effects of silvicultural modifications of temperate rainforest on breeding and wintering bird communities, Prince of Wales Island, Southeast Alaska. Condor 98:706-721.  43  Drolet, B., A . Desrochers, and M . J. Fortin. 1999. Effects of landscape structure on nesting songbird distribution in a harvested boreal forest. Condor 101:699-704. Enoksson, B., P. Anglestram, and K. Larsson. 1995. Deciduous forest and resident birds: the problem of fragmentation within a coniferous landscape. Landscape Ecology 10: 267-275. Faaborg, J., M . Brittingham, T. Donovan, and J. Blake. 1995. Habitat fragmentation in the temperate zone. Pages 357-380 in T. E. Martin, and D. M . Finch, (eds). Ecology and management of Neotropical migratory birds. Oxford University Press, New York, New York, USA. Fahrig, L . 1997. Relative effects of habitat loss and fragmentation on population extinction. Journal of Wildlife Management 61:603-610. Feller, M . 1997. Ecological Niches of seedling establishment in high elevation forests. In: Hollstedt, C, and A . Vyse. (eds). Sicamous Creek Silvicultural Systems Project. April 24-26,1997 Workshop Proceedings. Ministry of Forest, Victoria, B C . Working Pap. 24/1997. Finch, D. M . , and P. W. Stangel, 1994. Status of Management of Neotropical Migratory Birds. Gen. Tech. Report. RM-229. Fort Collins CO: U.S. Dept. of Agriculture. Forest Service. Rocky Mtn. For. Exp. Stat. 422 pp. Galati, R. 1991. Golden-crowned kinglets: treetop nesters of the north woods. Iowa State Univ. Press. 142 pp. Germaine, S.S., S.H. Vessey, and D.E. Capen. 1997. Effects of small forest openings on the breeding bird community in a Vermont hardwood forest. Condor 99:708-718. Hagan, J. M . , W. M . van der Haegen, and P. S. McKinley. 1996. The early development of forest fragmentation on birds. Conservation Biology 10:188-202. Hollstedt, C, and A . Vyse. 1997. Sicamous Creek Silvicultural Systems Project. April 2426,1997 Workshop Proceedings. Ministry of Forest, Victoria, B C . Working Paper 24/1997. Harris, L. D. 1984. The fragmented forest. Island biogeography theory and the preservation of biotic diversity. University of Chicago Press. Chicago. Hartley, M . J., and M . L. Hunter. 1998. A meta-analysis of forest cover, edge effects, and artificial nest predation rates. Conservation Biology 12:465-469. Hunter, M . S. 1990. Wildlife, Forests and Forestry. Prentice Hall: Englewood Cliffs, N.J. 44  Hunter, M . S. 1996. Fundamentals of Conservation Biology. Blackwell Science, Cambridge, Massachussets. Hutto, R. L., S. J. Hejl, C. R. Preston, and D. Finch. 1993. Effects of silvicultural treatments on forest birds in the Rocky Mountains: implications and management recommendations. In: Finch, D. M . , and P. W. Stangel, Eds.. 1993. Status and management of Neotropical migratory birds. Gen. Tech. Rep. RM-229, U S D A Forest Service, Rocky Mtn. For. Exp. Stat. 422 pp. Krebs, C, J. 1999. Ecological Methodology. 2 Publishers. Menlo Park, Ca. 580pp.  nd  Ed. Addison-Welsey Educational  Kuehl, R. O. 1994. Statistical principles of research design and analysis. Duxbury Press. Belmont. Ca. Lloyd, D. A . , K . Angove, G. Hope, and C. Thompson. 1990. A guide for site identification and interpretation of the Kamloops Forest Region V o l 2. B C Ministry of Forests, Land Management Handbook No. 23 Victoria, B C . Lloyd, D., K . Yearsley, and A . Arsenault. 1997. Spatial and temporal response of vegetation to silvicultural treatments in ESSF forests at Sicamous Creek. In: Hollstedt, C, and A . Vyse. (eds). Sicamous Creek Silvicultural Systems Project. April 24-26, 1997 Workshop Proceedings. Ministry of Forest, Victoria, B C . Working Paper 24/1997. Lloyd, D., and A . , Inselberg. 1997. Ecosystem Mapping for the Sicamous Creek Silvicultural Systems Research Site. In: Hollstedt, C, and A . Vyse. (eds). Sicamous Creek Silvicultural Systems Project. April 24-26, 1997 Workshop Proceedings. Ministry of Forest, Victoria, B C . Working Paper 24/1997 Mac Arthur, R. H . , and E. O. Wilson. 1967. The theory of island biogeography. Princeton University Press, Princeton New Jersey. Martin, K . 2001. Wildlife in Alpine and Sub-alpine Habitats. In: D. H . Johnson, and T. A . O'Neil (Managing Directors). Wildlife Habitat Relationships in Oregon and Washington. Oregon State University Press. Pages 285-310. Martin, K . , and J. M . Eadie. 1999. Nest Webs: a community wide approach to the management and conservation of cavity nesting birds. Forest Ecology and Management 115: 243-257. McGarigal, K., and W. C. McComb. 1995. Relationships between landscape structure and breeding birds in the Oregon Coast Range. Ecological Monographs 65:235-260. 45  Mannan, R.H., and E. C. Meslow. 1984. Bird populations and vegetation characteristics in managed and old-growth forests , Northeastern Oregon. Journal of Wildlife Management 48:1219-1238. Moorman, C. E. and D. C. Guynn Jr. 2001. Effects of group selection opening size on breeding bird habitat use in a bottomland forest. Ecological Applications 11:16801691. Norton, M.R., and S. J. Hannon. 1997. Songbird responses to partial cutting in the boreal mixedwood forest of Alberta. Canadian Journal of Forestry Research 27:44-53. Parish, R., J. A . Antos, and M . J. Fortin. 1999. Stand development in an old-growth subalpine forest in southern interior, British Columbia. Canadian Journal of Forestry Research 29:1347-1356. Puttonen, P., J. Kaipanen, and A . Vyse. 1997. Advanced Regeneration in Engelmann Spruce- Subalpine Fir Forests. ppl74-186 In: Hollstedt, C, and A . Vyse. (eds). Sicamous Creek Silvicultural Systems Project. April 24-26, 1997 Workshop Proceedings. Ministry of Forest, Victoria, B C . Working Paper 24/1997 Ralph, C. J., G. R. Geupel, P. Pyle, T. E. Martin, and D. F. DeSante. 1993. Handbook of field methods for monitoring landbirds. Gen. Tech. Report. PSW-GTR-144. Pacific Southwest Research Station, U.S. Forest Service. U.S. Dept. of Agriculture. Raphael, M . G. 1987. Nongame wildlife research in subalpine forests of the central Rocky Mountains, ppl 13-122 in: Management of subalpine forests: building on 50 years of research. U S D A Forest Serv. Gen Tech. Rep. RM-149. Renkonen. O. 1938. Statish-okologische Untersuchungen iiber die terrestiche kaferweltder Finnischen Bruchmoore Ann. Zool. Soc. Bot. Fenn. Vanamo. 6:1-231. Reynolds, R. T., J. M . Scott, and R. A . Nussbaum. 1980. A variable circular plot method for estimating bird numbers. Condor 82:309-313. Rice, J., B. W. Anderson, and R. D. Ohmart 1984. Comparison of the Importance of Different Habitat Attributes to Avian Community Organization. Journal of Wildlife Management 48:895-911. Robbins, C. S. 1981. Bird activity levels related to weather. Studies in Avian Biology 6:301-310. Robbins, C.S., J.R. Sauer, R. S. Greenberg, and S. Droege. 1989. Population declines in North American birds that migrate to the neotropics. Proceedings of the National Academy of Sciences (USA) 86:7658-7662. 46  Robinson, D.W., and S. K . Robinson 1999. Effects of selective logging of forest bird populations in a fragmented landscape. Conservation Biology 13:58-66. Robinson, S. K . 1992. Population dynamics of breeding Neotropical migrants in a fragmented Illinois landscape. In: Ecology and conservation of Neotropical  migrant  landbirds., J. M . Hagan and D. W. Johnston (eds), Washington; Smithsonian Institute Press. Pp 408-418. Robinson, S. K., F. R. Thompson III, T. M . Donovan, D. R. Whitehead, and J. Faaborg. 1995. Regional forest fragmentation and the nesting success of migratory birds Science 267:1987-1990. Rudickny, T. C , and M . L. Hunter. 1993. Avian nest predation in clearcuts, forests, and edges in a forest-dominated landscape. Journal of Wildlife Management. 57:358-364. Sabo, S. R. 1980. Niche and habitat relations in subalpine bird communities of the White Mountains of New Hampshire. Ecological Monographs 50:241-259. Sabo, S. R., and R. T. Holmes. 1983. Foraging niches and the structure of forest bird communities in contrasting montane habitats. Condor 85:121-137. Sallabanks, R., E. B . Arnett, and J. M . Marzluff. 2000. A n evaluation of research on the effects of timber harvest on bird populations. Wildlife Society Bulletin 28:11441155. Sauer, J. R., J. E. Hines, I. Thomas, J. Fallon, and G. Gough. 2001. The North American Breeding Bird Survey, Results and Analysis 1966 - 2000. Version 2001.1, USGS Patuxent Wildlife Research Center, Laurel, M D . Schieck, J., K . Lertzman, B. Nyeberg, and R. Page. 1995. Effects of patch size on birds in old-growth montane forests. Conservation Biology 9:1072-1084. Schmiegelow, F. K . A., and M . Monkkonen. 2002. Habitat loss and fragmentation in dynamic landscapes: avian perspectives from the boreal forest. Ecological Applications 12:375-389 Schmiegelow, F. K . A . , C S . Machtans, and S. J. Hannon 1997. Are boreal forest birds resilient to forest fragmentation? A n experimental study of short-term community responses. Ecology 78:1914-1932.  47  Scott, V . E., G. L . Crouch, and J. A . Whelan. 1982. Responses of birds and small mammals to clearcutting in a subalpine forest in central Colorado. Research Note RM-422. Fort Collins, CO: U.S. Department of Agriculture, Forest Service, Rocky Mountain Forest and Range Experiment Stations. Spies, T. A . , J. F. Franklin, and M . Klopsch. 1990. Canopy gaps in Douglas-fir forests of the Cascade Mountains. Canadian Journal of Forestry Research 20:649-658. Steventon, J. D., K . L . MacKenzie, and T. E. Mahon. 1998. Response of small mammals and birds to partial cutting and clearcutting in northwest British Columbia. The Forest Chronicle 74:703-713. Sokal, R. R. and F. J. Rohlf. 1995. Biometry 3 Ed. W. H . Freeman and Company. New York, N Y . rd  Thomas, J. W. 1987. Do we know enough to manage subalpine wildlife habitats?-It all depends. In: Management of Subalpine Forests: Building on 50 years of research. U S D A Forest Service Geological Survey. Technical Report. R M 149. Thompson, F.R. III., and D. E. Capen. 1988. Avian assemblages in serai stages of a Vermont forest. Journal of Wildlife Management 52:771-777. Thompson, F.R. III. 1993. Simulated response of a forest interior bird population to forest management options in central hardwood forests of the United States. Conservation Biology 7:325-333. Titterington, R. W., H . S. Crawford, and B. N . Burgason. 1979. Songbird responses to commercial clear-cutting in Maine spruce-fir forests. Journal of Wildlife Management 43:602-609. Van Home, B . 1983. Density as a misleading indicator of habitat quality. Journal of Wildlife Management 47:893-901. Veblen, T. T. 1986. Trefalls and the coexistence of conifers in subalpine forests of the Central Rockies. Ecology 67:679-690. Wetmore, S. P., R. A . Keller, and G. E. J. Smith. 1985. Effects of logging on bird populations in British Columbia as determined by a modified point-count method. Canadian Field-Naturalist 99:224-233. Wiens, J. A . 1989. The ecology of bird communities. Volume I. Cambridge University Press. New York, New York. 529 pp. Wolf, A . T., R. W . Howe, and G . J. Davis. 1995. Detectability of forest birds from stationary points in Northern Wisconsin, pp 45-48. In: Ralph, C . J . , J.R. Sauer, 48  and S. Droege (eds). Monitoring Bird Populations By Bird Counts. Gen. Tech. Rep. PSW-GTR-149. Albany, C A . : Pacific Southwest Research Station, Forest Service, U S . Department of Agriculture. Yanner, R. H., and D. P. Scott. 1988. Effects of forest fragmentation on depredation of artificial nests. Journal of Wildlife Management 52:158-161. Zar, J. H . 1999. Biostatistical Analysis. Second edition. Prentice Hall. Englewood Cliffs, NJ.  49  A P P E N D I X I. Sample data sheet f o r songbird sampling at Sicamous Creek  S I C A M O U S C R E E K S O N G B I R D S T U D Y 1996 Date:  Weather: Observer(s):  Transect #:  Start Time: Census Point:  Census Period:  Site Description:  Species  Time  Distance  s/c/v  # of Indiv.  M/F  Comments  Comments:  50  


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