Differential responses of seabirds to environmental variability over 2 years in the continental shelf and oceanic habitats of southeastern Bering Sea

Seasonal sea-ice cover has been decreasing in the southeastern Bering Sea shelf, which might affect ecosystem dynamics and availability of food resources to marine top predators breeding in the region. In this study, we investigated the foraging responses of two seabird species, surfaceforaging red-legged kittiwakes Rissa brevirostris (hereafter, RLKI) and pursuit-diving foraging thick-billed murres Uria lomvia (TBMU) to different marine environmental conditions over 2 years. At-sea distributions of RLKI and TBMU breeding on St. George Island, the largest seabird colony in the region, were recorded using GPS loggers, and blood samples were taken to examine their physiological condition and isotopic foraging niche in a given year. Between the study years, winter ice retreated earlier and summer water temperatures were relatively warmer in 2014 compared to those in 2013. RLKI foraging occurred mostly over the oceanic basin in both years. TBMU, however, foraged mostly over the shelf but showed a relatively higher use of the shelf break and oceanic basin in 2013. The foraging distances from the colony peaked at 250–300 km in 2013 and bimodally at 150– 250 and 300–350 km in 2014 for RLKI and tended to be farther in 2013 compared to those in 2014 for TBMU. Plasma levels of corticosterone did not differ between the years in RLKI but differed in TBMU, showing higher levels of physiological stress incurred by murres in 2013, the year of relatively cooler sea surface temperatures with later sea-ice retreat. δN (a proxy of trophic level of prey) did not differ between the years in either RLKI or TBMU. These results suggest that the response of ecosystem dynamics to climate variability in the southeastern Bering Sea may differ between the ocean basin and continental shelf regions, which, in turn, may generate differential responses in seabirds relying on those habitats for foraging.


Introduction
The Bering Sea is a productive marine ecosystem (Springer et al., 1996;Grebmeier, 2012) that supports immense populations of diverse marine fauna (Highsmith and Coyle, 1990;Piatt and Springer, 2003;Aydin and Mueter, 2007;Grebmeier, 2012).Sea-ice cover has been decreasing in duration and concentration over the southeastern Bering Sea shelf (Post et al., 2013), which influences the temperature of the water column in the region, including the extent of the "cold pool" (Stabeno and Overland, 2001;Overland and Stabeno, 2004;Sarmiento et al., 2004;Stabeno et al., 2007;Steele et al., 2008).Such shifts in the physical environment have been Published by Copernicus Publications on behalf of the European Geosciences Union.

T. Yamamoto et al.: Differential responses of seabirds to environmental variability
shown to affect the ecosystem, including the seasonality and biomass of primary production, metabolic rates, distribution, and abundance of consumers, and changes in pelagic-benthic coupling (Grebmeier et al., 2006;Mueter and Litzow, 2008;Hunt et al., 2011;Wassmann, 2011;Wassmann et al., 2011;Dorresteijn et al., 2012).The Bering Sea is a transition region between Arctic and sub-Arctic seas, and, hence, physical and biological changes in this region may also influence the extent of sea-ice cover and species abundance and composition in the adjacent Arctic Sea (i.e., the Chukchi Sea) (Shimada et al., 2006;Matsuno et al., 2012;Yamamoto et al., 2015).
Predicting the effects of climate change on marine top predators is a major challenge in ecology.Long-term monitoring of seabird demography has been conducted on the Pribilof Islands (Byrd et al., 2008a;Renner et al., 2012;Mudge et al., 2015), which host one of the largest concentrations of piscivorous seabirds in the North Pacific.Previous studies have demonstrated that historical fluctuations in the diet of seabirds (Byrd et al., 2008a;Sinclair et al., 2008;Renner et al., 2012) might reflect broad-scale changes in climate (e.g., regime shift: Benson and Trites, 2002).Although some studies found broad species-and regional-specific relationships between climate variables and breeding parameters (Byrd et al., 2008b), the mechanistic response of seabirds to local climate variability has been elusive and others suggested only weak relationships (Satterthwaite et al., 2012;Renner et al., 2014).This is probably due, in part, to reproductive failure that may occur at several stages of the breeding process (e.g., nest building, egg-laying, incubation, and chick-rearing).It may also be influenced by reproductive effort associated with foraging conditions not only in the current season but also during the previous breeding season (Harrison et al., 2011;Catry et al., 2013).Furthermore, seabirds can adapt their behavior by increasing foraging range and effort in response to changes in the environment, potentially masking effects on some breeding parameters (Kitaysky et al., 2000;Pinaud et al., 2005;Harding et al., 2007).Meanwhile, changes in behavior and prey availability relating to environmental conditions appear to affect their physiological condition (i.e., nutritional stress as reflected in secretion of corticosterone).For example, piscivorous birds breeding on the Pribilof Islands have been shown to experience greater food limitation on the continental shelf during cold years, attributed to higher levels of nutritional stress (Benowitz-Fredericks et al., 2008;Satterthwaite et al., 2012;Harding et al., 2013).To obtain more direct mechanistic insight into their responses to ecosystem dynamics in relation to climate variability, at-sea foraging behavior of breeding seabirds should be examined in concert with the physiological condition.However, there is little information available for the comparative at-sea behavior of seabirds in relation to different environmental conditions in this region (Kokubun et al., 2010;Paredes et al., 2014).
Ship-based observations can provide information on atsea habitat utilization of species (Hunt et al., 2008(Hunt et al., , 2014;;Kuletz et al., 2014;Wong et al., 2014) together with oceano-graphic characteristics (Piatt and Springer, 2003;Gall et al., 2013).Although these studies are valuable to detect seasonal, annual, and decadal changes in species distributions (Gall et al., 2013;Hunt et al., 2014;Kuletz et al., 2014), spatial and temporal coverage as well as the context of reproductive processes studied at colonies are limited.The recent availability of animal-borne devices enhances our ability to examine habitat utilization of free-ranging individuals (review by Burger and Shaffer, 2008) and may provide more insight into population processes in relation to ocean variability (Weimerskirch et al., 2001;Paredes et al., 2014).
In this study, we examined the foraging behavior of two seabird species that exhibit different habitat use: surfaceforaging red-legged kittiwakes Rissa brevirostris (hereafter, RLKI) feeding in the oceanic habitat and pursuit-diving thick-billed murres Uria lomvia (TBMU) feeding mainly in the continental shelf habitats, and how they responded to changes in environmental conditions over 2 years.The effects of ocean variability on an ecosystem may differ between water masses, and, hence, seabird responses may show different patterns (Benowitz-Fredericks et al., 2008;Byrd et al., 2008b), which, in turn, could provide information on how ecosystem dynamics respond to fluctuations in marine environmental conditions (Frederiksen et al., 2007;Piatt et al., 2007).

Study site
Fieldwork was conducted on St. George Island (56 • 34 N, 169 • 37 W) in the Pribilof Islands, Alaska, USA, over 2 years in July-August 2013 and 2014.Birds were captured from their nesting sites using a noose pole, and GPS loggers (GiPSy-2 with chip antenna or GiPSy-4 with patch antenna; TechnoSmart, Rome, Italy) were attached to the backs of 19 RLKIs and 11 TBMUs in 2013 and 14 RLKIs and 14 TBMUs in 2014 using Tesa ® tape and cyanoacrylate glue (Loctite ® 401).The loggers were housed in heat-shrink tubing for water-proofing and were set to record five successive fixes every minute for GiPSy-2 and one fix every minute for GiPSy-4.The equipped birds were recaptured after 2-6 days since the deployment, and the loggers were recovered.We retrieved the loggers from 15 RLKIs and 9 TBMUs in 2013 and 10 RLKIs and 11 TBMUs in 2014.Some equipped birds were resighted, but we failed to recapture them as they nest at the cliff.Previous studies suggested that attachment of small and lightweight tags (usually < 5 % of body mass) do not appear to affect foraging and/or reproductive behavior of individuals (e.g., Phillips et al., 2003;Carey, 2011), while other studies reported an adverse effect on their behavior as well as physiological condition (e.g., Barron et al., 2010;Elliott et al., 2012).In this study, the total weight of the logger including the heat-shrink tubing and tape was 15-16 g, which corresponds to less than 5 % of the mean body mass of equipped birds (the mean ± SD: RLKI 375 ± 29 g, TBMU 1024 ± 43 g).The recovery rate excluding some resighted individuals was relatively high (71-82 %), and the attachment of tags did not result in, at least, the breeding abandon.
Of the loggers retrieved, some failed to record locations.Hence, location data were available for 5 and 7 RLKIs (20 July-5 August) and 5 and 10 TBMUs (2-12 August) in 2013 and 2014, respectively.Data for RLKIs in 2013 were reanalyzed from Kokubun et al. (2015).At the time of recapture, blood samples were taken from the brachial vein of each individual and kept on ice until centrifugation to separate the plasma from the red blood cells, and both were kept frozen until assayed.Plasma was used for measurement of physiological stress exposure (corticosterone: CORT) and red blood cells for determining trophic level (stable isotopes: SI).CORT was measured only for samples that were taken within 3 min of capture, as it takes 3 min for levels of CORT to begin to rise in the blood in response to the acute stress of capture and restraint (Romero and Reed, 2005).
During the study period, we opportunistically obtained adult diets of RLKIs by regurgitation at the time of logger deployment and/or retrieval.Prey species of RLKI samples were identified visually or using otoliths (N = 22 in 2013 and N = 15 in 2014) (also see Kokubun et al., 2015).TBMU chick diet was recorded from direct observation of adult birds (both with and without data loggers) carrying prey items back to their nests in their bill.Prey items were visually identified during observation or later from photographs (N = 13 in 2013 and N = 39 in 2014).

Data analysis
GPS locations were re-sampled every 1 min by averaging fixes recorded within each min for GiPSy-2.We used a forward-backward speed filter (McConnell et al., 1992), and positions that exceeded 20 m s −1 were considered erroneous and removed (Paredes et al., 2012;Evans et al., 2013).We defined foraging trips as any time period when the birds beyond a 500 m buffer around the colony for more than 30 min.We determined locations of resting on water (as a proxy for foraging) during foraging trips based on flight speed (Zavalaga et al., 2011;Kokubun et al., 2015).Flight speed less than 3 m s −1 for RLKIs (Paredes et al., 2012) and 5 m s −1 for TB-MUs (Evans et al., 2013) were considered "resting on water".The straight-line distances between the colony and on-water locations were measured, as were the bottom depths where the birds were resting on the water.The marine habitats were categorized into three regions based on bathymetry as follows: on-shelf (0-200 m bottom depth), shelf break (200-1000 m bottom depth), and oceanic basin (> 1000 m bottom depth) (Paredes et al., 2012).
To examine the differences in marine environment between the 2 study years (2013 vs. 2014), satellite remotesensed monthly mean sea surface temperatures (SSTs) in August (NOAA POES AVHRR, GAC, 0.1 • ) within 350 km around the colony (within the foraging ranges of RLKI and TBMU; see Results) and the timing of sea-ice retreat in the southeastern Bering Sea (a Bering Sea Ice Retreat Index; IRI) were obtained from the National Oceanic and Atmospheric Administration (NOAA), available at http://coastwatch.pfel.noaa.gov/coastwatch/CWBrowserWW180.jsp for SSTs and http://access.afsc.noaa.gov/reem/ecoweb/dataWindow.php?Data=IRI for IRI.IRI represents the number of days after March 15 in which areal sea-ice concentration was greater than 10 % in a 2 • × 1 • box (bounded by 56.5-57.5 • N and 163-165 • W).Locations and environmental data were analyzed and mapped using the ESRI ® ArcGIS.
In addition to the GPS tracking, we also analyzed behavioral data of birds obtained by geolocators (2.5 g, Mk19; Biotrack Ltd., UK) and accelerometers (12 mm diameter × 45 mm length, 10 g, ORI-380 D3GT; Little Leonardo, Japan).As the location records did not cover a complete foraging trip in several GPS tracks (see Results, Fig. S1 in Supplement), we used these data to confirm the foraging trip durations in each year supplementarily.For the geolocatorcarrying birds, the foraging trip duration was defined as the time between the first and last landing on water (i.e., immersion) before and after a long dry event, which is likely an underestimation, though comparable between the years (see Fig. S2).For the accelerometer-carrying birds, the start and end of a foraging trip was identified from changes in bird posture as well as outward/inward flight activity recorded as cyclic fluctuations of acceleration (see details for Takahashi et al., 2008).Data were analyzed for 22 trips from 4 birds in 2013 and 14 trips from 5 birds in 2014 for RLKI (26 July-2 August) and 9 trips from 9 birds in 2013 and 21 trips from 12 birds in 2014 for TBMU (31 July-12 August).
CORT concentrations were measured for 8 RLKIs and 20 TBMUs in 2013 and 7 RLKIs and 21 TBMUs in 2014.CORT concentrations (ng mL −1 ) were measured using a radioimmunoassay (for details see Kitaysky et al., 1999).Briefly, each sample was equilibrated with 2000 cpm of tritiated CORT prior to extraction with 4 mL re-distilled dichloromethane.After extraction, percent tritiated hormone recovered from each individual sample (average hormone recovery was, mean ± SD, 94.68 ± 2.86 %) was used to correct final CORT concentrations.Samples were reconstituted in phosphate-buffered saline gelatin buffer and combined with antibody and radiolabel in a radioimmunoassay.Dextrancoated charcoal was used to separate antibody-bound hormone from unbound hormone.All samples were analyzed in two different assays; CV = 7 % for inter-assay and < 2 % for intra-assay).
The instrumentation used was a Delta + XP interfaced with a Costech ESC 4010 elemental analyzer.Stable isotope ratios are reported in δ (Delta) notation as parts per thousand (‰) deviation from the international standards δ 15 N air according to: δ 15 N = [(R sample /R standard )−1] × 1000 ‰, where R sample/standard is the corresponding ratio 14 N / 15 N. Replicate measurement of an internal laboratory standard (Peptone) indicated measurement errors to be ±0.16‰.Samples were analyzed at the University of Alaska Fairbanks Stable Isotope Facility.

Statistical analysis
Statistical analyses were carried out in R software (version 2.15.3,R Development Core Team 2008).Differences in foraging parameters (bathymetry and distance from the colony in on-water locations and trip duration) between the years were examined with generalized linear mixed models (GLMM) using Poisson (for the bathymetry and trip duration) or Gaussian (for the distance) distributions, including bird identity as a random factor.We tested the interannual differences in CORT (log-transformed) and SI by conducting one-way ANOVA.Statistical significance was assumed at P <0.05.Values reported are means ± standard errors or standard deviations (SDs).3 Results

Foraging behavior
For RLKI, 12 trips in 2013 and 8 trips in 2014 were recorded with GPS loggers.Two trips were recorded partially, and the other trips included complete tracks (N = 5) and tracks recorded until close to the beginning of or during the homing commute phase (N = 13, see Fig. S1a), having 59 ± 26 % of available location fixes during the trips.In both years, RLKIs traveled predominantly towards the south from the colony and to a lesser extent towards the north and west (Fig. 1a, b).On-water locations (a proxy for foraging) occurred mostly over the oceanic basin in both years (> 87 % of the locations; Fig. 2) (GLMM, Z = −0.28,P = 0.78).Foraging distances from the colony peaked at 250-300 km in 2013 and bimodally at 150-250 and 300-350 km in 2014 (Fig. 3), though mean distance did not differ significantly between the years (GLMM, t = 0.92, P = 0.36).
For TBMU, 11 trips in 2013 and 22 trips in 2014 were recorded with GPS loggers, including 2 partial tracks, 29 complete tracks, and 2 incomplete tracks (recorded until close to the beginning of or during the homing commute phase) (Fig. S1b), having 68 ± 24 % of available location fixes during the trips.TBMU traveled to the southeast and west of the colony in 2013 (Fig. 1c), while birds traveled mostly towards the north and east in 2014 (Fig. 1d).In both years, TBMU foraged mostly over the shelf (GLMM, Z = 0.23, P = 0.82) but showed a relatively higher use of the shelf break and oceanic basin in 2013 (Fig. 2).The foraging distances from the colony tended to be farther in 2013 compared to these in 2014, though not significantly so (GLMM, t = −1.30,P = 0.19) (Fig. 3).

Annual differences in marine environment
SSTs within the foraging range (< 350 km from the colony;

Discussion
Surface-feeding RLKI and pursuit-diving TBMU showed differences in habitat use.RLKI foraged extensively over the deep oceanic basin, while TBMU foraged mostly on the shelf.The behavioral and physiological responses to the ocean variability over 2 years differed between the species.
Between the 2 study years, SST around the colony was relatively cooler in 2013 than in 2014, probably reflecting the later sea-ice retreat in 2013 as winter sea-ice conditions strongly influence water temperatures during the following summer (Khen, 1999;Overland et al., 1999;Kokubun et al., 2010;Stabeno et al., 2012).RLKI showed a consistent use of the oceanic habitat with similar levels of CORT in both years, though they reached to relatively farther areas in 2013 than 2014.In comparison, TBMU used the oceanic basin to the south of the colony more frequently in 2013, exhibiting relatively farther travel distances and higher levels of CORT.Based on the δ 15 N values (an indicator for trophic level; Hobson et al., 2002) and diet sampling/observation, both RLKI and TBMU probably had similar prey composition between the years.
During the study period, the fledgling success (the mean ± SD) of RLKI and TBMU on St. George Island differed between the years: dramatically for RLKI, with 0.57 ± 0.07 in 2013 and 0.92 ± 0.02 in 2014, and less so for TBMU, with 0.95 ± 0.02 in 2013 and 0.89 ± 0.02 in 2014 (Mudge et al., 2015).Fledgling success may be related to behavior prior to breeding (i.e., the timing of breeding; Renner  (Mudge et al., 2015).Therefore, the fledgling success during the study period may be related to food resource conditions during the breeding season in the given years, suggesting better conditions in 2014 (relatively warmer SSTs with earlier sea-ice retreat) than 2013 (relatively cooler SSTs with later sea-ice retreat).RLKIs mainly feed on myctophids over deep oceanic regions (Sinclair et al., 2008;Kokubun et al., 2015).As RLKIs are a surface-feeding seabird, they are considered to feed on vertically migrating myctophids (Hunt et al., 1981).The water column in the deep ocean may show less interannual variation in water temperature compared to that of the shallower shelf region (see Results in this study) where the deep cold pool (temperature remains below < 2 • C) forms in relation to the timing of sea-ice retreat (Stabeno et al., 2012).Previous studies suggested that the availability of prey for seabirds in shelf habitats may be less stable (Einoder et al., 2011) and less predictable over long timescales compared to basin habitats (Weimerskirch, 2007).Furthermore, myctophids are supposed to be still available when prey availability over the shelf is low (Sinclair et al., 2008;Paredes et al., 2014).Nonetheless, RLKI showed a slight difference in foraging locations over the oceanic basin between the years, which may be affected by other factors besides SST and IRI (Sinclair et al., 2008).Recently, Paredes et al. (2014) hypothesized that the existence of mesoscale eddies, which typically develop in the Aleutian Basin (Mizobata et al., 2002), may affect the vertical distribution of myctophids for kittiwakes (Godø et al., 2012).The sympatric and closely related blacklegged kittiwakes (Rissa tridactyla) foraged at locations near the perimeter of anticyclonic eddies (upwelling) and inside or near cyclonic eddies (downwelling) and experienced higher levels of nutritional stress when eddies were weak possibly due to low availability of prey (Paredes et al., 2014).Similarly, RLKIs in this study may have altered their foraging locations in relation to the existence of these eddies (Fig. S3).However, it has been not certain how distribution and abundance of myctophids are actually related to the strength of eddies, and no correlations were found between eddy kinetic energy and fledging success of black-legged kittiwakes (Paredes et al., 2014).Compared to TBMU, RLKI exhibited consistently high levels of CORT in both years with different fledgling success.This may reflect potential competition with black-legged kittiwakes that also feed on myctophids in the ocean basin (Sinclair et al., 2008;Renner et al., 2012).In the Pribilof islands, black-legged kittiwakes had switched their reliance upon Pollock during the 1970s and 1980s to myctophids by the 1990s (Sinclair et al., 2008).Accordingly, red-legged kittiwakes are the species most threatened by population declines since the 1980s.Hence, there is a possibility that the foraging effort of RLKI is at the limit, as the indi-cation of elevated CORT includes the increase in foraging effort (Kitaysky et al., 2010).Such inter-specific competition appears to be relatively higher during cold years (Satterthwaite et al., 2012;Paredes et al., 2014), possibly resulting in the lower fledgling success in 2013, the year of relatively cooler SSTs with later sea-ice retreat.In fact, the mean (±SD) growth rate (g day −1 ) of RLKI was better in 2014 (14.9 ± 3.7 g) than 2013 (11.7 ± 3.6 g) (Mudge et al., 2015).
Compared to RLKI, TBMU exhibited fluctuating physiological condition and flexible behavioral changes in parallel to the ocean variability between the years, yet without a difference in fledgling success.Late sea-ice retreat is associated with an early, cold-water phytoplankton bloom, relatively low biomass of small shelf copepods, and poor survival of larval and juvenile forage fish, including their main prey (juvenile walleye pollock: Hunt et al., 1996;Sinclair et al., 2008;Renner et al., 2012).However, early sea-ice retreat is associated with a later, warm-water plankton bloom, a large biomass of small shelf copepods later in the season, and high abundance of larval and juvenile forage fish (Hunt et al., 2002).Moreover, forage fish species including juvenile walleye pollock are less abundant on the continental shelf during cold years because they either disperse or travel deeper to avoid cold waters (Hollowed et al., 2012), as juvenile pollock are associated with warm bottom temperatures (Brodeur et al., 1998).A northern location of the ice edge during spring may be linked to higher SST and water temperature at depth (Kokubun et al., 2010;Stabeno et al., 2012).The cold pool acts as a cross-shelf migration barrier for subarctic fish species (e.g., walleye pollock and Pacific cod), forcing these fish to remain on the outer shelf and separating them from food sources in the middle shelf and coastal domain.Thus, a warmer shelf would provide them with a larger area of suitable habitat (Ciannelli and Bailey, 2005;Kotwicki et al., 2005).In addition, distribution and availability of euphausiids and copepods, the prey species for juvenile walleye pollock (Schabetsberger et al., 2000;Ciannelli et al., 2002), likely change in relation to interannual differences in water temperatures in the shelf region (Smith, 1991;Ohashi et al., 2013;Yamamoto et al., 2015).Hence, we assume that the abundance/availability of pollock on the shelf was probably relatively higher in 2014 (the year of warmer SSTs and earlier sea-ice retreat) compared to 2013 (the year of cooler SSTs and later sea-ice retreat).The closer proximity of St. George to the continental shelf break may be considered to be an important buffer in years when food supply on the shelf is poor (Byrd et al., 2008b;Renner et al., 2014).Previous studies showed that TBMU breeding on St. George Island traveled longer distances to forage at the shelf break and the ocean basin in a cold year (Harding et al., 2013).Seabirds are known to increase foraging ranges in response to reductions in prey availability (Suryan et al., 2000;Pinaud et al., 2005;Harding et al., 2007;Bertrand et al., 2012), but longer and farther foraging trips likely cause higher levels of nutritional stress (2013 in this study), especially for TBMU whose flight cost is presumed to be high (Houston et al., 1996).
In this study, chick-rearing RLKIs did not change their foraging locations largely in relation to marine environmental changes probably due to their reliance on myctophids, which live in the deep waters of the pelagic zone (Sinclair and Stabeno, 2002), for feeding young (Kokubun et al., 2015).However, their foraging effort might also be affected by the position and strength of local eddies, which are reflected by atmospheric control (the North Pacific Index and Multivariate ENSO Index; Ladd et al., 2012, andLadd, 2014).TBMU showed fluctuations in physiological condition and flexible foraging behavior, which probably corresponded to ocean variability (exhibited longer and farther trips in the relatively cooler year of 2013).Hence, although we compared foraging behavior of seabirds in different environmental conditions only over 2 years with limited sample sizes, our study has suggested that there is possible interspecific differences in species' response to warming, which may reflect differences in ecosystem dynamics between habitats they use for foraging, as the decrease in sea-ice extent showed negative effects on foraging behavior for other species in a different Arctic region (e.g., black guillemots Cepphus grylle mandtii; Divokey et al., 2015).Elevated stress levels may have a cascading effect on subsequent life stages, such as migration, postbreeding survival, breeding propensity, and timing of breeding (Verhulst and Nilsson, 2008;Schoech et al., 2009;Goutte et al., 2010;Kitaysky et al., 2010;Harrison et al., 2011), and, as a result, overall productivity (Kitaysky et al., 2007(Kitaysky et al., , 2010;;Renner et al., 2014).We suggest that year-round monitoring of foraging distribution and stress incurred by birds, including those during the post-breeding migration, should be conducted to understand further how these species are affected by changing climate (Kitaysky et al., 2010;Satterthwaite et al., 2010;Schultner et al., 2014).

Figure 1 .
Figure 1.Foraging trip trajectories of red-legged kittiwakes, RLKI (a, b), and thick-billed murres, TBMU (c, d), in 2013 and 2014, respectively.Black dots represent location fixes and blue or red circles represent on-water (i.e., foraging) locations.The star indicates the breeding colony, St. George Island.The background shows the bathymetry: white indicates on-shelf (0-200 m bottom depth), light grey is shelf break (200-1000 m), and grey is oceanic basin (> 1000 m).

Figure 3 .
Figure 3.The straight-line distances between the colony and onwater locations of red-legged kittiwakes (RLKI) and thick-billed murres (TBMU) in 2013 (blue bars) and 2014 (red bars).The mean and standard error are presented.