- Top of page
- Material and Methods
- Conflict of Interest
Under current climate trends, spring ice breakup in Hudson Bay is advancing rapidly, leaving polar bears (Ursus maritimus) less time to hunt seals during the spring when they accumulate the majority of their annual fat reserves. For this reason, foods that polar bears consume during the ice-free season may become increasingly important in alleviating nutritional stress from lost seal hunting opportunities. Defining how the terrestrial diet might have changed since the onset of rapid climate change is an important step in understanding how polar bears may be reacting to climate change. We characterized the current terrestrial diet of polar bears in western Hudson Bay by evaluating the contents of passively sampled scat and comparing it to a similar study conducted 40 years ago. While the two terrestrial diets broadly overlap, polar bears currently appear to be exploiting increasingly abundant resources such as caribou (Rangifer tarandus) and snow geese (Chen caerulescens caerulescens) and newly available resources such as eggs. This opportunistic shift is similar to the diet mixing strategy common among other Arctic predators and bear species. We discuss whether the observed diet shift is solely a response to a nutritional stress or is an expression of plastic foraging behavior.
- Top of page
- Material and Methods
- Conflict of Interest
Polar bears (Ursus maritimus) are the most carnivorous of the Ursids, feeding primarily on ringed seals (Phoca hispida) and less frequently on bearded seals (Erignathus barbatus) and other marine mammals while sea ice is available for hunting (Stirling and Archibald 1977; Thiemann et al. 2008). Most of this foraging occurs in spring when polar bears accrete the majority of their fat reserves from ringed seals and their newborn pups (Stirling and Øritsland 1995). The ice in western Hudson Bay melts completely by mid- to late July forcing the bears ashore without easy access to their primary prey until freeze-up in the following fall (Gagnon and Gough 2005). While ashore, polar bears are in a negative energy balance (Derocher et al. 1993), reportedly surviving primarily on their fat reserves, although supplementary, terrestrial foods are also consumed when available (e.g., Lunn and Stirling 1985; Derocher et al. 2013). This period onshore is projected to increase as warming trends keep Hudson Bay ice free for progressively longer periods each year (e.g., Stirling and Parkinson 2006). Surviving these extended periods on land without access to seals is believed to be critical to the persistence of polar bears in western Hudson Bay (Molnár et al. 2010).
Polar bears are known to consume various types of terrestrial and marine foods during the ice-free period (hereafter terrestrial or land-based foods). Items reported include marine algae (Harrington 1965), grasses (Koettlitz 1898), berries (Russell 1975), fish (Dyck and Romberg 2007), small mammals (Pedersen 1966; Russell 1975), caribou (Rangifer tarandus) (Derocher et al. 2000), seals (Russell 1975), various species of waterfowl and their eggs (e.g., Stempniewicz 1993; Drent and Prop 2008; Rockwell and Gormezano 2009), and willow ptarmigan (Lagopus lagopus) (Miller and Woolridge 1983).
Despite these observations, some of which date back to the late 1800s (Koettlitz 1898), polar bears are often referred to as “fasting” while ashore (e.g., Amstrup et al. 2007; Molnár et al. 2010; Robbins et al. 2012). Although the term may apply to some polar bears, extension to the majority of the western Hudson Bay population seems inappropriate given multiple observations to the contrary (see above), and the inherent limitations of behavioral and physiological studies (Knudsen 1978; Latour 1981; Ramsay and Hobson 1991; Hobson et al. 2009) that are often used to justify the term's use. For example, observational studies may only offer a snapshot of behavior for discrete periods (Knudsen 1978; Latour 1981) and coastal or inland sampling may preclude certain demographic groups because they tend to spatially segregate once ashore (Latour 1981; Derocher and Stirling 1990). Physiological studies, such as stable carbon isotopes and fatty acid signatures offer a more integrated assessment of the diet but are fraught with inconsistencies. For example, stable carbon isotopes can give variable results depending on the tissue examined (Ramsay and Hobson 1991; Hobson et al. 2009) and the mixing of marine and terrestrial signatures of foods polar bears commonly consume on land (e.g., marine algae, waterfowl feeding in salt marshes; McMillan et al. 1980; Hobson et al. 2011). Fatty acid signatures can vary by individual depending on differential accumulations and deficits (Pond et al. 1992; Grahl-Nielsen et al. 2003).
The direct analysis of passively sampled scat offers several advantages for determining dietary details on the extent and pattern of land-based foraging by polar bears. Scats deposited reflect foods consumed over longer spans (i.e., spring, summer, or fall), through various diurnal cycles, and during weather changes in which periods of active foraging may fluctuate. Although exact numbers and sexes of polar bears sampled cannot be assessed from scat in the absence of genetic analyses, collection of scats over a large geographic extent increases the chances of sampling from different sex and age groups and from different individual polar bears given their tendency to move relatively little once ashore (Derocher and Stirling 1990; Parks et al. 2006). While exploring the nutritional and energetic value of terrestrial food is beyond the scope of this study, we use scat analysis to examine the land-based diet of polar bears across a large portion of the terrestrial habitat used during the ice-free period in western Hudson Bay.
Reports of polar bears exploiting land-based prey have become more common in recent years (e.g., Derocher et al. 2000; Drent and Prop 2008; Rockwell and Gormezano 2009; Iles et al. 2013). For example, consumption of eggs and young from nesting colonies of waterfowl across the Arctic is increasingly pervasive, and predation on larger land mammals, such as caribou, had been reported (Derocher et al. 2000). Although categorized as specialists that primarily hunt seals on the ice (Derocher et al. 2004; Amstrup et al. 2007), polar bears have been observed walking, running, and even climbing cliffs (Smith et al. 2010) on land to pursue alternate prey. Like other bear species, polar bears may well be opportunists, pursuing the most readily available food source (Lunn and Stirling 1985; Beckmann and Berger 2003; Thiemann et al. 2008). It remains unclear whether exploiting these alternate foods (behavioral shifts) is mainly a response to nutritional stress or simply a typical Ursid response to a changing food supply.
To better understand how polar bears may be reacting to climate change or other environmental factors, we first created a comprehensive inventory of the current polar bear diet across their terrestrial range in western Hudson Bay by analyzing passively collected scat. Second, to identify any dietary shifts during the ice-free season that may have occurred since the recent onset of rapid climate changes we compared our data to a similar scat-based diet study performed in the Hudson Bay Lowlands 40 years earlier by Russell (1975). In parallel with this comparison, we compared the average 50% breakup dates during this and Russell's diet study as an index of climate-related environmental change between the two time periods. Finally, we explore other possible bases for the observed shifts in land-based foraging we document and discuss the implications they have for polar bears' ability to persist in the face of reduced ice conditions that limit their time to hunt seals.
- Top of page
- Material and Methods
- Conflict of Interest
We collected a total of 1262 scats and analyzed 642 of them; 219, 248, and 175 in 2006, 2007, and 2008, respectively (Table 1). Of these, 593 scats were collected from coastal areas and 49 from inland areas. Nearly one-third (29.0%) of all scats contained bird and/or egg remains, the majority of which were snow geese (43.1% of bird remains) and Canada Geese (9.7% of bird remains). Eggs occurred in 4.4% of scats. The most common mammals were caribou (10.1%), seal (most likely P. hispida) (6.5%), and polar bear (from cannibalism, not grooming) (5.1%), with small mammals (i.e., rodents, Arctic or snow-shoe hares [Lepus arcticus and L. americanus]) occurring in lower frequencies (<1.0%). Grasses (61.7%; mainly Lyme grass, 57.0%) and various species of marine algae (46.1%) were the primary forms of vegetation. Other common food items include mosses, puffball mushrooms, and berries, occurring in 13.6%, 8.9%, and 8.7% of scats, respectively.
Table 1. The frequencies of food items in 642 polar bear scats from western Hudson Bay 2006-2008
| ||Raw frequenciesa||Scat occurrences|
|Taxa|| n ||%||%|
| Birds |
|Anser caerulescens caerulescens||80||5.9||12.5|
|Galliformes, Lagopus lagopus||3||0.2||0.5|
|Passeriformes, Plectrophenax nivalis||1||0.1||0.2|
| Limnodromus griseus ||1||0.1||0.2|
|Egg shell/hatching membrane||28||2.1||4.4|
|Aves – total||208||15.3||29.0|
| Mammals |
|Ursidae, Ursus maritimus||33||2.4||5.1|
|Cervidae, Rangifer tarandus||65||4.8||10.1|
|Lagomorpha, Lepus spp.||2||0.1||0.3|
|Mammalia – total||157||11.6||22.0|
|Animal (Mammal or Bird), indeterminable||11||0.8||1.7|
| Marine invertebrates |
|Asteroidea (sea stars)||1||0.1||0.2|
|Bivalvia, Mytilus edulis||4||0.3||0.6|
|Leymus arenarius (43 had seed heads)||366||27.0||57.0|
|Grasses – total||433||31.9||61.7|
| Mushrooms |
|Lycoperdon pyriforme or L. perlatum||57||4.2||8.9|
No pairs of food items in scat piles showed significant patterns of co-occurrence at our adjusted alpha error level, and we therefore consider food items to occur independently in scats. This lack of co-occurrence justifies the use of the raw frequencies of food items as a unit of measure in subsequent statistical tests rather than the number of scats containing each item. Perhaps not surprisingly, marine algae and berries were observed together less often than expected (G = 6.31, df = 1, P = 0.013), although the result did not reach the adjusted alpha level (14 tests; α = 0.0035) required to avoid error inflation.
Comparison of diet changes over time
We compared 593 scats (1237 occurrences) of our coastal data with 212 scats (528 occurrences) from Russell's study to examine polar bear diet changes over time. We found a shift in the frequencies of major food categories (animals, vegetation, garbage) (G = 25.54, df = 2, P < 0.0001). This result was due to a larger proportion of animals ( = 27.32, CI = 25.13–29.18 vs. = 23.48, CI = 20.00–27.16) and less garbage ( = 3.23, CI = 2.11–4.61 vs. = 9.09, CI = 6.05–12.58) in scats in our study compared to Russell's study (Fig. 2A). Within these major food categories, there were differences in the frequencies of nine major food items (birds, mammals, Lyme grass, other grasses, marine algae, berries, mushrooms, moss, and garbage; G = 130.31, df = 8, P < 0.0001). The two diets (historic vs. current) also differ in the rank order of items (Mann–Whitney test: U = 317; P = 0.015).
Figure 2. The percent frequencies of some food items found in scat along the coast of western Hudson Bay differed between collections made in 1968–1969 and 2006–2008. Analytical 95% confidence intervals are indicated for each. Note the y-axis scale differences in the depictions for (A) pooled categories (animals, vegetation, and garbage) and individual (B) animal and (C) plant, fungi, and garbage food items.
Download figure to PowerPoint
Among animals, rodents occurred considerably more frequently in Russell's study ( = 7.95, CI = 5.80–10.59) than in ours ( = 0.65, CI = 0.28–1.27), but we observed more polar bear remains ( = 2.59, CI = 1.48–3.63 vs. = 0.38, CI = 0.05–1.36). Russell did not detect any caribou, whereas caribou was the most common mammal found in our study ( = 4.69, CI = 3.58–6.02). There was no significant difference in the frequencies of seals or birds, but we found eggs in scats ( = 2.18, CI = 1.44–3.16), whereas Russell did not (Fig. 2B).
Table 2. Comparison of food items in polar bear scats from coastal areas of western Hudson Bay, Manitoba, (2006-2008) and Cape Churchill, Cape Henrietta Maria, and the west Pen Island (1968-1969)
| || ||Gormezano & Rockwell (2006-2008)||Russell (1968-1969)|
| || ||Raw frequencies||Scat occurrences||Raw frequencies||Scat occurrences|
|Taxa|| || n ||%||%|| n ||%||%|
|Aves – unidentified||43||3.5||7.3||52||9.8||24.5|
|Egg shell/hatching membrane||27||2.2||4.6||0||0.0||0.0|
|Aves total + eggs||192||15.5||28.8||56||10.6||26.4|
|Ursidae, Ursus maritimus||32||2.6||5.4||2||0.4||0.9|
|Cervidae, Rangifer tarandus||58||4.7||9.8||0||0.0||0.0|
|Mammalia – unidentified||6||0.5||1.0||4||0.7||1.9|
|Mammalia – total||146||11.8||24.6||68||12.9||32.1|
|Grasses – total||410||33.1||63.1||170||32.2||80.2|
Coincident with these dietary changes, we estimated the mean breakup date during Russell's study (1968–1968) to have been 17 July, which is 22 days later than the mean breakup date for this study (2006–2008).
- Top of page
- Material and Methods
- Conflict of Interest
If the trend toward earlier spring ice breakup in Hudson Bay continues, polar bears will spend more time onshore during summer, making any foods consumed during this period increasingly important for the bears' persistence. Their current land-based diet is diverse, consisting of many plants and animals, often consumed together in various combinations. Numerous scats were collected across the entire Cape Churchill Peninsula, from both coastal and inland areas. Given the spatial extent of our sampling, and the propensity for bears to segregate (Latour 1981; Derocher and Stirling 1990) and to move relatively little once ashore (Parks et al. 2006), we assume our results reasonably reflect the land-based diet of those polar bears that do forage on the Cape Churchill Peninsula during the ice-free period. However, consistent with behavioral observations we have made (Iles et al. 2013; Gormezano and Rockwell, in review) and foraging reports by others (e.g., Dyck and Romberg 2007; Smith et al. 2010), it appears that a number of polar bears do not abstain from eating during the ice-free period. Continued use of the term fasting to describe the behavior of polar bears in general during this period (e.g., Stirling and Derocher 2012) seems rather misleading.
Many foods polar bears are consuming have not changed since the 1960s on the Cape Churchill Peninsula, but we did find new foods and marked changes in the frequency of others. The overall proportion of animals in the diet has increased, whereas the proportion of vegetation has not changed. Caribou and eggs are now present in the diet, the proportion of polar bear remains has increased and that of small mammals has decreased. We also identified more species of birds (11 vs. 1), the majority of which were lesser snow geese. Most scats contained at least one type of vegetation and there were only minor shifts in the types consumed. We also found less garbage in scats than was found in the 1960s (Russell 1975). In the following, we discuss various habitat and environmental changes that occurred during the ensuing 40 years coincident with observed diet changes, including a 22-day advance in the date of sea ice breakup and the closing of the Churchill dump.
Russell did not report caribou or snow geese in polar bear fecal samples collected along the coast of the Hudson Bay Lowlands. In the 1960s, fewer than a hundred caribou were estimated for the population north of the Nelson River (C. Jonkel, S. Kearney, pers. comm.) and sparse groups of <50 animals were counted further south (Abraham and Thompson 1998). Caribou numbers have been increasing steadily (30- to 50-fold) since (Williams and Heard 1986; C. Jonkel, S. Kearney, and R. Brook, pers. comm.), while the animals are also expanding their summer range toward the coast (Abraham and Thompson 1998), thus increasing potential interactions with arriving bears (Fig. 3). Similarly, snow goose abundance has increased 5- to 20-fold across the region since the 1960s (Hanson et al. 1972; Kerbes et al. 2006; Alisauskas et al. 2011), with highest increase and geographic expansion being on the Cape Churchill Peninsula (Rockwell et al. 2009).
Figure 3. A polar bear looks up from the recently killed caribou it was eating at Keyask Island (58.16958°N 92.85194°W) on July 26, 2010. Photograph by R. F. Rockwell.
Download figure to PowerPoint
Although the scarcity of snow geese in the region during the 1960s likely explains their absence in Russell's study, it is important to note that considerably more (96.2%) of his bird remains were left unidentified compared to our study (21.6%). This may have been due, in part, to our use of more stringent bird identification techniques (see Material and Methods). However, all of Russell's unidentified bird remains comprised “trace to 5.0%” amounts by volume, whereas only 16.2% of our snow goose remains occurred in “trace to 5.0%” amounts. The remaining 83.8% of our scats with snow goose comprised an average of 65.0% of a scat pile by volume, with nearly 40% comprising >90% of a pile. Given the size of lesser snow geese and direct observations of how polar bears consume them (Iles et al. 2013), these larger volumes seem reasonable and their absence in Russell's study further suggest that the unidentified bird remains were likely not snow geese.
Polar bears seem to have taken advantage of the substantial increase in availability of both caribou and snow geese (Table 1). During the summer months, when the two species are raising their offspring, polar bears arriving onshore now regularly overlap herds of caribou and flocks of geese as the bears travel along the coast and move inland (Iles et al. 2013; L. J. Gormezano and R. F. Rockwell, unpubl. obs.). The increased co-occurrence of polar bears and the now plentiful caribou and snow geese facilitate opportunities for both predation as well as scavenging of kills made by other predators (e.g., wolves, Canis lupus, [Brook and Richardson 2002]; grizzly bears, Ursus arctos, [Rockwell et al. 2008]). Predation events on other waterfowl species during incubation or brood rearing on our study area (Table 1) and elsewhere (e.g., Madsen et al. 1998; Drent and Prop 2008) suggest that other avian species are similarly vulnerable.
Egg remains occurred in 4.6% of scats we collected along the coast, contrasting with Russell's study that reported no eggs (Russell 1975). Earlier observations had documented polar bears eating eggs as part of a varied diet (e.g., Harrington 1965; Pedersen 1966) or had reported them in the stomachs of harvested bears (pers. comm. to R. H. Russell 1975). Russell (1975) found egg remains in 5.0% of scats on the Twin Islands in James Bay, Ontario, but concluded that foraging on eggs was likely uncommon because polar bears were on the ice during the peak periods of hatch. With breakup occurring on average 22 days earlier, however, polar bears are arriving onshore sooner and are overlapping the incubation period of snow geese, common eiders, and other species of waterfowl (Rockwell and Gormezano 2009). Reports of polar bears consuming eggs of nesting waterfowl have increased across the polar bears' range (see Drent and Prop 2008; Smith et al. 2010). We also observed polar bears capturing adult birds (e.g., snow geese, Canada geese, common eiders) guarding their nests in addition to consuming their eggs. Consistent with our observations, we found that 25% of the scats with egg remains occurred in the same pile as the remains of adult snow geese.
Although the overall proportion of mammals in our scats has not changed substantially from Russell's study (24.6% vs. 32.1% of scats, respectively), we found caribou (above), more polar bear remains, and fewer rodent remains in our samples (Table 2). Assuming the rodent estimates in Russell (1975) are typical for the Cape Churchill area, the difference in rodents may be due either to our sampling occurring during 3- to 5-year cyclic fluctuations (Krebs and Myers 1974) or to declines in peak lemming abundance thought to be associated with warmer temperatures during fall freeze-up and subsequent high levels of precipitation into early winter that drive lemmings to higher ground where they are less protected through the harsh winter (Scott 1993).
The increased number of scats with polar bear remains relative to the 1960s (Table 2) is consistent with reported higher rates of cannibalism (i.e., intraspecific predation and/or scavenging). Several authors have speculated that because of earlier breakup of ice, nutritional stress could lead to increased intraspecific aggression and cannibalism (e.g., Taylor et al. 1985; Amstrup et al. 2006; Stirling et al. 2008). Recent observations of intraspecific attacks initiated by polar bears in poor condition support this suggestion (Lunn and Stenhouse 1985; Taylor et al. 1985), but many instances of healthy polar bears initiating similar attacks have also been reported (Taylor et al. 1985; Derocher and Wiig 1999; Dyck and Daley 2001; Stirling and Ross 2011). Furthermore, not all polar bears that are killed are consumed, suggesting that there may be other reasons for this behavior (Taylor et al. 1985; Derocher and Wiig 1999).
Different types of vegetation, particularly grasses and marine algae, were pervasive; occurring in 84.9% of polar bear scat piles and this is similar to observations across the circumpolar range of polar bears (Koettlitz 1898; Pedersen 1966; Russell 1975). Although the overall proportion of vegetation items has not changed since the 1960s (67% and 69%), the proportion of Lyme grass has increased while other grasses have decreased (Table 2). Like other predatory mammals, polar bears might consume vegetative roughage (e.g., grass stalks, marine algae, moss) as part of self-medicative efforts to reduce loads of worm parasites (Huffman 2003), to acquire a source of fiber to facilitate bowel movement (McKeown 1996) or to acquire nutrients that are lacking from animal sources. For example, polar bears preferentially consume the spikes of Lyme grass (Russell 1975; Lunn and Stirling 1985) that have protein-rich seed heads in early July through late August (Johnson 1987). Lyme grass has occurred along the entire coast of western Hudson Bay for many years (Jefferies et al. 2006) and unless polar bears are recently targeting it to fulfill a protein or other dietary need we can offer no firm explanation of its increased consumption. However, preliminary analyses of plant phenology on the Cape Churchill Peninsula (C. P. H. Mulder and R. F. Rockwell, unpubl. ms.) suggest that flowering and seed set is advancing although not as fast as sea ice dissolution. It is thus possible that polar bears are increasingly overlapping the seed heads much as snow goose eggs.
We also found a higher proportion of scats with mushrooms along the coastal portions of our study area than Russell (1975) found in the 1960s (Table 2). The two species we identified, Lycoperdon pyriforme and L. perlatum, occur from July through November along the entire western Hudson Bay coastline and thrive on driftwood that litters the coastline, fallen trees further inland, and soil substrates across the landscape (McKnight and McKnight 1998). Although Russell (1975) commented that mushrooms were typically found in low volumes (5–10%) with crowberries and suggested that they were consumed together at the same site, we found no patterns of co-occurrence of mushrooms with any other foods. Mushrooms were typically found in volumes of 10% or less, but we also found many (28.1% of scats with mushrooms) where mushrooms comprised 50% or more of a scat pile. There were four scats that contained only mushrooms, indicating that polar bears may consume them in large quantities when available, perhaps in attempt to acquire limiting micronutrients (e.g., Iversen et al. 2013).
The decrease in proportion of garbage in scats in the current diet may be due to marked changes in the availability of garbage both near the town of Churchill and in areas further east along the Hudson Bay coast. In 2005, the town of Churchill closed the landfill, which previously attracted numerous polar bears (Lunn and Stirling 1985). Garbage was subsequently secured from bears prior to recycling or removal from the area. Also, rules governing the securing and removal of waste from research camps, including Nester 1, from which Russell's Cape Churchill collections were based, became more stringent with the establishment of Wapusk National Park in 1996 (R. F. Rockwell, pers. obs.). Stored garbage depots were systematically removed from areas south of Cape Churchill and more effectively secured from polar bears in subsequent field seasons.
Our data indicate that polar bears are now foraging on increasingly abundant terrestrial prey such as caribou and snow geese and utilizing novel resources like eggs that have become newly available through climate-induced shifts in their onshore arrival. These observations combined with those of other studies and the diverse patterns of different foods in scats (Gormezano and Rockwell, in review) suggest that some polar bears are opportunistic omnivores. If this observed foraging renders some present or future benefit, it may be an example of “diet mixing” (ingestion of multiple species over an animal's lifetime or life cycle that differ qualitatively to the consumer) (Singer and Bernays 2003), a foraging strategy shared by many predators in Arctic ecosystems (Samelius and Alisauskas 1999; Elmhagen et al. 2000). This mode of foraging is similar to that observed in other bear species that are known to shift their diet regularly to exploit both seasonally (e.g., Persson et al. 2001) and newly available resources (Beckmann and Berger 2003) to meet their nutritional needs. In the closely related brown bear, dramatic differences in diet have been observed in response to local prey and vegetation abundance (e.g., Hilderbrand et al. 1999), competition (e.g., Gende and Quinn 2004), and environmental change (e.g., Rodríguez et al. 2007).
It is generally agreed that polar bears diverged from brown bears at least 600,000 years ago and evolved to survive in the specialized Arctic environment (Hailer et al. 2012; Cahill et al. 2013; Weber et al. 2013). One or more hybridization events have likely occurred since then, evidenced by brown bear mitochondrial DNA having introgressed into polar bear lines (Hailer et al. 2012). It has been suggested that such events may have helped polar bears persist through multiple interglacial warm phases (Edwards et al. 2011; Hailer et al. 2012). We suggest that the wide range of foraging behaviors observed for polar bears, like those present in brown bears, may reflect an inherent plasticity and shared genetic legacy that was likely retained over time (e.g., Agosta and Klemens 2008; Miller et al. 2012; Weber et al. 2013). Among those polar bears foraging, the shifts in the diet that have occurred (and are occurring) since Russell's (1975) study may be an innate plastic response to changing prey availability and exemplify the type of foraging behavior that these polar bears are capable of as climate change reduces their opportunities to hunt seals. Pending the outcome of current genetic analyses, however, it is yet unclear how many polar bears are exhibiting this behavior and thus the extent of any benefits that may be gleaned from it.
There is evidence that body mass and survival of at least some demographic classes of polar bears has declined coincident with the advancing date of breakup of Hudson Bay sea ice (e.g., Stirling and Parkinson 2006; Regehr et al. 2007). It is suggested that the declines are the result of the bears becoming increasingly nutritionally stressed and that this may, in turn, lead them to seek alternative food sources (Stirling and Parkinson 2006; Regehr et al. 2007). While possible, this seems unlikely to be the only cause of such terrestrial foraging because land-based hunting, scavenging, and grazing actually predate recorded climate-related changes (e.g., Pedersen 1966; Russell 1975).
Also, polar bears have switched between major prey items in the past when nutritional stress was likely not a causative factor. For example, Thiemann et al. (2008) found that polar bears switched their primary consumption from bearded to ringed seals when the abundance of the two species changed in western Hudson Bay. The switch was independent of the date of ice breakup and they concluded that polar bears are “… capable of opportunistically altering their foraging to take advantage of locally abundant prey, or to some degree compensating for a decline in a dominant prey species.” (Thiemann et al. 2008). Our observations on consumption of increasingly abundant caribou, snow geese, and their eggs are consistent with this assessment. Observations of polar bears coming ashore seeking eggs even while seals were still available on the ice (Madsen et al. 1998; Drent and Prop 2008) lend additional support to their prey switching abilities and general plasticity in foraging.
Current threats to the persistence of polar bears in western Hudson Bay are clear as the ice-free season expands, limiting polar bear access to seals on the ice (e.g., Stirling and Derocher 2012). However, with a history of adaptive foraging behavior and pursuit of novel prey across their Arctic habitat (e.g., Dyck and Romberg 2007; Smith et al. 2010), it is unlikely that polar bears will abstain from exploiting new terrestrial resources solely because they were ignored in the past in favor of more easily accessible marine prey. Some polar bears currently eat a variety of terrestrial animals and plants during the ice-free period, taking opportunistic advantage of abundant species. We suggest that research now focus on determining both the number of polar bears making this shift and the nutritional and energetic gains associated with this shifting terrestrial diet. Furthermore, these gains must be considered when modeling future polar bear survival. Shifts in diet composition, even for what may comprise a small fraction of the annual nutritional and energy budget may become increasingly important for some individuals in the population as ice conditions worsen (e.g., Dyck and Kebreab 2009; Rockwell and Gormezano 2009).
- Top of page
- Material and Methods
- Conflict of Interest
We thank N. Duncan and A. Rodriguez for help with bone and hair identification, and C. Dove for assistance and tutorials in feather identification. Quinoa, the detection dog, eagerly found our scat samples and made field work way more fun. He was assisted in the field by K. Burke, M. DiBrizzi, D. Koons, and C. Witte. We would also like to thank F. Baldwin, R. Brook, D. Hedman, C. Jonkel, S. Kearney, S. Kowalchuk, and K. Rebizant for additional contributions. M. Freeman, D. Koons, J. Lovvorn, J. Roth, and H. B. Underwood provided constructive criticism on an earlier draft of this work. Financial support for this work was provided primarily by the Hudson Bay Project, but also the American Museum of Natural History – Theodore Roosevelt Memorial Grant (#0655), Arctic Institute of North America – Grants-In-Aid, Churchill Northern Studies Centre – Northern Research Fund, City University of New York and Manitoba Conservation – Sustainable Development Innovations Fund (#27070). Logistical and in-kind support was provided by Calm Air Airlines, Great White Bear Tours, Praxair, Inc., Ruffwear, Inc., and Wapusk National Park. This study is dedicated to the memories of the late Malcolm Ramsay and Robert Jefferies, both of whom pondered the nature and worth of terrestrial foraging by polar bears.