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  • Research article
  • Open Access

Scavenging on a pulsed resource: quality matters for corvids but density for mammals

BMC EcologyBMC series – open, inclusive and trusted201717:22

https://doi.org/10.1186/s12898-017-0132-1

©  The Author(s) 2017

  • Received: 3 March 2017
  • Accepted: 8 June 2017
  • Published:

Abstract

Background

Human food subsidies can provide predictable food sources in large quantities for wildlife species worldwide. In the boreal forest of Fennoscandia, gut piles from moose (Alces alces) harvest provide a potentially important food source for a range of opportunistically scavenging predators. Increased populations of predators can negatively affect threatened or important game species. As a response to this, restrictions on field dressing of moose are under consideration in parts of Norway. However, there is a lack of research to how this resource is utilized. In this study, we used camera-trap data from 50 gut piles during 1043 monitoring days. We estimated depletion of gut piles separately for parts with high and low energy content, and used these results to scale up gut pile density in the study area. We identified scavenger species and analyzed the influences of gut pile quality and density on scavenging behavior of mammals and corvids (family Corvidae).

Results

Main scavengers were corvids and red fox (Vulpes vulpes). Parts with high energy content were rapidly consumed, mainly by corvids that were present at all gut piles shortly after the remains were left at the kill site. Corvid presence declined with days since harvest, reflecting reduction in gut pile quality over time independent of gut pile density. Mammals arrived 7–8 days later at the gut piles than corvids, and their presence depended only on gut pile density with a peak at intermediate densities. The decline at high gut pile densities suggest a saturation effect, which could explain accumulation of gut pile parts with low energy content.

Conclusions

This study shows that remains from moose harvest can potentially be an important food resource for scavengers, as it was utilized to a high degree by many species. This study gives novel insight into how energy content and density of resources affect scavenging patterns among functional groups of scavengers.

Keywords

  • Carrion ecology
  • Scavenging
  • Human subsidies
  • Pulsed resources
  • Gut piles
  • Scavenger community

Background

Human subsidies such as food waste, crop residuals, feeding stations for game species and carcass remains from hunting, are abundant in large quantities worldwide. Predictable Anthropogenic Food Subsidies (PAFS) are resources offered intentionally, or unintentionally, to wild animals by humans and are predictable in time and/or space [1]. PAFS can increase body condition, fecundity and survival of scavengers [2–7], and in the end lead to multiple changes of processes in the ecosystem. For example, predator species can increase in abundance through buffered temporal variability in food [8, 9], leading to altered predator–prey dynamics potentially affecting whole communities [1]. PAFS could also be negative for certain species when artificially increased populations disrupts the social system [10].

In temperate ecosystem, scavenging on remains from ungulate harvest are potentially important as PAFS [11–14]. A regulated harvest of ungulates and historical low numbers of large carnivores in Fennoscandia have resulted in large populations of ungulates, especially the moose (Alces alces) have shown an unprecedented increase the last 75 years [15, 16]. About 35,000 moose are annually harvested during a few weeks in September and October in Norway. Internal organs including lungs, intestines, liver and sometimes the heart are removed at the kill site and these gut piles dominate the amount of available moose carrion in autumn [17, 18]. Gut piles from moose are a predictable and high amplitude temporal resource pulse during a time when low temperatures reduce the proliferation of insects, bacteria and fungi on the remains [18–20]. Autumn is also a critical period for many carnivores and scavengers, especially for young individuals. Autumn mortality in juvenile corvids is high, [21], and starvation is an important mortality factor in juvenile raptors as goshawks (Accipiter gentilis) [22] and golden eagles (Aquila chrysaetos) [23]. Mortality in dispersing juvenile American martens (Martes americana) was related to body condition [24], and low food availability increase trapping vulnerability of the European pine marten (Martes martes) [25]. Hence, gut piles might increase juvenile survival of scavengers by increasing availability of food resources. In addition, adaptations by scavengers, e.g. storing of body fat or food caching may lead to prolonged effects of food pulses [26–30].

Gut piles from harvested moose at kill sites have recently become a conservation concern, and this artificial support of scavenging species can have negative impact on other species. For example, ground nesting birds may suffer increased nest predation as a consequence of increased densities of scavenging generalist predators [31–33]. In Scandinavia, the red fox (Vulpes vulpes) is of special concern, as it has been documented to reduce breeding success through nest and chick predation [32, 34] and as a threat to the arctic fox (Vulpes lagopus) through interference and resource competition [35]. An increasing number of landowners now enforces restrictions on field dressing of ungulates, but the potential effect of this management policy is unclear.

The aim of this study was to investigate scavenging patterns on the large quantities of gut piles from the moose harvest in Norway. We hypothesize that a wide range of facultative scavengers will use this human created resource, and that avian species will be the first to detect the remains. Firstly, we measured how the different species in the scavenger community utilize the resource by comparing the arrival time and group size of different species at gut piles. Secondly, we quantified the rate of gut pile depletion and the temporal change in gut pile density as an indication on the potential effects pulsed resource can have on the scavenging community [36, 37]. Thirdly, gut piles contains different tissues as fat, muscle and connective with varied energy content, which could be expected to influence foraging behavior [19, 38–41]. Therefore we evaluated how temporal variation in gut pile density and energy content influenced the foraging patterns of different functional groups of scavengers.

Methods

Study area

The study was conducted in an area of 65 km2 90–485 m.a.sl. within the Ogndal valley in central Norway (63.95 N–64.03 N, 11.76 E–11.97 E). At elevations below 165 m the geology is dominated by marine deposits, mostly agriculture land interspersed with commercially managed forest, mainly Norway spruce (Picea abies). The area above the marine deposits is dominated by coniferous forest (Norway spruce and Scots pine Pinus sylvestris) interspersed with bogs. Potential scavenging species are red fox, European badger (Meles meles), pine marten, golden eagle, white-tailed eagle (Haliaeetus albicilla), northern goshawk and corvid species. There is no obligate scavengers in Scandinavia. Ungulate present includes moose, roe deer (Capreolus capreolus), and occasional red deer (Cervus elaphus). Free ranging semi-domesticated reindeer (Rangifer tarandus) are usually present in the area from October to May. Eurasian lynx (Lynx lynx) populations were relatively low during the study period [42] while wolverine (Gulo gulo) and brown bear (Ursos arctos) were only sporadically registered within the area. Average monthly temperature varied between 3–5, 1–3 and −5 to 0 °C in October, November and December, respectively. Monthly precipitation ranged from 30 to 148 mm. Snow covered the ground periodically each winter and snow layer >25 cm was restricted to a few days.

The number of moose harvested in the study area was 61 in 2012, 62 in 2013 and 60 in 2014, resulting a pooled average of 0.94 moose/km2. Calves constituted 60% of the harvest. The hunting season was closed during 1 week at the peak rut to avoid disturbance. The first hunting period was starting at September 25th, and the second hunting period began October 10 and lasted to October 30 in 2012 and to November 14 in 2013 and 2014. Head, legs, hide and often the heart were brought out with the carcass, while gut piles, containing stomachs and intestines, including visceral fat, and other internal organs were usually left in the field. The lowest energy density of the gut piles is in the stomach tissue with ~0.5 kcal/g, about half of what is found in muscle and liver. Lungs have an intermediate energy density of ~0.85 kcal/g [43]. Highest energy density is found in fat (~9 kcal/g dry weight), however the energy density of fat tissue is lower, dependent on water content [44]. Estimated biomass of moose gut piles in our study area (rumen contents excluded; calculated as Wikenros et al. [18]) was higher (33 kg/km2) compared to the surrounding region (20 kg/km2 in the county of Nord-Trøndelag [17]).

Scavenging observations

Camera traps (Reconyx Hyperfire PC 900 in 2012 and Wingcam II TL in 2013/2014) were set up on 50 gut piles, totaling 1043 monitoring days, during the hunting season in 2012–2014 (Fig. 1). Cameras were set up by the hunters before they left the dressing site (1 camera per site) and were placed 4–6 m away from the gut pile and 1−1.5 m above ground. The cameras were programmed to take a picture every 10 min and also when triggered by the motion sensor, with a 2 min delay between triggers to maintain battery and memory card capacity. Cameras were removed when only the rumen contents remained and occasionally smaller pieces of the intestines. All pictures were examined and the number of individuals present of each species in each picture was registered. To estimate daily energetic quality of the remains of the gut pile, we visually evaluated the first picture of each day. Gut piles were then categorized into two classes: (1) high energy content (parts with high energy density like fat, liver and lungs still present), (2) low energy content (only stomach and/or intestines present, including rumen content).
Fig. 1
Fig. 1

Location of gut piles with camera-traps 2012–2014. Map showing the location of moose gut piles with camera-traps, N = 50 out of totally 183 moose killed within the study area. Locations of moose gut piles without camera-traps were not recorded. Grey show agricultural areas. Lines are roads

Gut pile depletion curves and gut pile density

Kaplan–Meier curves were used to estimate gut pile depletion for class 1 and 2 separately due to different usage by different scavengers. Right censored events occurred when presence of high energy parts were uncertain due to snow cover or when the gut pile was moved so that only low energy parts were visible on pictures, this was included as a right-censored event in the Kaplan–Meier analyses for class 1. Class 2 was categorized as depleted when only rumen content was left.

To evaluate if depletion varied between years or hunting periods, we compared the depletion rates by using Cox proportional hazard models. We tested for the difference in depletion rate between class 1 and 2 in different years. There were no significant differences between years for either class (coxph class 1; year 2012 v 2013: z = 1.083, p = 0.279, year 2012 v 2014: z = −0.843, p = 0.399, coxph class 2; year 2012 v 2013: z = −0.043, p = 0.966, year 2012 v 2014: z = −0.819, p = 0.413), and data were pooled for all years. We further compared depletion rates between the early (Sep 25–Oct 1) and late (Oct 10–Nov 14) hunting period. All analyses were done in R [45] with the package survival [46]. The function cox.zph was used to evaluate the assumptions of constant proportional hazard models.

Secondly, we calculated gut pile density throughout the hunting season (all years pooled). Separate estimates were calculated for the parts with high (class 1) and low (class 2) energy content. The change in density of the two classes was calculated by reducing the accumulated gut piles from harvest with the Kaplan–Meier depletion estimates for each day of the hunting season.

Scavenging patterns

For each scavenging species, we estimated the proportion of gut piles visited, the mean number of days with visits and the maximum number of individuals recorded at one time for each day. Maximum number of individuals was used to investigate variation in aggregation of individuals between species.

To analyze if daily presence of scavengers responded primarily to days since the moose was killed or to density of gut piles we used binomial generalised linear mixed-effects models (GLMM; in R-package lme4 [47]). We analysed the daily probability (N = 1043) for each scavenging species to visit gut piles (0 or 1, where 1 is defined as ≥1 pictures including the species). We pooled scavenging species into three functional groups: (1) mammals, (2) large corvids [magpie (Pica pica), hooded crow (Corvus cornix) and common raven (Corvus corax)] and (3) small corvids [Eurasian jay (Garrulus glandarius) and Siberian jay (Perisoreus infaustus)] for separate analyses. Raptors were not included in this analysis due to small sample sizes. We included gut pile ID (N = 50), nested under year (N = 3), as random intercept in the model to account for possible variation in scavenger densities between the years of the study and for repeated measures at the same gut pile within a single year. As gut pile densities were not independent of days since harvest we did not combine the two variables in the same model but rather viewed them as competing models, evaluated by AICc values. The effect of age and density was evaluated through a second order polynomial, and AIC was used to determine if the non-linear (second order) was better than the linear (first order). Gut piles were removed from the analyses when only rumen content remained.

Results

The gut pile parts with high energy content (class 1) were depleted at significantly higher rate compared to parts with low energy content (class 2) (coxph: z = −7.504, p < 0.001). Already 10 days after the moose were killed, only 15% of the gut piles contained parts with high energy content, although 90% still had remains. Ten percent were depleted (i.e. only rumen content left) (Fig. 2). There was no significant difference (coxph: z = 1.333, p = 0.183) in depletion of the class 2 parts between the hunting periods. Depletion of the class 1 part tended to go faster in the second hunting period, but differences could not be estimated because coxph model assumptions were violated.
Fig. 2
Fig. 2

Depletion of gut pile parts with high and low energy content. Grey high energy content, black low energy content. Dashed lines show 95% confidence intervals

Density of gut piles with high energy content parts remaining was highest during the first hunting period, whereas low energy parts lasted longer and at higher density (Fig. 3).
Fig. 3
Fig. 3

Temporal development of the availability of gut pile parts with high and low energy content. Years are pooled

Scavenging patterns

In total, 15 species scavenged on the gut piles. Magpie, Eurasian jay, hooded crow and common raven were the most common avian scavengers while red fox was the most common mammal (Table 1). In addition to species in Table 1, arctic fox, American mink (Neovison vison) and domestic dog (Canis lupus familiarizes) were registered scavenging on one gut pile each. Pine martens only visited a quarter of the available gut piles but were often observed many days to the same gut pile (Table 1). The same pattern (high species revisiting rate) was also observed for several corvids species. Crows, and partly ravens and magpie, were the only species aggregating in groups, up to 27, 16 and 12 individuals were recorded at one time respectively. Jays, raptors and mammals were usually only present one individual at a time (Table 1). Interestingly, even domestic cats (Felis catus) visited some of the gut piles, and returned frequently to the same gut pile.
Table 1

Species documented on gut piles (N = 50) from moose harvest in Central Norway in 2012–2014

Speciesa

Latin name

% visited

Days present

Max no. ind.

Birds

 Magpie

Pica pica

100

10.9 (7.1)

3 (1–12)

 Eurasian jay

Garrulus glandarius

90 (82–96)

7.6 (7.9)

1 (1–5)

 Hooded crow

Corvus cornix

90 (82–94)

5.2 (3.2)

8 (1–27)

 Raven

Corvus corax

70 (55–81)

2.8 (2.1)

3 (1–16)

 Siberian jay

Perisoreus infaustus

10 (6–18)

2.6 (0.9)

1 (1–2)

 White-tailed eagle

Haliaeetus albicilla

20 (17–27)

2.6 (2.3)

1 (1–2)

 Golden eagle

Aquila chrysaetos

16 (9–27)

1.4 (0.5)

1 (1–2)

 Goshawk

Accipiter gentilis

6 (0–19)

2.3 (1.3)

1

Mammals

 Red fox

Vulpes vulpes

68 (45–78)

4.0 (2.6)

1 (1–3)

 Badger

Meles meles

40 (35–55)

4.4 (3.5)

1 (1–2)

 Pine marten

Martes martes

24 (6–35)

7.5 (4.9)

1 (1–2)

 Domestic cat

Felis catus

6 (0–13)

9.0 (4.6)

1

Proportion of gut piles visited (% visited) is presented with all years pooled and range for the different years, while numbers of days with visits per gut pile (days present) is presented as mean (±SD) and daily maximum number of individuals recorded at one time (Max no. ind) as the median and range (min–max)

aArctic fox (Vulpes lagopus), American mink (Nivea vision) and domestic dog (Canis lupus familiaris) were registered scavenging on one gut pile each

Scavenging birds (raptors, large corvids and small corvids) arrived 5–8 days earlier at gut piles than mammals did (ANOVA: F3,258 = 30.5, p < 0.001), while there was no difference in arrival time between groups of birds (eagle sp.; TukeysHSD: p = 0.08–0.4; Fig. 4). The probability of mammals to visit gut piles was best explained by density of gut piles, showing a strong non-linear response peaking at around median densities (Fig. 5; β1 = −3.3, SE = 3.7; β2 = −19.0, SE = 3.8). Gut pile age had no effect on daily visits by mammals (ΔAICc = 29.9, c.f. Null model: ΔAICc = 29.5). There were some variance in random intercept between gut piles (1.4, 1.2 SD) and a tendency for variation between years (0.06, 0.24 SD).
Fig. 4
Fig. 4

Arrival time at gut piles from moose harvest (days after harvest) by different scavenger species. Based on 50 harvested moose in central Norway in 2012–2014. Box plots show median (bold horizontal lines), interquartile range (box), and range up to 1.5 times interquartile range (bars)

Fig. 5
Fig. 5

Probability of scavenging mammals to visit gut piles in relation to gut pile density. Gut piles remaining after field dressing of hunted moose in Central Norway in 2012–2014

In contrast, the probability of both small and large corvids to visit gut piles was only influenced by days since harvest. Model with gut pile density increased AICc by 172 and 108 for small and large corvids respectively. The daily presence of small corvids decreased rapidly (Fig. 6; β1 = −46, SE = 4.2; β2 = 29, SE = 3.1), while the daily presence of large corvids decreased in a linear manner and more gradually with increasing age of the gut pile (non-linear ΔAICc = 1.4, β = −0.09, SE = 0.009).
Fig. 6
Fig. 6

Probability of scavenging corvids to visit gut piles in relation to gut pile age. Gut piles remaining after field dressing of hunted moose in Central Norway in 2012–2014

The general probability of visits varied between gut piles (4.3, SD 2.1 for small corvids and 1.3, 1.2 SD for large) but there was no variance between years thus this variable was removed from the analyses.

Discussion

We have shown that gut piles from moose hunt are rapidly detected, and parts with high energy content are removed in less than 3 weeks. Gut piles constitute a large amount of food and are likely to have a positive influence on several of the scavenger populations. This pulse of food increased resource availability for scavenging species during a 3-month period. It seems safe to conclude that moose gut piles fit the PAFS concept.

In this study, corvids, red fox, pine marten and badger were the main scavenger species. Northern ecosystems lack obligate scavengers and the low abundances of large scavenging carnivores opens up for smaller carnivores [13, 18, 48, 49]. The high moose harvest in Scandinavia is one, if not the most, important food resource for scavengers, making it unique compared to boreal areas in other parts of the world. There has been high moose harvest for about 40 years, and the harvest periods do not change much between years. We believe that the scavenging species in this ecosystem have adapted to this resource, and it may be an important food buffer potentially reducing juvenile mortality [21–25, 50]. The high energy content of the visceral fat in the gut piles is easily converted to body fat storage in mammals, reducing the risk of starvation during winter bottle-necks [30]. Alternatively, the remains can be cached and utilized later [26–29, 51–53].

In our study, gut pile parts with high energy content were utilized rapidly, primarily by corvids. Corvids were present at all gut piles shortly after harvest, and had access to all parts of the gut pile. Corvid presence declined with time probably reflecting reduction in gut pile quality. Optimal foraging theory predicts that only the energy rich parts should be utilized before moving to a new patch if available, as observed in both predators and scavengers [38, 40, 41]. Our results suggest that corvids move to a more recent harvest site nearby rather than staying and feeding on remains of poorer quality. Stomachs and intestines have high content of connective tissue, and corvids might have limited ability to digest collagen compared to mammal scavengers [54]. Dependent on size, corvid species might also be restricted by limited beak strength [55]. This also reflects the benefits of direct access to harvest remains for birds compared to whole carrions where access to parts with high energy content may require opening by larger species [56].

The late arrival of mammals seems to limit their access to parts with high energy content, already consumed by avian scavengers. Mammals responded primarily to gut pile density and daily presence peaked at intermediate densities. Reduced mammal presence at high gut pile densities might indicate a saturation effect, comparable to seed predation during masting events [57]. On the other hand, accumulation of gut pile parts with low energy content lead to longer resource pulse duration, with possible prolonged positive effects on mammal scavengers [37]. Hence, even a reduction in gut pile density may reduce the potential positive effects on the density of mammalian scavengers. Nonetheless, corvids probably have an important ecological impact in limiting gut pile availability to other scavengers through resource competition [58]. Hence, lower corvid abundance may benefit mammalian scavengers. Large scavenging predators (wolverine, brown bear) were only present sporadically in our study area and were not observed at any of the gut piles. This contrasts to comparable studies on autumn pulses of gut piles, where bear species were the main mammal scavengers [12, 59]. Red fox is the main mammal scavenger in other studies from northern Europe [18, 19, 48], and in studies of human provided subsidies in general [60].

Direct negative impacts of scavenging on gut piles from harvested moose is potential lead poisoning arising from bullet remains [59, 61]. An estimated deposit of 182 kg of lead in moose gut piles yearly in Scandinavia could be a management concern regarding scavenging species [62]. For example, golden eagles show an increase in blood lead levels during the moose hunting season, and might experience increased mortality both through lethal and sub lethal doses of lead [63]. Legislation banning the use of lead ammunition or forcing removal of gut piles would effectively reduce the risk of lead poisoning. However, the latter would in addition result in a radical reduction regarding food abundance for scavenging species, possibly with larger ecosystem impact [64, 65]. In addition, anthropogenic resources can alter wildlife–pathogen dynamics and create opportunities for cross-species transmission of pathogens [66]. The protozoan parasites Toxoplasmoso gondii, Giardia spp. and Cryptosporidium spp. found in moose and other cervids [67, 68] can infect several scavenger species [69–71]. On the other hand, red fox use of anthropogenic food sources may indirectly reduce the prevalence of the zoonotic tapeworm Echinococcus multilocularis in foxes if it results in reduced predation on small rodents, the intermediate hosts of the parasite [72, 73]. Interestingly, prevalence of E. multilocularis in small rodents increases during autumn and winter [74], the period gut piles are present. However, possible effects of gut piles on wildlife–pathogen dynamics are probably diverse [66], but should be considered.

Conclusions

In this study, we show that gut piles left at the kill site after moose harvest are an intensively used food source by a range of scavenging birds and mammals during autumn and early winter. This study also provides novel insight into how quality and density of carrion affect scavenging patterns among functional groups of scavengers. Enforcing a removal of gut piles by hunters will reduce food supply in a critical period for several scavenging species. This may have direct negatively effects on several scavenging species utilizing this predictable food resource, but it is difficult to predict the long-term effect on the relative abundance of scavengers. It could potentially reduce less wanted species as corvids and red fox, but also impact eagles and wolverines. Reducing the amount of gut piles in the landscape would reduce the potential risk of lead poisoning [59, 61], but could also be mitigated by using lead free bullets. However, to what extend this pulsed resource is important for the overall survival, reproduction and population dynamics of both scavenging and potential prey species needs further investigation. Ignoring these PAFS would make the understanding of the food web structure and dynamics in the boreal forest difficult.

Declarations

Authors’ contributions

GG conceived the study, participated in its design, performed statistical analyses and drafted the manuscript. TW participated in the design of the study and helped drafting the manuscript. JM performed statistical analyses and helped drafting the manuscript. PFM helped drafting the manuscript and collecting data. BRH collected data. All authors read and approved the final manuscript.

Acknowledgements

We thank students and local hunters for their help in data collection.

Competing interests

The authors declare that they have no competing interests.

Availability of data and materials

The datasets used and analyzed during the current study are available from the corresponding author on reasonable request.

Funding

This study was supported by the Norwegian Environment Agency. The funding body had no role in the design of the study and collection, analysis, and interpretation of data or in writing the manuscript.

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Authors’ Affiliations

(1)
Nord University, 8049 Bodø, Norway
(2)
Norwegian Institute for Nature Research (NINA), 7484 Trondheim, Norway
(3)
Inland Norway University of Applied Sciences, 2418 Elverum, Norway

References

  1. Oro D, Genovart M, Tavecchia G, Fowler MS, Martínez-Abraín A. Ecological and evolutionary implications of food subsidies from humans. Ecol Lett. 2013;16:1501–14.View ArticlePubMedGoogle Scholar
  2. Bino G, Dolev A, Yosha D, Guter A, King R, Saltz D, Kark S. Abrupt spatial and numerical responses of overabundant foxes to a reduction in anthropogenic resources. J Appl Ecol. 2010;47:1262–71.View ArticleGoogle Scholar
  3. Pons J-M, Migot P. Life-history strategy of the herring gull: changes in survival and fecundity in a population subjected to various feeding conditions. J Anim Ecol. 1995;64(5):592–9.View ArticleGoogle Scholar
  4. Steigerwald EC, Igual JM, Payo-Payo A, Tavecchia G. Effects of decreased anthropogenic food availability on an opportunistic gull: evidence for a size-mediated response in breeding females. Ibis. 2015;157:439–48.View ArticleGoogle Scholar
  5. Tixier P, Authier M, Gasco N, Guinet C. Influence of artificial food provisioning from fisheries on killer whale reproductive output. Anim Conserv. 2015;18:207–18.View ArticleGoogle Scholar
  6. Oro D, Margalida A, Carrete M, Heredia R, Donázar JA. Testing the goodness of supplementary feeding to enhance population viability in an endangered vulture. PLoS ONE. 2009;3:e4084.View ArticleGoogle Scholar
  7. Margalida A, Colomer MA, Oro D. Man-induced activities modify demographic parameters in a long-lived species: effects of poisoning and health policies. Ecol Appl. 2014;24:436–44.View ArticlePubMedGoogle Scholar
  8. Martínez-Abraín A, Tavecchia G, Regan HM, Jiménez J, Surroca M, Oro D. Effects of wind farms and food scarcity on a large scavenging bird species following an epidemic of bovine spongiform encephalopathy. J Appl Ecol. 2012;49:109–17.View ArticleGoogle Scholar
  9. Ruffino L, Russell J, Vidal E. Anthropogenic subsidies mitigate environmental variability for insular rodents. Oecologia. 2013;172:737–49.View ArticlePubMedGoogle Scholar
  10. Carrete M, Donazar JA, Margalida A. Density-dependent productivity depression in pyrenean bearded vultures: implications for conservation. Ecol Appl. 2006;16:1674–82.View ArticlePubMedGoogle Scholar
  11. Haroldson MA, Schwartz CC, Cherry S, Moody DS. Possible effects of elk harvest on fall distribution of grizzly bears in the Greater Yellowstone Ecosystem. J Wildl Manag. 2004;68:129–37.View ArticleGoogle Scholar
  12. Lafferty DJR, Loman ZG, White KS, Morzillo AT, Belant JL. Moose (Alces alces) hunters subsidize the scavenger community in Alaska. Polar Biol. 2015;39:1–9.Google Scholar
  13. Mateo-Tomás P, Olea PP, Moleón M, Vicente J, Botella F, Selva N, Viñuela J, Sánchez-Zapata JA. From regional to global patterns in vertebrate scavenger communities subsidized by big game hunting. Divers Distrib. 2015;21(8):913–24.View ArticleGoogle Scholar
  14. Wilmers CC, Stahler DR, Crabtree RL, Smith DW, Getz WM. Resource dispersion and consumer dominance: scavenging at wolf- and hunter-killed carcasses in Greater Yellowstone, USA. Ecol Lett. 2003;6:996–1003.View ArticleGoogle Scholar
  15. Lavsund S, Nygrén T, Solberg EJ. Status of moose populations and challenges to moose management in Fennoscandia. Alces. 2003;39:109–30.Google Scholar
  16. Selås V, Vik JO. Possible impact of snow depth and ungulate carcasses on red fox (Vulpes vulpes) populations in Norway, 1897–1976. J Zool. 2006;269:299–308.View ArticleGoogle Scholar
  17. Hagen BR. Estimating ungulate carrion biomass and possible ecological effects on red fox (Vulpes vulpes) in central Norway. Master Thesis. Hedmark University College; 2014.Google Scholar
  18. Wikenros C, Sand H, Ahlqvist P, Liberg O. Biomass flow and scavengers use of carcasses after re-colonization of an apex predator. PLoS ONE. 2013;8:e77373.View ArticlePubMedPubMed CentralGoogle Scholar
  19. Selva N, Jędrzejewska B, Jędrzejewski W, Wajrak A. Factors affecting carcass use by a guild of scavengers in European temperate woodland. Can J Zool. 2005;83:1590–601.View ArticleGoogle Scholar
  20. DeVault TL, Rhodes JOE, Shivik JA. Scavenging by vertebrates: behavioral, ecological, and evolutionary perspectives on an important energy transfer pathway in terrestrial ecosystems. Oikos. 2003;102:225–34.View ArticleGoogle Scholar
  21. Holyoak D. Movements and mortality of corvidae. Bird Study. 1971;18:97–106.View ArticleGoogle Scholar
  22. Kenward RE, Marcström V, Karlbom M. Demographic estimates from radio-tagging: models of age-specific survival and breeding in the goshawk. J Anim Ecol. 1999;68:1020–33.View ArticleGoogle Scholar
  23. McIntyre CL, Collopy MW, Lindberg MS. Survival probability and mortality of migratory juvenile golden eagles from interior alaska. J Wildl Manag. 2006;70:717–22.View ArticleGoogle Scholar
  24. Johnson CA, Fryxell JM, Thompson ID, Baker JA. Mortality risk increases with natal dispersal distance in American martens. Proc R Soc Lond B: Biol Sci. 2009;276:3361–7.View ArticleGoogle Scholar
  25. Helldin JO. Diet, body condition, and reproduction of Eurasian pine martens Martes martes during cycles in microtine density. Ecography. 1999;22:324.View ArticleGoogle Scholar
  26. Fjeld PE, Sonerud GA. Food caching, cache recovery, and the use of an egg shell dump in Hooded Crows Corvus corone cornix. Ornis Scand (Scand J Ornithol). 1988;19:268–74.View ArticleGoogle Scholar
  27. Legg EW, Clayton NS. Eurasian jays (Garrulus glandarius) conceal caches from onlookers. Anim Cogn. 2014;17:1223–6.View ArticlePubMedPubMed CentralGoogle Scholar
  28. Heinrich B, Pepper J. Influence of competitors on caching behaviour in the common raven, Corvus corax. Anim Behav. 1998;56:1083–90.View ArticlePubMedGoogle Scholar
  29. Macdonald DW. Food caching by red foxes and some other carnivores. Z Tierpsychol. 1976;42:170–85.View ArticlePubMedGoogle Scholar
  30. Kowalczyk R, Jȩdrzejewska B, Zalewski A. Annual and circadian activity patterns of badgers (Meles meles) in Białowieża Primeval Forest (eastern Poland) compared with other Palaearctic populations. J Biogeogr. 2003;30:463–72.View ArticleGoogle Scholar
  31. Fletcher K, Aebischer NJ, Baines D, Foster R, Hoodless AN. Changes in breeding success and abundance of ground-nesting moorland birds in relation to the experimental deployment of legal predator control. J Appl Ecol. 2010;47:263–72.View ArticleGoogle Scholar
  32. Jahren T, Storaas T, Willebrand T, Fossland Moa P, Hagen B-R. Declining reproductive output in capercaillie and black grouse—16 countries and 80 years. Anim Biol. 2016;66:363–400.View ArticleGoogle Scholar
  33. Rickenbach O, Grueebler MU, Schaub M, Koller A, Naef-Daenzer B, Schifferli L. Exclusion of ground predators improves Northern Lapwing Vanellus vanellus chick survival. Ibis. 2011;153:531–42.View ArticleGoogle Scholar
  34. Marcstrom V, Kenward RE, Engren E. The impact of predation on boreal tetraonids during vole cycles: an experimental study. J Anim Ecol. 1988;57:859–72.View ArticleGoogle Scholar
  35. Hamel S, Killengreen ST, Henden JA, Yoccoz NG, Ims RA. Disentangling the importance of interspecific competition, food availability, and habitat in species occupancy: recolonization of the endangered Fennoscandian arctic fox. Biol Conserv. 2013;160:114–20.View ArticleGoogle Scholar
  36. Holt RD. Theoretical perspectives on resource pulses. Ecology. 2008;89:671–81.View ArticlePubMedGoogle Scholar
  37. Yang LH, Edwards KF, Byrnes JE, Bastow JL, Wright AN, Spence KO. A meta-analysis of resource pulse–consumer interactions. Ecol Monogr. 2010;80:125–51.View ArticleGoogle Scholar
  38. Darimont CT, Reimchen TE, Paquet PC. Foraging behaviour by gray wolves on salmon streams in coastal British Columbia. Can J Zool. 2003;81:349–53.View ArticleGoogle Scholar
  39. Reimchen TE. Some ecological and evolutionary aspects of bear–salmon interactions in coastal British Columbia. Can J Zool. 2000;78:448–57.View ArticleGoogle Scholar
  40. Shardlow TF. Activity, behaviour, and rates of use of Pacific salmon carcasses by large vertebrate scavengers. In: Canadian technical report of fisheries and aquatic sciences. 2013:p. 44.Google Scholar
  41. Knarrum V, Sorensen OJ, Eggen T, Kvam T, Opseth O, Overskaug K, Eidsmo A. Brown bear predation on domestic sheep in central Norway. Ursus. 2006;17:67–74.View ArticleGoogle Scholar
  42. Brøseth H, Tovmo M, Nilsen, EB. Antall familiegrupper, bestandsestimat og bestandsutvikling for gaupe i Norge i 2015. NINA Rapport 2015.Google Scholar
  43. Sundli JO. Slakteavfall fra storviltjakt: småviltpredatorenes næringsgrunnlag? Basert på en analyse av slakteavfall fra elgjakt (In Norwegian). In: Høgskolen i Hedmark avd. Evenstad; 1993.Google Scholar
  44. Robbins CT. Wildlife feeding and nutrition. 2nd ed. San Diego: Academic Press; 1993.Google Scholar
  45. R Core Team. R: A language and environment for statistical computing. R Foundation for Statistical Computing, Vienna, Austria; 2013. http://www.R-project.org/. Accessed 13 June 2017
  46. Therneau T. A Package for Survival Analysis in S. version 2.38; 2015. https://CRAN.R-project.org/package=survival. Accessed 13 June 2017
  47. Bates D, Maechler M, Bolker B, Walker S. Fitting linear mixed-effects models using lme4. J Stat Softw. 2015;67:1–48.View ArticleGoogle Scholar
  48. Killengreen ST, Strømseng E, Yoccoz NG, Ims RA. How ecological neighbourhoods influence the structure of the scavenger guild in low arctic tundra. Divers Distrib. 2012;18:563–74.View ArticleGoogle Scholar
  49. Scholten J. Comparing behavior and species diversity of scavengers between two areas with different density of brown bears. In: University of applied sciences, HAS Den Bosch; 2012.Google Scholar
  50. Bevanger K, Lindström ER. Distributional history of the European badger Meles meles in Scandinavia during the 20th century. Ann Zool Fennici. 1995;32:5.Google Scholar
  51. Helldin JO. Seasonal diet of pine marten Martes martes in southern boreal Sweden. Acta Theriol. 2000;45:409–20.View ArticleGoogle Scholar
  52. Henry JD. Red fox: the catlike canine. Smithsonian Institution; 2013.Google Scholar
  53. Sklepkovych BO, Montevecchi WA. Food availability and food hoarding behaviour by red and arctic foxes. Arctic. 1996;49:228–34.View ArticleGoogle Scholar
  54. Karasov WH, Douglas AE. Comparative digestive physiology. Compr Physiol. 2013;3:741–83.PubMedPubMed CentralGoogle Scholar
  55. Moreno-Opo R, Trujillano A, Margalida A. Behavioral coexistence and feeding efficiency drive niche partitioning in European avian scavengers. Behav Ecol. 2016;27:1041–52.View ArticleGoogle Scholar
  56. Selva N, Jedrzejewska B, Jedrzejewski W, Wajrak A. Scavenging on European bison carcasses in Bialowieza primeval forest (eastern Poland). Ecoscience. 2003;10:303–11.View ArticleGoogle Scholar
  57. Zong C, Wauters LA, Van Dongen S, Mari V, Romeo C, Martinoli A, Preatoni D, Tosi G. Annual variation in predation and dispersal of Arolla pine (Pinus cembra L.) seeds by Eurasian red squirrels and other seed-eaters. For Ecol Manag. 2010;260:587–94.View ArticleGoogle Scholar
  58. Inger R, Per E, Cox DTC, Gaston KJ. Key role in ecosystem functioning of scavengers reliant on a single common species. Sci Rep. 2016;6:29641.View ArticlePubMedPubMed CentralGoogle Scholar
  59. Legagneux P, Suffice P, Messier J-S, Lelievre F, Tremblay JA, Maisonneuve C, Saint-Louis R, Bêty J. High risk of lead contamination for scavengers in an area with high moose hunting success. PLoS ONE. 2014;9:e111546.View ArticlePubMedPubMed CentralGoogle Scholar
  60. Newsome TM, Dellinger JA, Pavey CR, Ripple WJ, Shores CR, Wirsing AJ, Dickman CR. The ecological effects of providing resource subsidies to predators. Glob Ecol Biogeogr. 2015;24:1–11.View ArticleGoogle Scholar
  61. Finkelstein ME, Doak DF, George D, Burnett J, Brandt J, Church M, Grantham J, Smith DR. Lead poisoning and the deceptive recovery of the critically endangered California condor. Proc Natl Acad Sci. 2012;109:11449–54.View ArticlePubMedPubMed CentralGoogle Scholar
  62. Stokke S, Brainerd S, Arnemo JM. Metal deposition of copper and lead bullets in moose harvested in Fennoscandia. Wildl Soc Bull. 2017;41:98–106.View ArticleGoogle Scholar
  63. Ecke F, Singh NJ, Arnemo JM, Bignert A, Helander B, Berglund ÅMM, Borg H, Bröjer C, Holm K, Lanzone M, et al. Sublethal lead exposure alters movement behavior in free-ranging golden eagles. Environ Sci Technol. 2017;51(10):5729–36.View ArticlePubMedGoogle Scholar
  64. Cortés-Avizanda A, Colomer MÀ, Margalida A, Ceballos O, Donázar JA. Modeling the consequences of the demise and potential recovery of a keystone-species: wild rabbits and avian scavengers in Mediterranean landscapes. Sci Rep. 2015;5:17033.View ArticlePubMedPubMed CentralGoogle Scholar
  65. Margalida A, Colomer MA. Modelling the effects of sanitary policies on European vulture conservation. Sci Rep. 2012;2:753.View ArticlePubMedPubMed CentralGoogle Scholar
  66. Becker DJ, Streicker DG, Altizer S. Linking anthropogenic resources to wildlife–pathogen dynamics: a review and meta-analysis. Ecol Lett. 2015;18:483–95.View ArticlePubMedPubMed CentralGoogle Scholar
  67. Hamnes IS, Gjerde B, Robertson L, Vikøren T, Handeland K. Prevalence of Cryptosporidium and Giardia in free-ranging wild cervids in Norway. Vet Parasitol. 2006;141:30–41.View ArticlePubMedGoogle Scholar
  68. Vikøren T, Tharaldsen J, Fredriksen B, Handeland K. Prevalence of Toxoplasma gondii antibodies in wild red deer, roe deer, moose, and reindeer from Norway. Vet Parasitol. 2004;120:159–69.View ArticlePubMedGoogle Scholar
  69. Dubey JP. A review of toxoplasmosis in wild birds. Vet Parasitol. 2002;106:121–53.View ArticlePubMedGoogle Scholar
  70. Lopes AP, Sargo R, Rodrigues M, Cardoso L. High seroprevalence of antibodies to Toxoplasma gondii in wild animals from Portugal. Parasitol Res. 2011;108:1163–9.View ArticlePubMedGoogle Scholar
  71. Majewska AC, Graczyk TK, Slodkowicz-Kowalska A, Tamang L, Jedrzejewski S, Zduniak P, Solarczyk P, Nowosad A, Nowosad P. The role of free-ranging, captive, and domestic birds of Western Poland in environmental contamination with Cryptosporidium parvum oocysts and Giardia lamblia cysts. Parasitol Res. 2009;104:1093–9.View ArticlePubMedGoogle Scholar
  72. Hegglin D, Bontadina F, Contesse P, Gloor S, Deplazes P. Plasticity of predation behaviour as a putative driving force for parasite life-cycle dynamics: the case of urban foxes and Echinococcus multilocularis tapeworm. Funct Ecol. 2007;21:552–60.View ArticleGoogle Scholar
  73. Robardet E, Giraudoux P, Caillot C, Boue F, Cliquet F, Augot D, Barrat J. Infection of foxes by Echinococcocus multilocularis in urban and suburban areas of Nancy, France: influence of feeding habits and environment. Parasite. 2008;15:77–85.View ArticlePubMedGoogle Scholar
  74. Liccioli S, Bialowas C, Ruckstuhl KE, Massolo A. feeding ecology informs parasite epidemiology: prey selection modulates encounter rate with Echinococcus multilocularis in urban coyotes. PLoS ONE. 2015;10:e0121646.View ArticlePubMedPubMed CentralGoogle Scholar

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