Translator Disclaimer
16 December 2010 Stable isotopes evaluate exploitation of anthropogenic foods by the endangered San Joaquin kit fox (Vulpes macrotis mutica)
Author Affiliations +
Abstract

The unprecedented rate of urbanization over the past several decades is a major concern for conservation globally and has given rise to the multidisciplinary field of urban ecology. This field explores the direct and indirect effects of human activities on food-web dynamics, community structure, and animal behavior in highly modified urban ecosystems. Urban ecosystems are typically characterized by reduced species diversity but increased abundance of a few species able to exploit anthropogenic food sources. For many urban mammalian and avian species direct resource subsidization is difficult to assess using traditional means such as scat analysis. Here we show how stable isotope analysis can be used to assess the exploitation of anthropogenic foods in an endangered carnivore, the San Joaquin kit fox (Vulpes macrotis mutica) inhabiting the southern San Joaquin Valley in California. Examination of carbon (δ13C) and nitrogen (δ15N) isotope data shows that kit foxes living in urban Bakersfield, California, extensively exploit anthropogenic foods, which sharply contrasts with dietary data derived from scat analysis. Urban kit foxes had significantly higher δ13C and lower δ15N values than foxes from adjacent nonurban areas and had similar isotope values as Bakersfield human residents, which suggests a shared food source. In contrast, examination of isotopic data for nonurban kit foxes shows that they largely consume the most abundant natural prey species found in their scats. Stable isotope analysis offers a rapid and cost-effective means of evaluating the degree to which urban wildlife populations exploit anthropogenic foods in areas where native C4 vegetation is relatively uncommon or absent, important in assessing the direct impacts of human activities on food-web dynamics in urban ecosystems. We anticipate that the isotopic gradients used here will be useful in assessing the exploitation of anthropogenic foods in other urban wildlife populations.

Urban and suburban sprawl has resulted in increasing interactions among humans and wildlife populations globally. The study of such interactions has led recently to the creation of the multidisciplinary field urban ecology, in which ecologists often collaborate with anthropologists, geographers, and conservation biologists to develop a greater understanding of ecological and evolutionary processes in highly dynamic urban ecosystems (Alberti et al. 2003; Faeth et al. 2005; Grimm et al. 2008; Shochat et al. 2006). Certain animal species have adapted to human-dominated habitats well and benefit directly or indirectly from human activities for a variety of reasons, including food, shelter, escape from natural predation, or a combination of these factors (Adams et al. 2006; Faeth et al. 2005; Shochat et al. 2004). Scavengers (e.g., raccoons [Procyon lotor], opossums [Didelphis virginiana], crows [Corvus spp.], and gulls [Larus spp.]) and some opportunistic generalist carnivores (e.g., foxes [Vulpes spp.] and coyotes [Canis latrans]) are increasingly common in urban habitats, suggesting that the relatively high abundance of food and the ease with which it is acquired attract some wildlife to urban areas (Adams et al. 2006; Sauter et al. 2006). It is difficult to identify the exploitation of anthropogenic food sources using traditional dietary proxies (e.g., scat analysis), however, because commercially processed foods typically do not contain identifiable, indigestible material (e.g., bone, hair, or chitinous exoskeletons) associated with the consumption of most natural prey.

Despite their endangered status, San Joaquin kit foxes (Vulpes macrotis mutica) commonly occur in suburban and urban areas in the southern San Joaquin Valley, including the large urban center of Bakersfield, California (Cypher 2010; Cypher and Frost 1999; Frost 2005), where little natural habitat remains. Kit foxes living within Bakersfield appear to prefer open habitats provided by golf courses, drainage sumps, vacant lots, and even school campuses.

Previous studies of the foraging ecology of the San Joaquin kit fox have focused on populations living in natural habitats (Moehrenschlager et al. 2004). In the Lokern Natural Area (Lokern) and Kern National Wildlife Refuge (Kern NWR), which are located to the west and northwest of Bakersfield, respectively (Fig. 1), kit foxes consume a wide variety of prey types, but rodents, especially kangaroo rats (Dipodomys spp.), appear to be preferred prey (Cypher 2003; McGrew 1979; Nelson et al. 2007). Urban kit foxes in Bakersfield consume some anthropogenic food, but it is thought that natural prey—rodents, insects, and birds—forms the majority of their diet (Cypher 2010; Cypher and Warrick 1993). Prey remains are commonly observed in urban kit fox scats, and although pieces of anthropogenic food packaging material (e.g., paper and plastic food wrappers) have been found in scats, the proportion of such food sources is difficult to quantify because their consumption typically does not produce identifiable traces in scats (Cypher 2010). Thus, the relative exploitation of anthropogenic food sources by the urban Bakersfield kit fox population remains unknown.

Figure 1

Map of the southern San Joaquin Valley showing the locations of the 3 populations examined in this study.

i1545-1542-91-6-1313-f01.tif

Recent studies have shown that processed foods commonly consumed by people living in North America typically have conspicuously high δ13C values in comparison to food grown in many European and some South American countries (Bol and Pflieger 2002; Jahren and Kraft 2008; Nakamura et al. 1982; but see Nardoto et al. 2006). The principal reason for this trend is that many foods consumed by North Americans contain corn (Zea mays) or its common industrial derivative, corn syrup. Moreover, most domesticated animals (cattle, pigs, or poultry) reared for meat in North America are fed corn during the later stages of maturation prior to slaughter. Corn is a C4 plant with distinctively high δ13C values ranging from −12‰ to −14‰ in comparison to plants that use the C3 photosynthetic pathway and have values ranging from −22‰ to −29‰ (Craig 1953; Farquhar et al. 1989). C3 plants dominate primary production in terrestrial ecosystems in the western United States, although C4 grasses are common seasonal components of native grassland ecosystems in central and southeastern North America (Suits et al. 2005).

Stable isotope analysis is a useful dietary tool for animal ecologists, especially for those who work on elusive species difficult to observe in their natural habitats. The carbon (δ13C) and nitrogen (δ15N) isotope compositions of animal tissues have been used to investigate trophic relationships and quantify diet composition of myriad terrestrial and marine species (Kelly 2000; Newsome et al. 2010; Schoeninger and DeNiro 1984). Through application of trophic discrimination factors to consumer isotope values, the isotopic composition of animal tissues can be compared directly to those of its diet. Typically, consumers are enriched in the rarer heavy isotope—13C or 15N—relative to their diets, and for examination of similar tissues among consumers and their prey this enrichment is ~1–2‰ for δ13C and ~3–5‰ for δ15N for each increase in trophic level (Kelly 2000; Vanderklift and Ponsard 2003).

In this study we used stable isotope analysis to determine the extent to which an urban wildlife population relies on anthropogenic food sources. We presented isotope values for hair and vibrissae (i.e., keratin) from 2 kit fox populations living in natural environments—Lokern and Kern NWR—together with values from kit foxes living within the city of Bakersfield. Kit fox values then were compared to isotope values of common natural prey species collected in Lokern and Bakersfield. Instead of directly comparing urban kit fox hair isotope values to those from anthropogenic food sources, we compared them to isotope values of human hair samples randomly collected from Bakersfield residents. Kit fox vibrissae samples from urban and nonurban populations also were subsampled to produce a continuous isotopic record to determine if individuals exhibit temporal (i.e., seasonal) shifts in dietary composition.

Materials and Methods

Study sites

Kit fox tissues (hair and vibrissae), rodent hair, kit fox scats, or a combination of these, were collected from 3 principal locations in California near the southern terminus of the San Joaquin Valley. We studied nonurban kit fox populations from Lokern (~35°18′18.0N, 119°37′21.0W) and Kern NWR (~35°44′38.0N, 119°37′02.0W) and an urban population inhabiting the city of Bakersfield (~35°22′23.0N, 119°01′07.0W; Fig. 1). The southern San Joaquin Valley is characterized by hot, dry summers and cool, wet winters with average daily temperatures ranging from 4°C to 14°C in December and 21°C to 37°C in July. Precipitation in the southern San Joaquin Valley primarily falls in the winter and early spring when daytime temperatures favor the C3 photosynthetic pathway (Ehleringer 1978; Paruelo and Lauenroth 1996; Tieszen et al. 1997), resulting in a mixed shrubland–grassland system dominated by C3 plants (δ13C ≈ −27‰). Lokern is located on the eastern flank of the Temblor Range near the small town of McKittrick, ~40 km west of Bakersfield. Kern NWR is located ~65 km northwest of Bakersfield. The Bakersfield study area was located primarily in the southwestern quadrant of the Bakersfield Metropolitan Area, which covers >580 km2 and contained a rapidly growing human population of ~400,000 residents as of winter 2003 (Bakersfield Chamber of Commerce 2006). Hair samples from kit foxes of known sex were collected from Lokern in 2002, 2006, 2007, and 2008, and from Bakersfield in 2002, 2006, and 2008. Hair samples from humans of known sex and age were collected from Bakersfield in 2008. Similar to many other canids, kit foxes undergo a single molt per year that occurs during the spring and early summer months. Because hair is metabolically inert, its isotopic composition reflects an average of diet consumed during those months.

Scat analysis

We determined the diet of kit foxes through analysis of scat samples by opportunistically collecting 484 kit fox scats from Lokern and 720 scats from Bakersfield in 2003 and 2004. Fresh scats were collected year-round on both study sites. Scats were air-dried in paper bags and then oven-dried at 60°C for ≥24 h to kill any parasite eggs and cysts. They then were placed in individual nylon bags, washed to remove soluble materials, and dried prior to separating and identifying contents of the remaining undigested material. Mammalian remains (e.g., hair, teeth, and bones) were identified using macroscopic (e.g., length, texture, color, and banding patterns) and microscopic (e.g., cuticular scale patterns) characteristics of hairs (Moore et al. 1974) and by comparing teeth and bones to reference guides (Glass 1981; Roest 1986) and specimens. Other vertebrates were identified to class and invertebrates to order, based on exoskeleton characteristics and comparison to reference specimens.

Isotopic and statistical methods

Kit fox hair and vibrissae samples were collected from animals captured alive or recovered dead as part of several ongoing ecological investigations; samples were collected under United States Fish and Wildlife Service permit TE-825573 and a Memorandum of Understanding from the California Department of Fish and Game. All procedures involving live animals met guidelines approved by the American Society of Mammalogists (Gannon et al. 2007). Samples from each individual fox were stored in labeled coin envelopes pending analysis. Hair samples of the most common rodent species were collected from scats found in urban and nonurban environments. Kangaroo rats are the primary prey for Lokern foxes, and pocket gophers (Thomomys bottae) and California ground squirrels (Spermophilus beecheyi) are the primary mammalian prey for urban foxes. Samples of rodent hair were collected only from scats in which remains of only 1 rodent species were present. We also collected chitinous exoskeletons of Orthoptera and Coleoptera from Lokern and Bakersfield scats, respectively. Bird feathers also were collected from Bakersfield scats, and we randomly collected hair samples from Bakersfield human residents of known sex and age at salons and barbershops in the city.

For carbon (δ13C) and nitrogen (δ15N) analysis, vibrissae, hair, feathers, and insect exoskeletons were rinsed once with a 2∶1 chloroform ∶ methanol solution to remove surface contaminants. Cleaned vibrissae were then subsampled into ~0.2- to 0.3-mg segments using nail clippers, and the length of the whisker was recorded from every 3rd sample. The number of vibrissae segments analyzed from each individual varied from 7 to 14 (  =  10) depending on the length of each vibrissa. Kit fox hair, human hair, and bird feather samples were homogenized by cutting bulk samples into small pieces using surgical scissors and sealed in tin boats for isotopic analysis. Insect exoskeletons were homogenized with a small mortar and pestle and then sealed in tin boats for isotopic analysis. δ13C and δ15N isotope values were determined using an elemental analyzer (Carlo Erba, Milan, Italy) interfaced with either a Delta Plus XL or Delta V isotope ratio mass spectrometer (Thermo Scientific, West Palm Beach, Florida) at the Carnegie Institution of Washington (Washington, D.C.). Isotopic results are expressed as δ values, δ13C or δ15N  =  1,000 × [(Rsample − Rstandard)/Rstandard], where Rsample and Rstandard are the 13C/12C or 15N/14N ratios of the sample and standard, respectively. The standards are Vienna-Pee Dee Belemnite limestone (V-PDB) for carbon and atmospheric N2 for nitrogen. The units are expressed as parts per thousand, or per mil (‰). The within-run standard deviation of an acetalinide standard was ≤0.2‰ for both δ13C and δ15N values. As a control for sample quality we measured the [C]/[N] ratios of each sample. Atomic [C]/[N] ratios of all keratin samples (i.e., hair, vibrissae, and feathers) were 3.3–3.5, encompassing the theoretical atomic [C]/[N] ratio of keratin (3.4). Isotopic differences among urban and nonurban groups or individual kit fox vibrissae values were assessed using analysis of variance and a post hoc Tukey honestly significant difference test; a Levene's test was used to test for homoscedasticity. Last, we used a linear regression to characterize the negative relationship between kit fox vibrissae δ13C and δ15N values. All statistical tests were performed in JMP version 7.0.1 (SAS Institute Inc., Cary, North Carolina).

Results

Kit fox scat analysis

Identification of food remains in scats suggested that both the Lokern and Bakersfield fox populations depended primarily on small vertebrates and insects (Table 1), but differences existed in the species consumed by foxes in the 2 populations. Foxes in the Lokern population ate primarily kangaroo rats, with kangaroo rat remains found in 68.0% of the scats, but the Bakersfield foxes ate ground squirrels, pocket gophers, and a greater proportion of birds than those in the Lokern population. The most common insects consumed at Lokern were Orthoptera (grasshoppers, 23.1%), and the most common insects eaten in Bakersfield were Coleoptera (beetles, 13.1%). We found no evidence that the Lokern foxes ate foods of anthropogenic origin, but Bakersfield scats contained evidence of anthropogenic food consumption, as evidenced by the occurrence of food packaging material in 12.5% of urban kit fox scats (Table 1).

Table 1

Occurrence and percent occurrence of prey types in Lokern Natural Area (n  =  484) and Bakersfield, California (n  =  720) kit fox scats. Kangaroo rats include 3 species: Dipodomys heermanni, Dipodomys nitratoides brevinasus, and Dipodomys ingens. Anthropogenic foods include paper and plastic food wrappers.

i1545-1542-91-6-1313-t01.tif

δ13C and δ15N isotope values

Kit fox hair samples collected from Lokern had significantly lower δ13C and higher δ15N values than kit fox or human hair samples collected within Bakersfield (δ13C: F2,138  =  122.18, P < 0.0001, δ15N: F2,138  =  106.46, P < 0.0001; Table 2; Fig. 2). Despite highly significant differences between mean hair isotope values for the urban and nonurban kit foxes, a small degree of overlap was evident in both δ13C and δ15N values for a relatively small percentage (7/88 or ~8%) of the individuals analyzed. Lokern and Bakersfield kit fox hair collected in the same year (e.g., 2008) was significantly different in both δ13C and δ15N (2008, δ13C: F1,42  =  67.54, P < 0.0001, δ15N: F1,42  =  68.31, P < 0.0001). Lokern kit foxes also showed significantly higher variance in δ15N values in comparison to hair from kit foxes or humans collected in the city (F2,138  =  22.75, P < 0.0001). The mean δ15N value of human hair was slightly (~1‰) but significantly higher than the mean δ15N value of urban kit foxes (F1,92  =  65.70, P < 0.0001); no differences were found in mean δ13C values between humans and kit foxes from Bakersfield (F1,92  =  0.16, P < 0.67). No sex-related differences occurred in δ13C or δ15N values within the urban kit foxes (δ13C: F1,38  =  0.53, P > 0.10, δ15N: F1,38  =  0.07, P > 0.10) or nonurban kit foxes (δ13C: F1,45  =  2.41, P > 0.10, δ15N: F1,45  =  0.11, P > 0.10).

Figure 2

A) Individual kit fox and human hair δ13C and δ15N values from Lokern Natural Area (Lokern) and Bakersfield, California, and B) mean isotope values for each group. Different uppercase and lowercase letters in panel B denote significant differences in mean δ13C and δ15N values, respectively, among groups; errors bars represent SD. C) Trophic-corrected mean kit fox and human hair, and measured potential prey δ13C and δ15N values from Lokern and Bakersfield. Mean kit fox and human hair values have been corrected by subtracting 1‰ and 3‰, respectively, from measured δ13C and δ15N isotope values presented in Table 2 and Fig. 2B. Error bars represent SE.

i1545-1542-91-6-1313-f02.tif

Table 2

Mean δ13C and δ15N values and associated variation (SD) of kit fox and human hair samples collected from Lokern Natural Area (LOK) and Bakersfield (BAK) metropolitan area, California (Fig. 1). An asterisk (*) denotes data from Jahren and Kraft (2008). See Table 1 for scientific names of prey species.

i1545-1542-91-6-1313-t02.tif

Lokern kangaroo rats had significantly higher δ15N (F1,43  =  30.90, P < 0.0001) but similar δ13C values (F1,43  =  0.59, P > 0.10) as ground squirrels in Bakersfield (Table 2; Fig. 2C). Bakersfield pocket gophers had significantly lower mean δ13C values than Lokern kangaroo rats or Bakersfield ground squirrels (F2,54  =  35.79, P < 0.0001). Bakersfield pocket gophers had mean δ15N values that were significantly lower than Lokern kangaroo rats (F1,34  =  22.32, P < 0.0001) but similar to Bakersfield ground squirrels (F1,31  =  1.67, P > 0.10). Coleoptera and pocket gophers collected from Bakersfield had similar δ13C and δ15N values as Orthoptera collected from Lokern (δ13C: F2,62  =  0.86, P > 0.10, δ15N: F2,62  =  0.33, P > 0.10). Bird feathers collected from Bakersfield had significantly higher δ15N values (F1,57  =  14.13, P < 0.001) than Coleoptera collected in the city. Birds also had significantly higher δ13C values than pocket gophers or Coleoptera from Bakersfield (F2,68  =  13.42, P < 0.0001).

Temporal analysis of hair isotope values collected from Lokern revealed significant differences among years for mean δ13C and δ15N values. For δ15N, kit fox hair samples collected in 2008 (n  =  20) were significantly lower by ~2‰ (F3,43  =  7.71, P < 0.001) than hair collected in 2002 (n  =  11) and 2006 (n  =  11); we found no significant differences in δ15N (F2,24  =  1.05, P > 0.10) between hair collected in 2002, 2006, and 2007 (n  =  5). For δ13C, Lokern hair samples collected in 2006 and 2007 had slightly (~1‰) but significantly lower values (F3,43  =  13.86, P < 0.0001) than hair collected in 2002 and 2008. Bakersfield kit fox hair samples collected in 2008 had significantly lower δ15N than hair collected in the city during 2002 and 2006 (F2,37  =  7.38, P < 0.01). No significant differences in δ13C were found among Bakersfield kit fox hair collected in 2002, 2006, and 2008 (F2,37  =  0.56, P > 0.10).

Differences in δ13C and δ15N between hair and vibrissae collected at Bakersfield were not significant (δ13C: F1,136  =  3.99, P > 0.05, δ15N: F1,136  =  0.01, P > 0.10). At Lokern, vibrissae δ13C values were slightly but significantly higher than those of hair (F1,131  =  26.43, P < 0.0001), but no differences were discovered in δ15N between these tissues (F1,131  =  0.88, P > 0.10). Intraindividual isotopic variation in kit fox vibrissae in all populations was relatively low in comparison to interindividual variation (Table 3; Fig. 3). Kit fox vibrissae from Bakersfield, however, appear to have a smaller degree of interindividual variation in mean vibrissae isotope values (especially in δ15N) than those from wild kit foxes collected from Lokern or Kern NWR (Table 3; Fig. 3).

Figure 3

Mean δ13C and δ15N values of all segments sampled from each kit fox vibrissa collected from the Lokern Natural Area, Bakersfield, and Kern National Wildlife Refuge, California. Error bars represent SD. See Table 3 for the number of segments recovered from each vibrissa.

i1545-1542-91-6-1313-f03.tif

Table 3

Mean δ13C and δ15N values and associated variation (SD) of kit fox vibrissae collected from Lokern Natural Area, Bakersfield, and the Kern National Wildlife Refuge, California. Year of collection, sex, overall length (cm), and number of subsamples obtained from each vibrissa are noted. M  =  male; F  =  female.

i1545-1542-91-6-1313-t03.tif

We discovered a significant negative linear trend in the kit fox vibrissae data set, with mean δ15N values decreasing as δ13C increased (F1,23  =  82.15, P < 0.0001; Fig. 3). In general, vibrissae from wild areas had higher mean δ15N and lower δ13C values than vibrissae from Bakersfield, but some overlap was apparent. Kern NWR vibrissae clustered into 2 isotopically distinct groups, and 2 individuals collected in 2008 plotted close to the Bakersfield kit foxes (Fig. 3). Only 1 of these individuals (U122M; Table 3) was statistically indistinguishable (δ13C: F1,22  =  2.50, P > 0.10, δ15N: F1,22  =  3.40, P > 0.05) from 1 Bakersfield kit fox (6285M). The other Kern NWR kit fox (U123M) that plots near the Bakersfield individuals (Fig. 3) has significantly lower δ13C (F1,23  =  22.52, P < 0.0001) values than Bakersfield individual 6285M and significantly higher δ15N values than Bakersfield individual U113F (F1,24  =  17.65, P < 0.001). The other 3 Kern NWR individuals collected in 1994 had significantly higher δ15N but lower δ13C values than Bakersfield foxes (δ13C: F14,136  =  89.26, P < 0.0001, δ15N: F14,136  =  257.63, P < 0.0001). Lokern vibrissae clustered into 3 isotopically distinct groups (Fig. 3), but all of the Lokern kit foxes had significantly different δ13C or δ15N values, or both, than the Bakersfield kit foxes (δ13C: F19,161  =  75.10, P < 0.05, δ15N: F19,161  =  158.13, P < 0.05).

Discussion

Isotopic comparisons between tissues of urban and wild kit foxes (hair), 3 rodent species (hair), 2 types of insects (chitinous exoskeletons), birds (feathers), and humans (hair) suggest that kit foxes living in Bakersfield extensively exploit anthropogenic food sources. After correcting for tissue-specific trophic discrimination by subtracting 1‰ and 3‰, respectively, from mean kit fox hair δ13C and δ15N values, urban kit foxes do not overlap with those of the rodent species, birds, or insects (Coleoptera) present in their scats. Instead, trophic-corrected urban kit foxes have statistically indistinguishable δ13C but slightly lower δ15N values than humans living in Bakersfield, suggesting that Bakersfield kit foxes and humans consume similar foods.

Applying a 3‰ keratin–diet trophic discrimination factor (C. M. Kurle, pers. comm.) to mean urban and wild rodent hair δ13C values yields an approximate mean δ13C value of −23‰ to −27‰ for Bakersfield and Lokern plants, which shows that primary production in both urban and nonurban kit fox habitats in the southern San Joaquin Valley is dominated by plants using the C3 photosynthetic pathway. In contrast, human diets in the United States are characterized by a high consumption of corn-based foods with relatively high δ13C values (indicative of a C4 photosynthetic pathway) in comparison to the wild ecosystems adjacent to most urban or suburban centers in western North America (Suits et al. 2005). For example, mean δ13C values of beef and poultry products from 3 popular restaurant chains throughout the United States ranged from −15‰ to −20‰ (Jahren and Kraft 2008). Due to differences in tissue amino acid composition, keratin (rodents and birds) typically has higher δ13C values by ~1–2‰ (Roth and Hobson 2000) than associated muscle assumed to be assimilated by kit foxes. Applying a 1.5‰ discrimination factor to prey keratin δ13C values to account for tissue-specific differences in amino acid composition shows that natural prey have higher δ13C values than anthropogenic foods (Jahren and Kraft 2008; Table 2). Several studies have used δ13C values to infer the origin of commercial meat products, based on the assumption that most nonorganic North American domesticated animals are typically fed corn before slaughter (Morrison et al. 2000; Schmidt et al. 2005; Schoeller et al. 1980; Schwertl et al. 2005). The conspicuous carbon isotope signature of a North American diet also has been used to assess transient travel activities of humans through comparison of hair δ13C values to that of domestic animals reared in countries worldwide (Bol and Pflieger 2002).

Strong support for extensive exploitation on anthropogenic foods is also evident in the δ15N data. Kit foxes and kangaroo rats collected in Lokern had significantly higher and more variable δ15N values than their urban counterparts. Plants and animals inhabiting semiarid environments typically have higher δ15N values (Amundson et al. 2003; Austin and Vitousek 1998; Handley et al. 1999; Murphy and Bowman 2006) than many commercially produced meat products consumed by humans in the United States, which are characterized by low and relatively invariant δ15N values. Popular fast-food menu items collected from across the United States have mean δ15N values that ranged only from 6.0‰ to 6.4‰ for beef and 2.2‰ to 2.5‰ for poultry (Jahren and Kraft 2008; Table 2), which is significantly lower and less variable than mean and variance of δ15N values for Lokern kangaroo rats.

The higher degree of δ15N variation in Lokern than in Bakersfield kit fox hair was primarily driven by interannual isotopic variation. Plant δ15N values are negatively correlated with water availability (Amundson et al. 2003; Austin and Vitousek 1998), which varies widely from year to year in the southern San Joaquin Valley. Annual rainfall in Bakersfield ranged from ~75 mm (2007) to ~340 mm (1998) from the period 1980–2008 (National Oceanic and Atmospheric Administration;  http://www.wrh.noaa.gov/hnx/bflmain.php); mean (±SD) rainfall over the same period was ~160 (±60) mm. Therefore, the large degree of interannual variation in Lokern kit fox hair δ15N values is likely related to local variation in the base of the food web, with δ15N of plants varying in response to rainfall.

We attempted to assess seasonal shifts in kit fox resource use or baseline changes in primary producer isotope values, or both, by subsampling kit fox vibrissae collected from 2 natural areas (Lokern and Kern NWR) and Bakersfield. In combination with isotopic data of common prey, the small degree of intraindividual isotopic variation observed in vibrissae from Lokern and Kern NWR suggests that primary production in these areas are dominated by plants that use the C3 photosynthetic pathway. Likewise, the low degree of intraindividual versus interindividual isotopic variation suggests that resource use at the individual level remains relatively constant through time but that different individuals might consume different types of resources. Patterns in inter- versus intraindividual isotopic variation in vibrissae have been used to examine individual dietary specialization in marine consumers (Lewis et al. 2006; Newsome et al. 2009) and might be useful in studies of terrestrial consumers.

Our finding that urban kit foxes extensively exploit anthropogenic foods highlights a major difference between dietary data derived from scat and isotopic analysis. Examination of kit fox scat data from Bakersfield shows a relatively even occurrence of prey types in comparison to scats from Lokern. With the exception of anthropogenic foods, the consumption of any of these natural prey types typically will produce indigestible material such as bone, hair, feather, and chitinous exoskeletons, which is why scat analysis is a useful ecological tool. In contrast, anthropogenic foods are less likely to produce identifiable fragments in consumer scats unless the consumer accidentally consumes the indigestible material often used to package human foods. Our results suggest that scat analysis of urban consumers therefore can provide a biased view of diet because prey types that typically do not contain indigestible remains (e.g., anthropogenic foods) are likely underrepresented.

Perhaps because of the availability of anthropogenic foods and intensive exploitation by Bakersfield kit foxes, this population is demographically more stable than wild populations in the southern San Joaquin Valley (Cypher 2010). Higher kit fox densities, smaller home ranges, and higher and less variable reproductive rates in the urban environment are likely due to the abundance and consistent availability of anthropogenic food. Kit foxes in natural areas are subject to dramatic annual variation in prey availability, which is related to annual variation in rainfall (Cypher et al. 2000; Ralls and Eberhardt 1997). Wild kit foxes in the Carrizo Plain (~25 km west of Lokern) maintained large home ranges of sufficient size to sustain their own body mass and condition during periods of prey scarcity (White and Ralls 1993). The primary effect of prey scarcity is to reduce female reproductive success (Cypher et al. 2000; White and Ralls 1993), so reproductive rates in nonurban fox populations vary more than those in Bakersfield. Higher survival rates in Bakersfield foxes also could relate to the scarcity of large predators (Cypher 2010), because interference competition with coyotes is a significant source of mortality for kit foxes in nonurban areas in the southern San Joaquin Valley (Cypher and Spencer 1998; Cypher et al. 2000; Nelson et al. 2007; Ralls and White 1995).

One might expect that the consistent consumption of anthropogenic foods would lead to a series of negative trade-offs for kit foxes and other members of the urban Bakersfield ecosystem, but little evidence for such effects exists. Anthropogenic foods can have nutritional deficiencies (e.g., calcium) in comparison to some natural prey (Pierotti and Annett 1990). Although Cypher and Frost (1999) found differences in hematological and serological values between urban and nonurban kit foxes, including higher cholesterol levels among urban foxes, urban foxes have higher survival rates than nonurban foxes. The consistent consumption of “junk food” potentially could affect reproductive rates and development in young animals (Heiss et al. 2009), but kit foxes in Bakersfield have higher fecundity than wild populations (Cypher 2010). Consistent use of urban habitats by endangered animals also could subject kit foxes to increased exposure to infectious disease agents carried by nonnative feral and domesticated species that are abundant in urban environments (Cypher 2010; Wobeser 2007), but no serious disease epidemics have been documented in urban kit foxes. Wild animals that live in close proximity to urban and suburban environments also can lose their fear of humans, leading to intimate interactions that often have detrimental consequences for animals. In addition, the increased presence of a small carnivore such as a kit fox in high densities relative to natural levels could result in increased top-down control of vulnerable native herbivores and omnivores that inhabit urban ecosystems (Crooks and Soulé 1999; Faeth et al. 2005). These trade-offs do not appear to be impacting the kit fox population or their natural prey within the metropolitan Bakersfield area (Cypher 2010; Cypher et al. 2003); however, the primary cause of mortality among urban kit foxes is collision with vehicles, and several individuals are suspected of having died of exposure to toxicants (e.g., rodenticide or antifreeze—Cypher 2010).

The significant negative trend between mean δ13C and δ15N values of kit fox vibrissae collected from 3 habitats in the southern San Joaquin Valley provides an informative summary of general isotopic patterns among food sources available to wild and urban kit fox populations in this region. Urban to nonurban isotopic gradients similar to the one we have documented likely could be used to assess anthropogenic food subsidies in other urban wildlife populations in regions where native C4 vegetation is entirely absent or not abundant (e.g., western and northeastern North America, western South America, and northern Asia). Our results indicate that stable isotopes can provide a rapid and cost-effective means of evaluating the degree to which wild animal populations exploit anthropogenic subsidies in these regions, which is a crucial 1st step in assessing the impacts of human activities on wildlife populations and food-web dynamics in urban ecosystems.

Acknowledgments

SDN was partially funded by the W. M. Keck Foundation (072000), the National Science Foundation (ATM-0502491), and the Carnegie Institution of Washington. We thank R. Bowden, E. Snyder, C. Mancuso, B. O'Connor, E. Swarth, W. Wurzel, and S. Phillips for laboratory assistance and A. C. Jakle for constructive reviews. We thank C. Bjurlin, A. Brown, S. Bremner-Harrison, C. Fiehler, S. Harrison, J. Nelson, J. Storlie, and C. Wingert for assistance in collecting kit fox hair samples and scats. We thank A. Madrid, T. Reedy, and E. Tennant for assistance in collecting prey remains from kit fox scats. We thank the following for their generous assistance in collecting human hair samples from Bakersfield, California: Dr. D. Germano and his fall 2008 Conservation Biology class from California State University Bakersfield, L. Saslaw and employees of the Bureau of Land Management Bakersfield Field Office, and A. Martinez from Italienne Salon.

Literature Cited

  1. C. E. Adams, K. J. Lindsey, and S. J. Ash . 2006. Urban wildlife management. CRC Press. Boca Raton, Florida. Google Scholar

  2. M. Alberti, J. M. Marzluff, E. Shulenberger, G. Bradley, C. Ryan, and C. Zumbrunnen . 2003. Integrating humans into ecology: opportunities and challenges for studying urban ecosystems. BioScience 53:1169–1179. Google Scholar

  3. R. Amundson, et al 2003. Global patterns of the isotopic composition of soil and plant nitrogen. Global Biogeochemical Cycles 17:1031. Google Scholar

  4. A. T. Austin and P. M. Vitousek . 1998. Nutrient dynamics on a precipitation gradient in Hawai'i. Oecologia 113:519–529. Google Scholar

  5. Bakersfield Chamber of Commerce 2006. Bakersfield community profile.  http://www.bakersfieldchamber.org/pdf/community-profile.pdf. Accessed 1 May 2010.  Google Scholar

  6. R. Bol and C. Pflieger . 2002. Stable isotope (13C, 15N and 34S) analysis of the hair of modern humans and their domestic animals. Rapid Communications in Mass Spectrometry 16:2195–2200. Google Scholar

  7. H. Craig 1953. The geochemistry of the stable carbon isotopes. Geochimica et Cosmochimica Acta 3:53–92. Google Scholar

  8. K. R. Crooks and M. E. Soulé . 1999. Mesopredator release and avifaunal extinctions in a fragmented system. Nature 400:563–566. Google Scholar

  9. B. L. Cypher 2003. Foxes. Pp. 511–546. in Wild mammals of North America: biology, management, and conservation. G. A. Feldhamer, B. C. Thompson, and J. A. Chapman . eds. 2nd ed. Johns Hopkins University Press. Baltimore, Maryland. Google Scholar

  10. B. L. Cypher 2010. Kit foxes. Pp. 49–60. in Urban carnivores: ecology, conflict, and conservation. S. D. Gehrt, S. P. D. Riley, and B. L. Cypher . eds. Johns Hopkins University Press. Baltimore, Maryland. Google Scholar

  11. B. L. Cypher and N. Frost . 1999. Condition of San Joaquin kit foxes in urban and exurban habitats. Journal of Wildlife Management 63:930–938. Google Scholar

  12. B. L. Cypher, P. A. Kelly, and D. F. Williams . 2003. Factors influencing populations of endangered San Joaquin kit foxes: implications for conservation and recovery. Pp. 125–137. in The swift fox: ecology and conservation in a changing world. M. A. Sovada and L. Carbyn . eds. Canadian Plains Research Center. Regina, Saskatchewan, Canada. Google Scholar

  13. B. L. Cypher and K. A. Spencer . 1998. Competitive interactions between coyotes and San Joaquin kit foxes. Journal of Mammalogy 79:204–214. Google Scholar

  14. B. L. Cypher and G. D. Warrick . 1993. Use of human-derived food items by urban kit foxes. Transactions of the Western Section of the Wildlife Society 29:34–37. Google Scholar

  15. B. L. Cypher, et al 2000. Population dynamics of San Joaquin kit foxes at the Naval Petroleum Reserves in California. Wildlife Monographs 145:1–44. Google Scholar

  16. J. R. Ehleringer 1978. Implications of quantum yield differences on the distribution of C3 and C4 grasses. Oecologia 31:255–267. Google Scholar

  17. S. H. Faeth, P. S. Warren, E. Shochat, and W. A. Marussich . 2005. Trophic dynamics in urban communities. BioScience 55:399–407. Google Scholar

  18. G. D. Farquhar, J. R. Ehleringer, and K. T. Hubick . 1989. Carbon isotope discrimination and photosynthesis. Annual Review of Plant Physiology 40:503–537. Google Scholar

  19. N. Frost 2005. San Joaquin kit fox home range, habitat use, and movements in urban Bakersfield. M.S. thesis, Humboldt State University, Arcata, California.  Google Scholar

  20. W. L. Gannon, R. S. Sikes, and the Animal Care and Use Committee of the American Society of Mammalogists. 2007. Guidelines of the American Society of Mammalogists for the use of wild mammals in research. Journal of Mammalogy 88:809–823. Google Scholar

  21. B. P. Glass 1981. Key to the skulls of North American mammals. Oklahoma State University. Stillwater. Google Scholar

  22. N. B. Grimm, et al 2008. Global change and the ecology of cities. Science 319:756–760. Google Scholar

  23. L. Handley, et al 1999. The 15-N natural abundance (δ15N) of ecosystem samples reflects measures of water availability. Australian Journal of Plant Physiology 26:185–199. Google Scholar

  24. R. S. Heiss, A. B. Clark, and K. J. McGowan . 2009. Growth and nutritional state of American crow nestlings vary between urban and rural habitats. Ecological Applications 19:829–839. Google Scholar

  25. A. H. Jahren and R. A. Kraft . 2008. Carbon and nitrogen stable isotopes in fast food: signatures of corn and confinement. Proceedings of the National Academy of Sciences 105:17855–17860. Google Scholar

  26. J. F. Kelly 2000. Stable isotopes of carbon and nitrogen in the study of avian and mammalian trophic ecology. Canadian Journal of Zoology 78:1–27. Google Scholar

  27. R. Lewis, T. C. O'Connell, M. Lewis, C. Campagna, and A. R. Hoelzel . 2006. Sex-specific foraging strategies and resource partitioning in the southern elephant seal (Mirounga leonina). Proceedings of the Royal Society of London, B. Biological Sciences 273:2901–2907. Google Scholar

  28. J. C. McGrew 1979. Vulpes macrotis. Mammalian Species 123:1–6. Google Scholar

  29. A. Moehrenschlager, B. Cypher, K. Ralls, R. List, and M. Sovada . 2004. Comparative ecology and conservation priorities of swift and kit foxes. Pp. 185–198. in Biology and conservation of wild canids. D. W. Macdonald and C. Sillero-Zubiri . eds. Oxford University Press. Oxford, United Kingdom. Google Scholar

  30. T. D. Moore, L. E. Spence, and C. E. Dugnolle . 1974. Identification of the dorsal hairs of some animals of Wyoming. Wyoming Game and Fish Department. Cheyenne. Google Scholar

  31. D. J. Morrison, B. Dodson, C. Slater, and T. Preston . 2000. 13C natural abundance in the British diet: implications for 13C breath tests. Rapid Communications in Mass Spectrometry 14:1321–1324. Google Scholar

  32. B. P. Murphy and D. M. J. S. Bowman . 2006. Kangaroo metabolism does not cause the relationship between bone collagen δ15N and water availability. Functional Ecology 20:1062–1069. Google Scholar

  33. K. Nakamura, D. A. Schoeller, F. J. Winkler, and H. L. Schmidt . 1982. Geographical variations in the carbon isotope composition of the diet and hair in contemporary man. Biomedical Mass Spectrometry 9:390–394. Google Scholar

  34. G. B. Nardoto, et al 2006. Geographical patterns of human diet derived from stable isotope analysis of fingernails. American Journal of Physical Anthropology 131:137–146. Google Scholar

  35. J. L. Nelson, B. L. Cypher, C. D. Bjurlin, and S. Creel . 2007. Effects of habitat on competition between kit foxes and coyotes. Journal of Wildlife Management 71:1467–1475. Google Scholar

  36. S. D. Newsome, M. T. Clementz, and P. L. Koch . 2010. Using stable isotope biogeochemistry to study marine mammal ecology. Marine Mammal Science 26:509–572. Google Scholar

  37. S. D. Newsome, et al 2009. Using stable isotopes to investigate individual diet specialization in California sea otters (Enhydra lutris nereis). Ecology 90:961–974. Google Scholar

  38. J. M. Paruelo and W. K. Lauenroth . 1996. Relative abundance of plant functional types in grasslands and shrublands of North America. Ecological Applications 6:1212–1224. Google Scholar

  39. R. Pierotti and C. A. Annett . 1990. Diet and reproductive output in seabirds. BioScience 40:568–574. Google Scholar

  40. K. Ralls and L. L. Eberhardt . 1997. Assessment of abundance of San Joaquin kit fox by spotlight surveys. Journal of Mammalogy 78:65–73. Google Scholar

  41. K. Ralls and P. J. White . 1995. Predation on San Joaquin kit foxes by larger canids. Journal of Mammalogy 76:723–729. Google Scholar

  42. A. I. Roest 1986. A key-guide to mammal skulls and lower jaws. Mad River Press. Eureka, California. Google Scholar

  43. J. D. Roth and K. A. Hobson . 2000. Stable carbon and nitrogen isotopic fractionation between diet and tissue of captive red fox: implications for dietary reconstruction. Canadian Journal of Zoology 78:848–852. Google Scholar

  44. A. Sauter, R. Bowman, S. J. Schoech, and G. Pasinelli . 2006. Does optimal foraging theory explain why suburban Florida scrub-jays (Aphelocoma coerulescens) feed their young human-provided food? Behavioral Ecology and Sociobiology 60:465–474. Google Scholar

  45. O. Schmidt, et al 2005. Inferring the origin and dietary history of beef from C, N, and S stable isotope ratio analysis. Food Chemistry 91:545–549. Google Scholar

  46. D. A. Schoeller, P. D. Klein, J. B. Watkins, and W. C. MacLean . 1980. 13C abundances of nutrients and the effect of variations in 13C isotopic abundances of test meals formulated for 13CO2 breath tests. American Journal of Clinical Nutrition 33:2375–2385. Google Scholar

  47. M. J. Schoeninger and M. J. DeNiro . 1984. Nitrogen and carbon isotopic composition of bone from marine and terrestrial animals. Geochemica et Cosmochimica Acta 48:625–639. Google Scholar

  48. M. Schwertl, K. Auerswald, R. Schaufele, and H. Schnyder . 2005. Carbon and nitrogen stable isotope composition of cattle hair: ecological fingerprints of production systems? Agriculture Ecosystems & Environment 109:153–165. Google Scholar

  49. E. Shochat, S. B. Lerman, M. Katti, and D. B. Lewis . 2004. Linking optimal foraging behavior to bird community structure in an urban-desert landscape: field experiments with artificial food patches. American Naturalist 164:232–243. Google Scholar

  50. E. Shochat, P. S. Warren, S. H. Faeth, N. E. McIntyre, and D. Hope . 2006. From patterns to emerging processes in mechanistic urban ecology. Trends in Ecology & Evolution 21:186–191. Google Scholar

  51. N. S. Suits, et al 2005. Simulation of carbon isotope discrimination of the terrestrial biosphere. Global Biogeochemical Cycles 19:1017. Google Scholar

  52. L. L. Tieszen, B. C. Reed, N. B. Bliss, B. K. Wylie, and D. D. Dejong . 1997. NDVI, C3 and C4 production and distributions in Great Plains grassland land cover classes. Ecological Applications 7:59–78. Google Scholar

  53. M. A. Vanderklift and S. Ponsard . 2003. Sources of variation in consumer-diet δ15N enrichment: a meta-analysis. Oecologia 136:169–182. Google Scholar

  54. P. J. White and K. Ralls . 1993. Reproduction and spacing patterns of kit foxes relative to changing prey availability. Journal of Wildlife Management 57:861–867. Google Scholar

  55. G. A. Wobeser 2007. Disease in wild animals: investigation and management. Springer-Verlag. Berlin, Germany. Google Scholar

Seth D. Newsome, Katherine Ralls, Christine Van Horn Job, Marilyn L. Fogel, and Brian L. Cypher "Stable isotopes evaluate exploitation of anthropogenic foods by the endangered San Joaquin kit fox (Vulpes macrotis mutica)," Journal of Mammalogy 91(6), 1313-1321, (16 December 2010). https://doi.org/10.1644/09-MAMM-A-362.1
Received: 2 November 2009; Accepted: 1 June 2010; Published: 16 December 2010
JOURNAL ARTICLE
9 PAGES


SHARE
ARTICLE IMPACT
Back to Top