Upper-trophic level piscivores, such as Bald Eagles (Haliaeetus leucocephalus), may be at risk of exposure to environmental contaminants in the western United States from coal-fired power plants and coal-bed methane wells. We collected 64 blood samples from nestling Bald Eagles in southeastern Montana and northwestern Wyoming during 2007–08 for analyses of heavy metals, trace elements, and organochlorine compounds. Mercury was detected in all blood samples and averaged (±SD) 0.28 ± 0.20 ppm. Most nestlings (82.8%) had concentrations near expected background levels, but 7.8% had elevated (>0.7 ppm) mercury levels. Nestlings in Wyoming ( = 0.37 ± 0.22 ppm) had higher blood mercury concentrations than nestlings from Montana ( = 0.22 ± 0.17 ppm; t31 = 3.151, P = 0.015). In Montana, nestlings sampled on Yellowstone River tributaries had lower blood mercury concentrations ( = 0.12 ± 0.10 ppm) than nestlings from the main stem of the Yellowstone River ( = 0.28 ± 0.21 ppm) and Wyoming ( = 0.37 ± 0.22 ppm; F2,32 = 12.439, P < 0.001). Blood levels of mercury and selenium were positively correlated (rS = 0.281, n = 64, P = 0.024). Lead ( = 0.07 ± 0.08 ppm) was detected in 81.3% of nestlings, but only 11.5% of those were considered above background levels. The organochlorine p,p′-DDE ( = 0.003 ± 0.003 ppm) was detected in 69.6% of nestlings sampled. Compared to previous studies in the region, mercury contamination has become more widespread, whereas the prevalence of lead contamination was similar to that of the past. Based on this study, we suggest that some Bald Eagle nestlings may be experiencing adverse effects from mercury contamination, and recommend that additional monitoring take place as coal-fired power plants and the coal-bed methane industry continue to expand.
In an evaluation of 38 bird species, Evers et al. (2005), reported that piscivores have the highest contaminant levels, and that Bald Eagles (Haliaeetus leucocephalus) were the species most at risk in aquatic ecosystems. Although point-source releases of mercury have been greatly reduced during the past two decades (Heinz 1996), concentrations in some Bald Eagle populations have not decreased. For example, mercury in nestling Bald Eagles from Michigan did not decrease between 1989 and 1999 (Bowerman et al. 2002). In Maine, mercury concentrations in Bald Eagle eggs have not decreased since 1970, and nestling mercury levels in blood have not declined since 1991 (DeSorbo and Evers 2005). Weech et al. (2003) recently reported the first known death of a Bald Eagle caused by mercury poisoning.
Coal-fired power plants have contributed 40% of anthropogenic mercury emissions to the atmosphere (U.S. Environmental Protection Agency 1997), and their emissions were once estimated to be two times higher than natural emissions from volcanoes, vents, and hot springs (Nriagu 1989). Subsequent atmospheric deposition and effluent sources in aquatic systems have raised mercury levels 2–4 times above natural levels (National Research Council 1978). Mercury deposition in Montana is above detectable levels only near coal-fired power plants (U.S. Environmental Protection Agency 1997), where most deposition occurs within 80–800 km from the plant (Cohen et al. 2004).
Another potential significant source of environmental contaminants for eagles in Montana is associated with coal-bed methane production, a recently developed industry on which little environmental research has been conducted (Stearns et al. 2005). Wastewater produced from methane wells is discharged or may seep from holding ponds into surface water (Nuccio 2000, Regele and Stark 2000). This water may contain bromine, barium, magnesium, ammonia, arsenic, cobalt, chromium, copper, manganese, nickel, and mercury, most of which can be harmful to wildlife (Rice et al. 2000). Although some of the contaminants are at very low levels in wastewater, the volume of discharge is increasing significantly. Wastewater production from coal-bed methane production rose from 130 000 barrels/day to 1.28 million barrels/day from 1997 to 2000. Moreover, the number of coal-bed methane wells is predicted to increase 6–28 times within the next 20–30 yr (Rice et al. 2000); thus, negative effects of contaminated water on aquatic habitats and wildlife may be pronounced (Stearns et al. 2005). The Powder River Basin of southern Montana and northern Wyoming is the center of coal-bed methane production within the United States.
Both the Montana Bald Eagle Management Plan (Montana Bald Eagle Working Group 1994) and the Greater Yellowstone Bald Eagle Management Plan (Greater Yellowstone Bald Eagle Working Group 1996) suggest sampling of environmental contaminants in eagles every 3 yr and 5 yr, respectively. With the exception of Harmata (2011), no contaminants sampling has been conducted in 11 yr in Montana or Wyoming. The National Bald Eagle Management Guidelines call for monitoring populations where bioaccumulating compounds have been documented as part of delisting activities (U.S. Fish and Wildlife Service 2006). In this study, we measured contaminant levels in nestling Bald Eagles from Montana and Wyoming to fulfill these management recommendations and to address concerns over recent eagle deaths from mercury contamination (Harmata 2011). Our objectives were to measure the prevalence and concentrations of environmental contaminants in nestling Bald Eagles produced in Montana and Wyoming to answer the following questions: (1) is mercury contamination in eaglets at a level of concern and are there geographic patterns of mercury contamination?; (2) is there a relationship between mercury and selenium in nestling tissues, given that selenium is known to mitigate the effects of mercury toxicity through sequestration in certain tissues?; (3) how do current contaminant levels compare to previous concentrations?; (4) Are contaminants from coal-bed methane wastewater at a level of concern in nestling eagles? We also examined levels of organochlorine (OC) compound levels (e.g., DDE), because they may persist in local environments from past pesticide use. We compare our mercury results with those found in three previous studies in the region (Harmata and Oakleaf 1992, Harmata and Restani 1995, Harmata 2011).
Our study area in Montana covered a narrow strip of northern floodplain deciduous forest from Livingston, Montana east toward the North Dakota border along the Yellowstone River and its major tributaries, the Bighorn, Tongue, and Powder rivers. Lower reaches of the rivers contained warmer water, gentler gradients, lower oxygen concentration, higher turbidity, greater sediment deposition, and finer substrate than upper reaches (Zelt et al. 1999). Fish species present in the middle and lower reaches of the Yellowstone and its tributaries included goldeye (Hiodon alosoides), burbot (Lota lota), sauger (Sander canadensis), walleye (Sander vitreus), channel catfish (Ictalurus punctatus), sunfishes (Centrarchidae spp.), drum (Aplodinotus grunniens), rainbow trout (Oncorhynchus mykiss), and brown trout (Salmo trutta; Zelt et al. 1999, Galat et al. 2005). Summers were sunny and warm and winters were cold with moderate snowfall. Mean monthly temperatures ranged from −11°C in January to 22°C in July. Precipitation was low, with 80% of the annual 30–36 cm falling in April–September (Compton et al. 1988). Major population centers located on the Yellowstone River and tributaries included Billings, Laurel, Livingston, Hardin, Miles City, Broadus, Glendive, and Sidney, Montana (Zelt et al. 1999). Agriculture was the most common land use in the riparian and adjacent areas, and most untilled areas were grazed extensively by cattle (Dusek et al. 1989, Zelt et al. 1999). Oil and gas production and coal mining were prevalent in the Bighorn and Powder River basins. Many tributaries were dewatered and irrigation accounted for 90% of water use.
In Wyoming, we analyzed blood from Bald Eagle nestlings along the upper Snake River, Jackson Lake, and Lower Slide Lake from the Jackson Lake dam to Hoback Junction. Headwaters of the river were fed from the south-central Rockies terrestrial ecoregion, an area of mountain ranges, intermontane valleys, and alpine lakes. Local fish species included Yellowstone cutthroat trout (O. clarki bouvieri), Snake River finespotted cutthroat trout (O. clarki behnkei), bull trout (Salvelinus confluentus), brown trout, brook trout (S. fontinalis), lake trout (S. namaycush), smallmouth bass (Micropterus dolomieui), carp (Cyprinus carpio), largemouth bass (M. salmoides), channel catfish, and whitefish (Coregonus clupeaformis; Stanford et al. 2005). During snowmelt, water clarity was low, but relatively high at other times. Climate was continental with cool summers and cold winters. Mean January temperature was −11.4°C, mean July temperature was 14.5°C, and average annual precipitation was 568 mm in the region (Swenson et al. 1986). No major human population centers or point sources of pollution existed along the upper Snake River. However, the river was impacted by isolated mines, cattle grazing, irrigation, and many dams and water diversions.
We chose Bald Eagle nests for contaminant sampling based on nest activity, landowner permission, and suitability/safety of the nest tree for climbing. We sampled nests in different territories in 2007 and 2008. We climbed to nests by rope-assisted climbing in late May and early June, when nestlings were 4–10 wk of age (Bortolotti 1984). We used a 22-gauge sterile syringe to collect 1–3 cc of blood from the brachial vein of each nestling. Blood was placed in a CaEDTA preservative vacutainer for heavy metal and trace element analysis. From the largest nestling, we also collected an additional 2–3 cc of blood for organochlorine pesticide analysis (both in 2007 and 2008 in Montana, only in 2007 in Wyoming). This sample was centrifuged and the serum separated for analysis. We refrigerated and stored samples until shipment to laboratories at the end of each field season in June. Total processing time averaged 10 min per nestling and 90 min at nests.
Blood samples were shipped to Michigan State University, College of Veterinary Medicine, Diagnostic Center for Population and Animal Health (DCPAH), Toxicology Section, for analysis. Whole blood was analyzed for the following heavy metals and trace elements (detection limit): arsenic, cadmium, mercury, and selenium (1 part per billion [ppb]); antimony, lead, and thallium (5 ppb); and chromium (25 ppb). Blood was analyzed for total mercury by cold vapor atomic absorption (Wood et al. 1996) using an M-6000 Analyzer (CETAC Technologies); for lead, chromium, arsenic, cadmium, thallium and antimony by inductively coupled plasma (ICP) atomic emission spectrometry (Vista Axial ICP-AES; modified from Braselton et al. 1981 and Stowe et al. 1985); and for selenium by ICP-mass spectrometry (Agilent 7500ce ICP-MS; Wilbur 2007). The AA analyzer was calibrated using 0, 25, 100, 500, and 5000 ppt standard solutions, ICP-AES was calibrated with 0, 1 and 10 ppm standards, ICP-MS was calibrated with 0, 5, 50, 250 and 500 ppb standards, and final concentrations were measured against standard reference solutions and digest blanks arranged for a linear relationship. Quality control was maintained by monitoring of results obtained with Bio-Rad (Hercules, California, U.S.A.) Lypochek Whole Blood Metals Controls 1 and 2. Calibrations were also checked against nitric acid digested Standard Reference Materials, such as NIST SRM 2976 mussel (see Harmata 2011 for detailed laboratory methodology).
Blood was also analyzed at DCPAH for the following organochlorine pesticides (as described in Hollamby et al. 2004; detection limit of 1 ppb): aldrin, alpha_BHC, beta_BHC, dieldrin, heptachlor, heptachlor epoxide, methoxychlor, oxychlordane, P,P′-DDE, P,P′-DDD, P,P′-DDT, and theta_BHC. Contaminants were analyzed in serum samples using a Varian 3400 Gas Chromatograph. Concentrations were determined in comparison to spiked serum samples containing 1 ppm of polychlorinated biphenyl, and 0.5 ppm of chlorinated pesticide mix. Extractions were performed with hexane/acetone, 9∶1, and final dried extracts were re-suspended in ethanol/iso-octane, 2∶8 (Hollamby et al. 2004). Blank solvent injections were run through the analyzer between samples. Extraction efficiency was based on recovery of compound standards from spiked blanks to ensure all recoveries exceeded 60%. Blanks, spikes, standards, and specimens were run simultaneously and GC peak identities were verified if retention times varied by <0.1 min from standards (see Harmata 2011 for detailed laboratory methodology).
Contaminant concentrations were reported in parts per million wet weight from DCPAH. Because of relatively small samples sizes, we combined the 2007 and 2008 data. We separated nestlings by state, and further separated nestlings from Montana into groups based on water body adjacent to nests (i.e., Yellowstone River, Snake River, Yellowstone River tributaries). We log-transformed data to improve normality and used an independent samples t-test or one-way ANOVA to compare arithmetic means. When statistical significance was analyzed among groups, we averaged contaminant concentrations of nestlings within nests and only performed tests when ≥50% of individual samples had detectable contaminants. We assigned a value of one-half the detection limit of the test to samples below the detection limit for the respective contaminant (Wiemeyer et al. 1989). Spearman's rank correlation was used to test for relationships between blood concentrations of mercury and selenium. We completed statistical analyses using SPSS 14.0 (SPSS 2006) and assigned significance at P ≤ 0.05.
We sampled 41 nestlings from 18 nests ( = 2.28 ± 0.75 nestlings/nest, = 46 ± 11 d old) in Montana and 25 nestlings from 15 nests in Wyoming ( = 1.67 ± 0.72 nestlings/nest, = 54 ± 8.1 d old; blood samples were obtained from 39 of 41 Montana nestlings). Heavy metals detected in ≥50% of nestling blood samples included mercury (100%), selenium (100%), lead (79.7%), and chromium (56.3%; Table 1). Other elements detected in <50% of whole blood samples included antimony, cadmium, arsenic, and nickel (Table 2).
Whole blood concentrations (ppm wet weight) of mercury (Hg), selenium (Se), lead (Pb), and chromium (Cr) in nestling Bald Eagles sampled in Montana and Wyoming, U.S.A., 2007 and 2008.
Frequency of occurrence, mean ± SD, and range (ppm whole blood) of cadmium (Cd), antimony (Sb), nickel (Ni), and arsenic (As) in blood of nestling Bald Eagles sampled in Montana and Wyoming, U.S.A., 2007 and 2008. Cd, Sb, Ni, and As were detected in ≤50% of samples.
Wyoming nestlings had higher mercury levels in blood (t31 = 3.151, P = 0.004) than Montana nestlings (Fig. 1). When grouped by water body (Yellowstone River, Snake River, or Yellowstone River tributaries combined), nestlings from Yellowstone River tributaries had lower blood mercury levels ( = 0.12 ± 0.10 ppm, n = 8) than Yellowstone River nestlings ( = 0.28 ± 0.21 ppm, n = 10) and Snake River nestlings ( = 0.37 ± 0.22 ppm, n = 15; F2,32 = 12.439, P < 0.001). Wyoming nestlings also had higher blood selenium levels than Montana nestlings (t25 = 3.574, P < 0.001; Fig. 1). Whole blood mercury and selenium were positively correlated (rS = 0.281, n = 64, P = 0.024).
Blood samples from 23 nestling Bald Eagles were analyzed for organochlorine compounds. Only p,p′-DDE was found above detectable levels and no differences existed between Montana ( = 0.004 ± 0.004 ppm, detected in 9 of 11 nestlings) and Wyoming ( = 0.002 ± 0.002 ppm, detected in 7 of 12 nestlings); however, the sample size was small.
All nestlings sampled contained detectable levels of mercury in blood. Mean blood mercury levels ( = 0.28 ppm) were similar to the level ( = 0.23 ppm) from nestlings sampled in Montana between 1985 and 1991 (Harmata and Oakleaf 1992). However, mercury was detected in only 50% of those samples; thus, the prevalence of mercury contamination has become more widespread during the last decade (see Harmata 2011, who used similar methodology as in our study). Mercury levels in our study also corresponded to background mercury levels found in captured Bald Eagles in the northwestern U.S. ( = 0.23 ppm, range 0.17–0.31 ppm; Wiemeyer et al. 1989).
Mercury concentrations in blood in this study fell within the range of levels detected in other populations. Lower levels have been documented in South Carolina ( = 0.10 ppm, range 0.03–0.25 ppm; Jagoe et al. 2002), Florida ( = 0.16 ppm, range 0.02–0.61 ppm; Wood et al. 1996), and the state of Washington ( = 0.23 ppm, range 0.075–0.65 ppm; Wiemeyer et al. 1989). Higher blood mercury levels were found in Maine ( = 0.53, range 0.1–1.20 ppm; DeSorbo and Evers 2005), the Columbia River Estuary ( = 0.47 ppm, range 0.19–1.40 ppm; Anthony et al. 1993), and Oregon ( = 1.2 ppm, range <detection limit −4.20 ppm; Wiemeyer et al. 1989).
DeSorbo and Evers (2005) proposed mercury exposure categories for Bald Eagle nestlings based on relationships between mercury and reproductive success in Common Loons (Gavia immer). Mercury levels in most nestlings from Montana and Wyoming fell within the “background” (0–0.39 ppm) and “moderate” (0.4–0.69 ppm) categories. However, 7.8% of nestlings sampled contained “elevated” (0.7–0.99 ppm) mercury levels. The “elevated” level in nestling Bald Eagles corresponds to a level >3.0 ppm in Common Loons (DeSorbo and Evers 2005), a threshold where negative effects on reproductive success and behavior became evident (Evers et al. 2004). This cross-species comparison may be tenuous because Bald Eagles appeared to be more efficient at detoxifying mercury in brain tissue than loons (Scheuhammer et al. 2008). Nonetheless, mercury concentrations in Bald Eagles from the Great Lakes caused significant neurological changes in brain receptor and enzyme activity (Rutkiewicz et al. 2011).
Selenium mitigates the effects of mercury toxicity by sequestration as insoluble HgSe in liver, kidneys, and brain (Cuvin-Aralar and Furness 1991, Scheuhammer et al. 1998, Hopkins et al. 2007). In this study, selenium and mercury levels in blood were correlated, albeit poorly (rS = 0.281). Other studies found very strong correlations between mercury and selenium in brain, liver, and kidneys (Hopkins et al. 2007, Rutkiewicz et al. 2011). At high levels of mercury concentration, selenium and mercury occur at approximately a 1∶1 molar ratio (2.54 ppm Se: 1 ppm Hg) in Bald Eagle brain, liver, and kidneys, and at that level selenium is effective in detoxifying mercury (Scheuhammer et al. 2008). In our study, selenium and mercury in blood occurred at a ratio greater than 1∶1. Blood is not a known sequestration tissue, which may explain the poor correlation we found.
A few geographic patterns of mercury contamination emerged from our study. A larger proportion of nestlings from Wyoming had “elevated” concentrations of mercury, and Wyoming nestlings also had higher average blood mercury compared to Montana nestlings. After we grouped nestlings by water body (Yellowstone River, Snake River, and Yellowstone River tributaries), differences in mercury levels became apparent. Nestlings sampled on Yellowstone River tributaries in Montana (Powder River, Tongue River, and Bighorn River) had lower mercury concentrations than nestlings on the main stem of the Yellowstone and Snake Rivers. White-tailed Eagles (H. albicilla) in Sweden (Olsson et al. 2000) and Bald Eagles along the Great Lakes (Dykstra et al. 2010) also exhibited geographic differences in mercury concentrations. The adult population on our study areas in Montana and Wyoming was nonmigratory, as was that studied by Olsson et al. (2000), who concluded that blood concentrations of mercury in nestlings were as useful a biomarker of contamination as egg concentrations.
Nestling Bald Eagles in our study had detectable levels of contaminants found in coal-bed methane wastewater (e.g., mercury, lead, selenium, chromium, arsenic, and nickel). Other than mercury and lead, concentrations of these contaminants in nestling blood were below levels associated with adverse effects. However, each coal-bed methane well produces approximately 57 L of discharge water per minute (Regele and Stark 2000). Discharge water is projected to increase significantly (6–28 times) with further industry development in the Powder River Basin (Rice et al. 2000). Thus, Bald Eagles may become vulnerable to water quality degradation from coal-bed methane wastewater.
Although lead was detected in 81.3% of nestlings ( = 0.07 ppm), 88.5% of nestlings contained “background” levels (<0.20 ppm) and only 11.5% were considered “exposed” (≥0.20 to 0.59 ppm; Redig 1984). All “exposed” nestlings were sampled in Montana. Harmata and Oakleaf (1992) detected lead in 33.3% of nestlings sampled using a detection limit of 0.06 ppm, and reported a higher mean blood level (0.14 ppm) than observed in our study. Eliminating lead levels below 0.06 ppm in our study produced a detection rate of 37.5%, comparable to that observed in the late 1980s.
Despite being banned in 1972, p,p′-DDE, a metabolite of the insecticide DDT, was detected in 69.6% of Bald Eagle nestlings, although all concentrations were well below levels considered adverse (Blus 1996, Elliott and Harris 2001/2002). A detection rate of 67% and higher mean level ( = 0.007 ppm) were reported a decade earlier in free-flying Bald Eagles from Montana when using a detection limit of 0.003 ppm (Harmata and Restani 1995). Eliminating values below 0.003 ppm in our study produced a detection rate of 48%. The decline in DDE concentrations mirrored that observed for Bald Eagles nesting along the Great Lakes (Dykstra et al. 2010).
In summary, some local mercury contamination in Bald Eagle nestlings was evident and contamination has become more widespread compared to the previous decades. However, the population of Bald Eagles that was sampled in our study has increased every decade since comprehensive monitoring began in 1980 (Hammond 2010). As of 2007, 151 new coal-powered plants are proposed for construction in the United States, including seven in Montana and 11 in Wyoming (U.S. Department of Energy 2007). Therefore monitoring of mercury in Bald Eagle nestlings should continue. Contaminants associated with coal-bed methane wastewater were not detected at a level of concern, yet with projected industry expansion, regular sampling of Bald Eagle nestlings from the Powder River Basin should continue.
L. Apple, K. DuBois, A. Puchniak, and K. Undlin provided data and technical assistance. G. Montopoli trained the senior author in tree-climbing techniques, and C. Cyrus, H. Harlow, and T. Karshnik assisted with fieldwork. Helpful project administration came from B. Kjellberg, M. McKenzie, and J. Ensign. Financial support was provided by the U.S. Bureau of Land Management and St. Cloud State University. The U.S. Bureau of Land Management, Miles City, MT, provided housing and vehicles. We are also grateful to many private landowners for allowing access to Bald Eagle nests on their property. The comments of three anonymous reviewers and C. Dykstra improved the draft manuscript.