Proximity to pollution sources and risk of amphibian limb malformation.
In 1995, amphibians with severely malformed limbs were discovered in Minnesota (Blaustein and Johnson 2003). The next year, amphibians with truncated and missing limbs were found at several sites stretching along 120 miles of Vermont's Lake Champlain shoreline (Levey et al. 2003). Since then, elevated rates of developmental abnormalities have been found in most U.S. states and Canada, raising concern that amphibians are serving as animal sentinels of human environmental health hazards (Burkhart et al. 1998, 2000; Daszak et al. 2001; van der Schalie et al. 1999).
The exact etiology of amphibian limb abnormalities (including missing, extra, and malformed limbs) remains unclear. The major suspects have been ultraviolet B (UV-B) radiation, trauma, parasitic trematode infestation, and xenobiotic pesticides or chemicals (Ouellet 2000). Although many researchers have searched for single causative agents, some have stated that the etiology is likely multifactorial (Linder et al. 2001).
In laboratory settings, some evidence has supported each of the etiologic hypotheses. Controlled exposure to UV radiation has produced amphibian dysmorphogenesis (Ankley et al. 1998, 2002) and truncated limbs (Levey et al. 2003; Meteyer et al. 2000; Ouellet et al. 1997). These studies, however, have generally failed to reproduce the spectrum of abnormalities occurring in wild populations. The abnormalities that result from experimental UV exposures are most often bilateral and symmetrical (Ankley et al. 1998, 2002), whereas abnormalities found in the wild are not (Levey et al. 2003; Meteyer et al. 2000; Ouellet et al 1997). Furthermore, the levels of UV exposure used in the laboratory experiments may not reflect real-world exposures.
Another primary etiologic hypothesis of limb abnormality is trauma related to predation. Although predation can account for some forms of abnormality in the wild, the hypothesis, more generally, has not been supported as the primary cause of increased amphibian abnormality rates in recent years (Blaustein and Johnson 2003; Levey et al. 2003). Although predation should always be considered in this field of research, it is likely that deformities caused by predation have a different etiologic pathway and therefore, in research, should be distinguished from the other hypotheses of dysmorphogenesis.
Macroparasite infection is the third etiologic hypothesis of amphibian limb abnormality. The parasite hypothesis continues to receive substantial attention and is perhaps the most thoroughly explored of all the hypotheses (Blaustein and Johnson 2003). The most commonly explored parasite is the trematode Ribeiraia ondatrae. Infestation with Ribeiroia is associated with limb abnormalities in some amphibian species (Johnson et al. 2001, 2002). Laboratory experiments suggest that the mechanism of Ribeiroia-induced abnormalities may involve mechanical disturbance of growing limb cells or interference with a retinoid-sensitive signaling pathway (Johnson and Sutherland 2003).
The role of exposure to potential chemical teratogens has also been investigated. Candidate toxicants have included nonpolar organics, metals (Burkhart et al. 1998; Linder et al. 2001; Stocum 2000), herbicides, pesticides, and other components of agricultural runoff (Bishop et al. 1999; Ouellet et al. 1997), sewage (Linder et al. 2001; Ouellet 2000), and pharmaceuticals (Mizgireuv et al. 1984). Such chemical agents could directly affect amphibians' development or act indirectly by increasing amphibian susceptibility to other environmental stressors such as infectious disease, predation, and UV-B light. Investigations into chemically mediated limb abnormalities have used two major approaches. First, amphibian eggs and larvae have been exposed to water and sediment collected from field sites with high abnormality rates (Fort et al. 1999, 2001). Second, the specific suspected amphibian teratogens have been tested in the laboratory using toxicologic assays (Degitz et al. 2000, 2003; LaClair et al. 1998). Together, these studies have shown that exposure to field-collected water and sediment can result in limb abnormalities and that a number of chemicals can have severe teratogenic effects on amphibians related to dose or concentration (Burkhart et al. 1998). However, there are inconsistencies between laboratory and field results and no single causative chemical has been identified.
The chemical teratogen hypothesis has particular relevance to human health risk. If waterborne chemical toxicants are involved in amphibian malformations, there is potential for shared exposure with human populations through dermal contact, ingestion, and inhalation routes.
Despite the fact that multiple hypotheses have emerged to explain the phenomenon of amphibian limb abnormalities, few studies to date have made use of research techniques allowing examination of multiple factors. For example, most studies of chemical causes did not also collect data regarding infectious agents, and few of the studies have used multivariable statistical techniques to model the relative effects of different factors.
We performed a cross-sectional study of risk factors for deformities in a large systematic sample of amphibians. The large sample size allowed for the creation of a multivariate model to test the association between amphibian limb malformation and a number of independent risk factors. The types of land use adjacent to wetlands where amphibians were surveyed served as a proxy measure for possible sources of water pollution. We hypothesized that, after adjusting for confounding factors, amphibians in wetlands adjacent to agriculture, septic systems, or lawns would be at greater risk for amphibian hind limb malformation due to the waterborne chemical runoff associated with such land uses.
Materials and Methods
Study sample. Between 24 May and 28 August 2002, amphibian specimens consisting of two species of hylids (Hyla versicolor and Pseudacris crucifer) and four species of ranids (Rana pipiens, Rana catesbeiana, Rana clamitans, and Rana sylvatica) were collected from 42 wetlands in the Lake Champlain Basin of Vermont. We selected wetlands in a representative fashion along an urbanization gradient ranging from relatively undisturbed forest habitat (Green Mountain National Forest), to rural communities, to neighborhoods in Burlington. To collect specimens at each site, standardized collection methodology consisted of pipe samplers (steel pipe, 35-cm diameter, 0.91 m long) and dip nets (46 cm x 23 cm with 1-mm mesh). An attempt was made to collect up to 300 specimens from each site (a maximum of 100 during each of three visits). After capture, specimens were first anesthetized in a solution of tricaine methanesulfonate and then placed in 70% ethanol, according to protocols for the study that were approved by the Yale University Animal Care and Use Committee. Each specimen was later examined in the laboratory in order to determine genus and species, Gosner stage, and presence of malformation. A subsample of specimens was examined by dissection for the presence of parasite metacercariae, including Ribeiroia.
Exposure assessment. For each of the 42 wetlands, on-site field observations were used to determine whether agriculture or lawns were located proximate to the wetland. The presence of agriculture and lawns were then scored as yes/no responses for each site. In addition, we independently estimated land use/land cover within 200 m of each amphibian sample site, which was calculated using geographic information system (GIS) data. The latitude and longitude coordinates of each site were used with land-use/land-cover GIS layers to map the land use within 200 m of each site. The Raster land-cover data set from Vermont GIS (U.S. Geological Survey 1999) was brought into ArcMap (Environmental Systems Research Institute, Redlands, CA) and was converted to vector data (polygons) to allow clipping of the features for each buffer zone. These polygons were then clipped using the geoprocessing command by a 200 m buffer surrounding the GPS (global positioning satellite) coordinates representing the study site's general area. These clipped land-use/land-cover areas were then summarized for each location by their classification codes to calculate land-cover percentages represented in the data. For this analysis, the 21 possible land-use categories were used to determine the presence of agriculture or forest. We compared the GIS measures for agriculture and forest with field observations of agriculture and lawns. There was a strong correlation between GIS coded agriculture land-use and field observations of agriculture and lawn near the study site (p < 0.0001 for both). Both observed agriculture and lawns were negatively correlated with GIS land-use estimates for forest cover (p < 0.0001 for both).
Several quantitative measurements were made at each site, including pH, conductivity, dissolved oxygen, temperature, total nitrogen, and total phosphorus for the water samples. If more than one measurement took place at an individual wetland, the measurements were averaged together for that site.
As an additional investigation into the possible role of parasitic infection, a representative sample of snails from the study wetlands was investigated for evidence of Ribeiroia infection.
Case definition. Each individual specimen was examined by a trained technician and classified according to a case definition adapted from a well-established amphibian limb abnormality classification scheme (Meteyer et al. 2000). To be classified as a "case" of limb malformation, a specimen had to exhibit one of the following: missing or reduced hind limb elements, complete but malformed hind limb, and/or duplicated hind limb elements or segments.
For the analysis of limb malformations, we included only those specimens with Gosner stage of [greater than or equal to] 26 (Gosner 1960). At this stage, hind limbs are visible, and it is possible to assess whether gross deformities are present.
Of the original 5,983 specimens, this led to the exclusion of 684 with stage < 26, and 27 with missing stage, leaving 5,272. An additional 8 cases were excluded because of unknown length, leaving 5,264 in the final study sample. For our case definition, we excluded trauma deformities (abnormalities that appeared to be a result of trauma, including presence of open wounds, edema, scarring, bone fractures, etc.) because of the differing etiologies of trauma and nontrauma abnormalities.
Statistical analysis. All analyses were performed using SAS software (version 8.02; SAS Institute Inc., Cary, NC).
Simple frequencies were calculated for categorical variables, including Gosner stage, genus, water-quality measures, presence of pollution sources, and presence of limb malformation. Means and SDs were calculated for continuous variables.
To determine bivariate associations between exposures and rates of malformation, we performed simple logistic regression. Odds ratios (ORs) and 95% confidence intervals (CIs) were calculated for each individual factor. An OR calculates the odds of a risk factor being present in the affected cases compared with the odds that it is present in the non-affected individuals. A multivariate logistic regression model was developed to determine the independent predictors of malformation. To determine which variables to include in the multivariate model, we examined collinearity between independent variables using correlation coefficients. Variables with correlations above levels at which multicollinearity would be considered likely (r > 0.40) were excluded from the multivariable analyses. We found that a number of variables had significant collinearity, including nitrogen and phosphorus (r = 0.67) and pH and dissolved oxygen (r = 0.79). Therefore, neither phosphorus nor pH was included in the final multivariate model.
The multivariate logistic regression analysis used a backward selection process to eliminate nonsignificant variables from the model (criteria for elimination from the model set at p > 0.05). ORs, 95% CIs, and p-values for association between individual risk factors and limb malformation were determined for variables remaining in the final model. The overall discriminant power of the model was assessed using a C-staristic.
Characteristics of study sample. Table 1 shows the characteristics of 5,264 specimens meeting eligibility criteria (specimens with Gosner stage of [greater than or equal to] 26). The average Gosner stage was 36 (field stage 4: toes 3-5 separated). Overall, 83 specimens (1.6%) showed evidence of nontraumatic limb malformation. The study-site--specific rate of malformation ranged from 0 to 10.2%. The lowest rates were found in the wetlands located in the Green Mountain National Forest. Table 1 also shows the relative prevalence of subtypes of nontraumatic malformation. The most common type was malformed limb or element (68 of 83), followed by missing limb or element (25 of 83). Some individuals had more than one type of abnormality.
Examination of a subsample of individual specimens (n = 40) revealed no evidence of Ribeiroia infection. Similarly, representative samples of host snails from the sample wetlands did not demonstrate evidence of Ribeiroia infection (Skelly D, unpublished data).
Exposure assessment. Table 2 summarizes the exposure characteristics of the 42 wetland study sites. More than 40% of the wetlands had some degree of agriculture nearby; this ranged from pastureland to cropland to intensive dairy farming. Lawns were present near > 35% of wetlands. The wide range of values for water-quality measures reflects, in part, variations in runoff sources; the wide variability of conductivity reflects proximity to roads treated with salt in winter. The highest nitrogen readings were found in a pond located downhill from a dairy barn.
Risk factor analysis. Table 3 shows the simple and multiple logistic regression measures of association between different risk factors and nontraumatic amphibian limb malformation. In the simple (bivariate) analyses, Gosner stage, proximity to agriculture, proximity to lawns, and dissolved oxygen each showed a positive association with malformation.
In the multivariate logistic regression model, Gosner stage remained highly significantly associated with malformation (OR = 1.18; p < 0.0001). In other words, the risk of malformation increased 18% for each increase in Gosner stage. Although malformation rates were slightly higher in ranids than in hylids, the effect of genus was not significant in the multivariate model. Furthermore, analyzing risk factors for malformation in ranid species alone or hylid species alone produced results similar to those of our combined model (data not shown). In the multivariate model, proximity to agriculture remained a highly significant predictor of malformation risk (OR = 2.26; 95% CI, 1.42-3.58; p < 0.001). None of the other independent variables tested showed a significant association in the multivariate model. The discrimination and fit of the logistic regression model were good, with a C-statistic = 0.79 and a p-value for the Hosmer-Lemeshow goodness-of-fit test of 0.10.
The results of this study, based on one of the largest systematic sampling of limb deformities in wild amphibian populations to date, suggest that the composition of landscapes surrounding wetlands affects rates of limb malformation. In particular, proximity to human-associated land uses, including agriculture and lawns, is associated with an increased risk. This positive association persists even after adjusting for the effect of developmental stage and variation in water-quality measures such as nitrogen and pH. Proximity to agriculture was associated with a more than doubling of the risk of limb malformation.
Major strengths of this study include its sample size and systematic design. Although other studies have assessed agricultural land use in relation to amphibian population size in specific geographic areas (Davidson et al. 2001, 2002; Ray et al. 2002), few studies have assigned exposure variables based on observed pollution sources in a systematic manner in order to assess malformation rates. Several studies have discussed land use and land-use change as drivers of the abnormality and decline phenomena (Collins and Storfer 2003; McCallum and Trauth 2003) but have not gone on to analyze outcomes with respect to these factors.
Unlike many previous studies, this study uses a human epidemiologic methodology to assess an ecologic problem (with possible relevance to human health). Evaluation of multiple stressors will require continued development of effective study methodologies and a movement away from the single-agent hypothesis testing of the past (Rabinowitz et al. 1999). To our knowledge, this is one of the first studies to use multivariate techniques (which require a large sample size) to evaluate the relative importance of multiple factors while adjusting for possible confounding. This reduces the possibility that an observed association between a risk factor (e.g., agriculture) and the outcome of interest (limb malformation) is due in fact to a confounding risk factor that is linked with both the exposure and the outcome in such a way that spurious etiologic associations are inferred.
What is the possible biologic basis of the observation that proximity to agricultural land use is associated with risk for amphibian limb malformation? We argue that exposure to sources of anthropogenic pollution is a likely explanation. Without identification of specific compounds, any specific hypothesis remains speculative. However, agricultural runoff may include a variety of chemicals, including pesticides, animal wastes, and fertilizers, that could threaten water quality. One study of an agricultural watershed found evidence of 38 pesticides in water samples, including 30 herbicides, 4 fungicides, 3 insecticides, and 1 metabolite of one of the herbicides (Kreuger 1998). Waterborne toxicants in agricultural runoff could directly affect development, either singly or in chemical mixtures (Burkhart et al. 2000). Agricultural runoff has been associated with impaired hatching success (De et al. 2002). Other lipophilic chemicals in runoff may also play a role--recent studies found that exposing Rana pipiens tadpoles to extracted compounds from semipermeable membrane devices in freshwater ponds could cause malformation in the presence of UV radiation (Bridges et al. 2004).
There are a number of biologic mechanisms by which chemicals in agricultural runoff could cause deformities. A recent study found an association between agricultural runoff including the herbicides atrazine, deethyl-atrazine, simazine, metolachlor, dimethenamide, chlopyralide, dicamba, and bentazone and plasma retinoid levels in Rana catesbiana (Berube et al. 2005); retinoids appear to function in signaling pathways for limb development (Stocum 2000). It is also possible that herbicides or other organic compounds could directly affect the expression of genes that help determine limb development. Because thyroid hormone has been found to protect against the development of abnormalities in the experimental setting (Fort et al. 2001), chemically induced alterations of thyroid function could potentially increase the malformation rate.
Another potential mechanism for the effect of agricultural chemicals on amphibian malformation could be through effects on either parasite population density or on host immune function leading to increased rate of parasite infection (Christin et al. 2003). Our investigation considered the possibility that parasitic infection with Ribeiroia could have played a role in the etiology of limb deformities at the study sites. However, our analysis to date does not support the parasitic infection hypothesis. Examination of individual amphibians as well as representative samples of host snails from the study sites did not reveal evidence that either this parasite or trematode infection in general was playing a role in the causation of limb malformation.
Some studies have suggested that nutrient loads such as phosphorus and nitrogen, present in some agricultural runoff, could contribute to developmental abnormality risk by contributing to eutrophication (Johnson and Chase 2004). In this sample, we had the opportunity to adjust for the effect of measured nutrients in sampled water and found that these nutrients did not remain significant predictors of malformation in the multivariate model.
There are several possible reasons why the overall rate of nontraumatic hind limb abnormality in this study sample (1.6%) was lower than figures reported for amphibian limb abnormalities in some other surveys (Burkhart et al. 2000). First, there was variation in rates of malformations between study sites, with rates in excess of 10% at some sites. The systematic nature of the present survey was designed to reduce selection bias, and most study sites were consequently selected without prior knowledge of the site-specific rate of amphibian limb abnormalities. As a result, in some locations, no abnormalities were detected. Second, we used a more restrictive case definition than many other surveys, taking care to exclude trauma-induced limb deformities, thereby lowering the overall abnormality rate. Third, rates of abnormalities fluctuate from year to year in individual wetlands, and some of the ponds sampled had experienced abnormality rates as high as 30% in previous years (Levey et al. 2003). It therefore seems likely that the variability in malformation rates between ponds was related to environmental factors.
The study relied on a limited number of measurements of water quality, as well as visual observations of land use as an indicator of potential pollution sources. Therefore, the observed associations between runoff sources, measured water quality, and malformation rate must be viewed as preliminary. Determining exposure at the level of the group rather than the individual risks the "ecologic fallacy" of assigning potential causation to one factor when in fact another, unmeasured factor is actually responsible. Although the rate of malformation in ponds near agriculture was increased, it could be that this difference was due to other factors that were not assessed. Further studies involving direct measurements of toxicants in water, and case-control comparisons of affected and unaffected individuals need to be carried out in order to identify candidate toxicants or chemical mixtures that could be investigated in the laboratory setting.
Water-quality measures are dependent on multiple factors and vary over a season and year to year depending on runoff sources, rainfall, temperature, and other factors. By using a limited number of water-quality measures taken during a single year, it is possible that some exposure misclassification occurred, with water conditions during sensitive periods of amphibian development varying from the measurements at the time of sampling. However, such misclassification, in epidemiologic studies of cause and effect, tends to be nondifferential and bias the results toward observing no effect (Checkoway and Eisen 2005). Therefore, the fact that we found strong associations between a number of exposures and the rate of malformation indicates that such associations are real and significant. The good discrimination and fit of the multivariate logistic regression model further support the strength of the observed associations.
The human health relevance of these findings remains to be determined. If a chemical toxicant or mixture could be identified that is capable of causing limb malformations in wild amphibians, several additional lines of investigation could shed light on whether a risk to humans exists. First, it would be useful to know what human health outcome would be analogous to amphibian limb deformities; this could be explored if gene sequence homology between humans and amphibians was present for target genes affected by the toxicants. Second, it would be important to establish a dose-response relationship and determine whether environmental exposures to such a toxicant would be capable of causing human health effects. Finally, epidemiologic studies including both amphibian and human populations could determine whether rates of malformation in amphibians show a correlation with a suspected human health outcome. Although to date none of these connections have been established, they will be worthy of further exploration if confirmatory studies support the role of toxicant chemicals in the etiology of amphibian developmental abnormalities.
Received 15 September 2004; accepted 11 July 2005.
Ankley GT, Diamond SA, Tietge JE, Holcombe GW, Jensen KM, Defoe DL, et al. 2002. Assessment of the risk of solar ultraviolet radiation to amphibians. I. Bose-dependent induction of hindlimb malformations in the northern leopard frog (Rana pipiens). Environ Sci Technol 36:2853-2858.
Ankley GT, Tietge JE, DeFoe DL, Jensen KM, Holcombe GW, Durhan E J, et al. 1998. Effects of ultraviolet light and methoprene on survival and development of Rana pipiens. Environ Toxicol Chem 17:2530-2542.
Berube V, Body MH, DeBlois C, Dassylva N, Spear PA. 2005. Plasma retinoid profile in bullfrogs, Rana catesbeiana, in relation to agricultural intensity of sub-watersheds in the Yamaska River drainage basin, Quebec, Canada. Aquat Toxicol 71:109-120.
Bishop CA, Mahony NA, Struger J, Ng P, Pettit K. 1999. Anuran development, density and diversity in relation to agricultural activity in the Holland River watershed, Ontario, Canada (1090-1992). Environ Monit Assess 57:21-43.
Blaustein AR, Johnson PT. 2003. Explaining frog deformities. Sci Am288(2):60-65.
Bridges C, Little E, Gardiner D, Petty J, Huckins J. 2004. Assessing the toxicity and teratogenicity of pond water in north-central Minnesota to amphibians. Environ Sci Pollut Res 11:233-239.
Burkhart JG, Ankley G, Bell H, Carpenter H, Fort D, Gardiner D, et al. 2000. Strategies for assessing the implications of malformed frogs for environmental health. Environ Health Perspect 108:83-90.
Burkhart JG, Helgen JC, Fort D J, Gallagher K, Bowers D, Propst TL, et al. 1998. Induction of mortality and malformation in Xenopus laevis embryos by water sources associated with field frog deformities. Environ Health Perspect 106:841-848.
Checkoway H, Eisen EA. 2005. Epidemiology. In: Textbook of Clinical Occupational and Environmental Medicine (Rosenstock L, Cullen MR, Brodkin CA, Redlich CA, eds). Philadelphia:Elsevier Saunders, 119-137.
Christin MS, Gendron AD, Brousseau P, Menard L, Marcogliese D J, Cyr D, et al. 2003. Effects of agricultural pesticides on the immune system of Rana pipiens and on its resistance to parasitic infection. Environ Toxicol Chem 22:1127-1133.
Collins JP, Storfer A. 2003. Global amphibian declines: sorting the hypotheses. Divers Distrib 9:89-98.
Daszak P, Cunningham AA, Hyatt AD. 2001. Anthropogenic environmental change and the emergence of infectious diseases in wildlife. Acta Trop 78:103-116.
Davidson C, Shaffer HB, Jennings MR. 2001. Declines of the California red-legged frog: climate, UV-B, habitat, and pesticides hypotheses. Ecol Appl 11:464-479.
Davidson C, Shaffer HB, Jennings MR. 2002. Spatial tests of the pesticide drift, habitat destruction, UV-B, and climate-change hypotheses for California amphibian declines. Conserv Biol 16:1588-1601.
De S, Pettit KE, Bishop CA, Cheng KM, Elliott JE. 2002. Effects of agricultural runoff on native amphibians in the Lower Fraser River Valley, British Columbia, Canada. Environ Toxicol Chem 21:353-360.
Degitz SJ, Holcombe GW, Kosian PA, Tietge JE, Durhan E J, Ankley GT. 2003. Comparing the effects of stage and duration of retinoic acid exposure on amphibian limb development: chronic exposure results in mortality, not limb malformations. Toxicol Sci 74:139-146.
Degitz SJ, Kosian PA, Makynen EA, Jensen KM, Ankley GA. 2000. Stage- and species-specific developmental toxicity of all-trans retineic acid in four native North American ranids and Xenopus laevis. Toxicel Sci 57:264-274.
Fort DJ, Propst TL, Stover EL, Helgen JC, Levey RB, Gallagher K, et al. 1999. Effects of pond water, sediment, and sediment extracts from Minnesota and Vermont, USA, on early development and metamorphosis of Xenopus. Environ Toxicol Chem 18:2305-2315.
Fort DJ, Rogers RL, Paul RR, Miller MF, Clark P, Stover EL, et al. 2001. Effects of pond water, sediment and sediment extract samples from New Hampshire, USA on early Xenopus development and metamorphosis: comparison to native species. J Appl Toxicol 21:199-209.
Gosner KL. 1960. A simplified table for staging anuran embryos and larvae. Herpetology 16:183-190.
Johnson P, Chase JM. 2004. Parasites in the food web: linking amphibian malformations and aquatic eutrophication. Ecol Lett 7:521-526.
Johnson P, Sutherland D. 2003. Amphibian deformities and Ribeiroia infection: an emerging helmithiasis. Trends Parasitol 19:332-335.
Johnson PTJ, Lunde KB, Haight RW, Bowerman J, Blaustein AR. 2001. Ribeiroia ondatree (Trematoda: Digenea) infection induces severe limb malformations in western toads (Bufo boreas). Can J Zool 79:370-379.
Johnson PT J, Lunde KB, Thurman EM, Ritchie EG, Wray SN, Sutherland DR, et al. 2002. Parasite (Ribeiroia ondatrae) infection linked to amphibian malformations in the western United States. Ecol Monogr 72:151-168.
Kreuger J. 1998. Pesticides in stream water within an agricultural catchment in southern Sweden, 1990-1996. Sci Total Environ 216:227-251.
LaClair J J, Bantle JA, Dumont J. 1908. Photoproducts and metabolites of a common insect growth regulator produce developmental deformities in Xenopus. Environ Sci Technol 32:1453-1461.
Levey R, Shambaugh N, Fort D, Andrews J. 2003. Investigations into the Causes of Amphibian Malformations in the Lake Champlain Basin of New England. Waterbury, VT:Vermont Department of Environmental Conservation. Linder G, Krest SK, Sparling D, eds. 2001. Amphibian Decline: An Integrated Analysis of Multiple Stressor Effects. Pensacola, FL:Society of Environmental Toxicology and Chemistry (SETAC).
McCallum ML, Trauth SE. 2003. A forty-three year museum study of northern cricket frog (Acris crepitans) abnormalities in Arkansas: upward trends and distributions. J Wildl Dis 39:522-528.
Meteyer CU, Loeffler IK, Fallon JF, Converse KA, Green E, Helgen JC, et al. 2000. Hind limb malformations in free-living northern leopard frogs (Rana pipiens) from Maine, Minnesota, and Vermont suggest multiple etiologies. Teratology 62:151-171.
Mizgireuv I, Flax N, Borkin L J, Khudoley VV. 1904. Dysplastic lesions and abnormalities in amphibians associated with environmental conditions. Neoplasma 31:175-181.
Ouellet M. 2000. Amphibian deformities: current state of knowledge. In: Ecotoxicology of Amphibians and Reptiles (Sparling DW, Linder G, Bishop CA, eds). Pensacola, FL: Society of Environmental Toxicology and Chemistry (SETAC), 617-646.
Ouellet M, Bonin J, Rodrigue J, DesGranges J, Lair S. 1997. Hindlimb deformities (ectromelia, ectrodactyly) in free living anurans from agricultural habitats. J Wildl Dis 33:95-104.
Rabinowitz PM, Cullen M, Lake H. 1099. Wildlife as sentinels for human health hazards: a review of study designs. J Environ Med 1:217-223.
Ray N, Lehmann A, Joly P. 2002. Modeling spatial distribution of amphibian populations: a GIS approach based on habitat matrix permeability. Biodivers Conserv 11:2143-2165.
Stocum DL. 2000. Frog limb deformities: an "eco-devo" riddle wrapped in multiple hypotheses surrounded by insufficient data. Teratology 62:147-150.
U.S. Geological Survey. 1099. LandLandcov_NLCDVT: Vermont Land Cover Data Set 1902. U.S. Geological Survey. Vermont Center for Geographic Information. Available: http://www.vcgi.org/ [accessed 10 February 2004].
van der Schalie WH, Gardner HS, Bantle JA, De Rosa CT, Finch RA, Reif JS, et al. 1999. Animals as sentinels of human health hazards of environmental chemicals. Environ Health Perspect 107:309-315.
Brynn Taylor, (1,2,3) David Skelly, (1) Livia K. Demarchis, (1) Martin D. Slade, (2) Deron Galusha, (2) and Peter M. Rabinowitz (2)
(1) School of Forestry and Environmental Studies, Yale University, New Haven, Connecticut, USA; (2) Occupational and Environmental Medicine Program and (3) Department of Epidemiology and Public Health, Yale University School of Medicine, New Haven, Connecticut, USA
Address correspondence to P.M. Rabinowitz, Yale University School of Medicine, Occupational and Environmental Medicine Program, 135 College St., New Haven, CT 06510 USA. Telephone: (203) 785-5885. Fax: (203) 785-7391. E-mail: firstname.lastname@example.org
We thank the field and laboratory research staff: S. Bolden, N. Cothran, B. Fellman, K. Freidenberg, N. Freidenfelds, and N. Rabinowitz. M.R. Cullen provided assistance with study design and analysis. M. Hines of the U.S. Geological Survey assisted with the geographic information system coding of land use. R. Levey provided critical logistical support and advice.
This study was funded in part by the National Institutes of Health/National Science Foundation Ecology of Infectious Diseases Program (National Institute of Environmental Health Sciences grant 5R01 ES011067).
The authors declare they have no competing financial interests.
Table 1. Characteristics of the study population (n= 5,264). Species No. (%) Gosner stage Malformation (mean [+ or -] [n(%)] SD) Hyla versicolor 235 (4.5) 36.0 [+ or -] 6.4 4 (1.7) Pseudacris crucifer 895 (17.0) 34.8 [+ or -] 6.2 6 (0.7) Total hylids 1,130 (21.5) 35.0 [+ or -] 6.2 10 (0.9) Rana catesbeiana 319 (6.1) 37.7 [+ or -] 6.7 5 (1.6) Rana clamitans 1,176 (22.3) 40.3 [+ or -] 6.2 32 (2.7) Rana pipiens 1,702 (32.3) 35.8 [+ or -] 8.0 33 (1.9) Rana sylvatica 937 (17.8) 31.7 [+ or -] 5.2 3 (0.3) Total ranids 4,134 (78.5) 36.3 [+ or -] 7.5 73 (1.8) Total 5,264 (100) 36.0 [+ or -] 7.2 83 (1.6) Malformation type (a) Species Missing Malformed Extra Hyla versicolor 1 3 0 Pseudacris crucifer 3 3 0 Total hylids 4 6 0 Rana catesbeiana 2 3 0 Rana clamitans 9 28 2 Rana pipiens 10 28 0 Rana sylvatica 0 3 0 Total ranids 21 62 2 Total 25 68 2 (a) Some individuals exhibited more than one type of malformed limb or element. Table 2. Exposure assessment for study sites (n = 42). Characteristic Exposure Proximity to pollution sources [n (%)] Agriculture nearby or adjacent 17 (40.5) Lawn nearby or adjacent 15 (35.7) Water-quality measures pH 7.6 [+ or -] 0.9 (5.7-9.7) Conductivity ((micro)S) 303.3 [+ or -] 307.8 (10-1,350) Dissolved oxygen (mg/L) 6.5 [+ or -] 3.4 (1.2-18.3) Temperature ([degrees]C) 21.2 [+ or -] 3.6 (12.8-29.1) Total nitrogen (mg/L) 0.8 [+ or -] 0.8 (0.1-5.4) Total phosphorus (mg/L) 0.2 [+ or -] 0.4 (0.004-2.2) [micro]S, micro-Siemens. Values shown are mean [+ or -] SD (range) except where indicated. Table 3. Risk factors for nontraumatic limb malformation. Bivariate analysis Risk factor OR (95% CI) p-Value Characteristic Gosner stage 1.20 (1.14-1.26) <0.0001 Genus (Rana vs. Hyla) 2.01 (1.04-3.91) 0.04 Proximity to pollution sources Agriculture (nearby or adjacent) 3.08 (1.96-4.85) <0.0001 Septic system or lawn adjacent 2.06 (1.34-3.19) <0.001 Water-quality measures Conductivity ([micro]S) 1.00 (1.00-1.00) 0.46 Dissolved oxygen (mg/L) 1.14 (1.06-1.23) <0.001 Temperature ([degrees]C) 1.05 (0.98-1.13) 0.14 Total nitrogen (mg/L) 1.22 10.91-1.63) 0.18 Multivariate model (a) Risk factor OR (95% CI) p-Value Characteristic Gosner stage 1.18 (1.13-1.24) -0.0001 Genus (Rana vs. Hyla) -- -- Proximity to pollution sources Agriculture (nearby or adjacent) 2.26 (1.42-3.58) -0.001 Septic system or lawn adjacent -- -- Water-quality measures Conductivity ([micro]S) -- -- Dissolved oxygen (mg/L) -- -- Temperature ([degrees]C) -- -- Total nitrogen (mg/L) -- -- [micro]S, micro-Siemens. (a) Certain variables were removed from the model during backward selection modeling (--; exclusion criteria, p > 0.05).
|Printer friendly Cite/link Email Feedback|
|Author:||Rabinowitz, Peter M.|
|Publication:||Environmental Health Perspectives|
|Date:||Nov 1, 2005|
|Previous Article:||Distribution of brevetoxin (PbTx-3) in mouse plasma: association with high-density lipoproteins.|
|Next Article:||Framing scientific analyses for risk management of environmental hazards by communities: case studies with seafood safety issues.|