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Summary There is growing concern of exposure of fish, wildlife and humans to water sources contaminated with oestrogens and the potential impact on reproductive health. Environmental oestrogens can come from various sources including concentrated animal feedlot operations (CAFO), municipal waste, agricultural and industrial effluents. US EPA’s drinking water contaminant candidate list 3 (CCL3) includes several oestrogenic compounds. Although these contaminants are currently not subject to any proposed or promulgated national primary drinking water regulations, they are known or anticipated to occur in public water systems and may require future regulation under the Safe Drinking Water Act. Using an in vitro transcriptional activation assay, this study evaluated oestrogens from CCL3 both individually and as a seven oestrogen mixture (fixed ray design) over a broad range of concentrations, including environmentally relevant concentrations. Log EC50 and Hillslope values for individual oestrogens were as follows: estrone, −11.92, 1.283; estradiol-17α, −9.61, 1.486; estradiol-17β, 11.77, 1.494; estriol, −11.14, 1.074; ethinyl estradiol-17α, −12.63, 1.562; Mestranol, −11.08, 0.809 and Equilin, −11.48, 0.946. In addition, mixtures that mirrored the primary oestrogens found in swine, poultry and dairy CAFO effluent (fixed-ratio ray design), and a ternary mixture (4 × 4 × 4 factorial design) of oestrogens found in hormone replacement therapy and/or oral contraceptives were tested. Mixtures were evaluated for additivity using both the concentration addition (CA) model and oestrogen equivalence (EEQ) model. For each of the mixture studies, a broad range of concentrations were tested, both above and below environmentally relevant concentrations. Results show that the observed data did not vary consistently from either the CA or EEQ predictions for any mixture. Therefore, either the CA or EEQ model should be useful predictors for modelling oestrogen mixtures.

The expression of estrogen receptors, ESR1 (ERα) and ESR2 (ERβ), and androgen receptors (AR) in the thyroid gland has been reported in few vertebrate species other than a few mammals. This study reports the presence of sex steroid hormone receptors and thyroid receptors (ERα, ERβ, AR, TRα, and TRβ) in the thyroid gland of the American alligator at several life stages. It provides a semiquantification and distribution of ERα in the thyroid follicle cells using an immunohistochemical approach as well as reports quantitative differences in mRNA expression of ERα, ERβ, TRα, TRβ, and AR in the same tissue using quantitative real time-PCR (Q-PCR) with primers designed specifically for alligators. The thyroid tissue of the American alligator expresses ERα, ERβ, and AR at all of the life stages examined here although no statistically significant differences were observed between male and female in thyroid mRNA expression for any of the genes analyzed. No sexual dimorphism was observed in ERα immunostaining. No statistical analysis across life stages were performed due to confounding factor of season.

Morphological differences in spleen and thymus are closely related to functional immune differences. Hormonal regulation of the immune system has been demonstrated in reptilian splenic and thymic tissue. Spleens and thymus were obtained from juvenile alligators at two reference sites in Florida, USA: Orange Lake and a National Wildlife Refuge, Lake Woodruff, as well as from a contaminated lake, Lake Apopka. Lake Apopka has been extensively polluted with agricultural pesticides. Tissues were prepared for histological analysis to determine if previously detected endocrine abnormalities associated with contaminant exposure might also be reflected in morphological differences in splenic and thymic structures important for immunological response. Similar tissues were taken from captive-raised juvenile female alligators (3 years old) that were hatched from eggs collected on Lake Woodruff and Lake Apopka. Differences in thymic ratios (medulla/cortex) were found among alligators collected from the two lakes (P = 0.0051). Alligators from Lake Apopka had smaller thymic ratios than animals from either reference lake. Males from Lake Woodruff had significantly smaller lymphocyte sheaths in the spleen than females (P = 0.0009), indicative of a normal sexual dimorphism. Lymphocyte sheath width differed among females obtained from the three lakes, with females from Lake Apopka having the smallest sheath width and those from Orange Lake having the largest. Malpighian body area was largest in alligators from Orange Lake, intermediate in Lake Woodruff, and smallest in Lake Apopka. In contrast to that observed for wild-caught animals, no difference was found in the thymic medulla/cortex ratio of captive-raised female alligators (P = 0.378). Captive-raised female alligators from Lake Apopka and Lake Woodruff displayed lake-associated differences in lymphocyte sheath width as observed in wild animals; Lake Apopka alligators had smaller lymphocyte sheath width compared to Woodruff alligators (P = 0.0396). In contrast to wild-caught animals, area of the Malpighian bodies did not differ by lake in the captive-raised female alligators (P = 0.066). The enlarged thymic cortex suggests a change in T-lymphocyte maturation within the thymus of alligators from a contaminated environment, Lake Apopka. The results point to alterations in the histology of the thymus and spleen. Further studies are required to examine the functional significance of these observations.

We examined variation in plasma thyroxine (T 4 ) in juvenile American alligators (Alligator mississippiensis) collected from three sites within the Kissimmee River drainage hasin (FL, USA). Based on historical sediment data, Moonshine Bay served as the low contaminant exposure site, Water Conservation Area 3A served as an intermediate contaminant exposure site, and Belle Glade served as the high contaminate exposure site. In May 1999, alligators (n= 22) from Water Conservation Area 3A exhibited higher T 4 concentrations than animals from both Belle Glade (n= 22; p=0.0003) and Moonshine Bay (n = 33; p = 0.001). In May 2000, alligators (n = 29) Water Conservation Area 3A again exhibited higher T, concentrations than those from Belle Glade (n = 49; p = 0.02) but not those from Moonshine Bay (n = 40). No sexual dimorphism was observed among mean T 4 concentrations within any of the sites during either year (p > 0.05). Animals within all sites exhibited higher T 4 concentrations in May 2000 when compared to May 1999. When variance was examined, animals from Water Conservation Area 3A exhibited higher variance in plasma T 4 concentrations than those from either Moonshine Bay or Belle Glade. We concluded that mean plasma T 4 concentrations did not match the sediment contaminant mixture data presently available to us, whereas variance seems to he a more reliable indicator of contaminant exposure.