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Experimental Evaluation of Vitellogenin as a Predictive Biomarker for Reproductive Disruption.

Vitellogenin (VTG) synthesis in male oviparous vertebrates is used as an indicator of environmental estrogen exposure, but the relationship between elevated VTG levels and the effects of environmental estrogens on reproductive success are poorly understood. To examine whether altered VTG expression predicts reproductive impairment, we exposed medaka (Oryzias latipes) for 2 or 8 weeks posthatch to 0, 0.5, 1.0, 2.5, and 7.5 ppb of the environmental estrogen o,p'-DDT. Fish were sampled 2, 4, and 8 weeks after hatch to examine VTG expression and gonad development. After exposure, fish were transferred to clean water, grown to sexual maturity, and placed in mating pairs. We collected eggs for 7 days and scored them for fecundity (number of eggs), fertility (percent fertilized), and hatching success (percent hatched). DDT had no effect on VTG expression after a 2-week exposure, whereas all doses induced VTG after 8 weeks. At both exposure durations, the highest doses of DDT caused a female-skewed sex ratio in adults. Gonadal feminization appeared to be progressive: some ovotestes were observed after 2- or 4-week exposure to the two highest doses, but the proportion of ovaries increased after 8 weeks. Both 2- and 8-week exposures significantly reduced fertility and hatching success at all doses, with lower doses having a greater effect after longer exposure. Fertility and hatching success were more sensitive to estrogenic disruption than were gonad differentiation and vitellogenin expression. We suggest that VTG expression may be interpreted as a warning of reproductive consequences, but absence of expression cannot be interpreted as absence of consequences. Key words, endocrine disruption, fish, medaka, reproductive success, sex differentiation, vitellogenesis. Environ Health Perspect 109:681-690 (2001). [Online 25 June 2001] http://ehpnet1.niehs.nih.gov/docs/2001/109p681-690cheek/abstract.html

The significance of endocrine disruption for population and ecosystem health is an important issue in contemporary environmental science. Endocrine disruption is defined as the perturbation of endogenous hormone function by exogenous chemicals. Endogenous sex steroid hormones may have two broad categories of influence on physiologic systems: organization and activation (1,2). Organizational effects are usually permanent changes in morphology that persist after the hormone stimulus is removed and that affect subsequent function and behavior. Activational effects are usually transient changes in morphology, function, and behavior that disappear when the hormone stimulus is removed. Classically, the organizational effects of sex steroid hormones include sex-specific morphologic differentiation of the gonads and brain. Activational effects of sex steroids in vertebrates include seasonal gonadal recrudescence and onset of breeding coloration and behavior (1,2). Both categories of action are essential for normal reproduction.

Endocrine disruption can alter both the organizational and activational effects of reproductive hormones, possibly having a profound effect on an organism's ability to reproduce and therefore on its fitness. Environmental contaminants can have organizational effects on sex differentiation and on expression of secondary sex characteristics in a variety of vertebrates (3-17). In addition, numerous studies have documented the activational effects of exogenous chemicals on levels of sex steroid hormones and on hormone-mediated protein synthesis (12, 18-36). The implicit proposition in many of these studies is that the more easily measured activational effects such as hormone and protein levels can be used as biomarkers of the potential organizational effects such as altered gonad morphology. However, in most cases, the effects of contaminants on reproductive capability are not known, nor are the relative sensitivities of the organizational and activational responses known. To understand the impact of endocrine disruption on natural populations, we must begin to analyze the relative sensitivity of these responses, giving particular attention to quantifying the consequences for individual fitness, that is, offspring production.

Although several classes of endocrine-disrupting agents have been identified, including environmental estrogens, antiestrogens, androgens, antiandrogens, antiprogestins, and retinoid mimics (37-39), environmental estrogens have been most thoroughly studied. Fish have been a particularly popular model for studying estrogenic endocrine disruption because both males and females produce vitellogenin (VTG), the precursor to egg yolk proteins, in response to estrogen or estrogen mimics (40). VTG production is nonexistent to low in males and immature females, whereas mature female fish have a seasonal cycle of serum VTG levels, with peak values reaching tens of milligrams per milliliter (40). In mature females, vitellogenesis is under hormonal regulation by estradiol, the major endogenous estrogen in all vertebrates. Increasing titers of estradiol stimulate the liver to produce VTG, which is then transported in the bloodstream to the ovary. VTG enters the oocyte via specific receptor-mediated endocytosis (41). Once inside the oocyte, VTG is cleaved into the smaller yolk proteins (phosvitin, lipovitellin, and beta-component), which accumulate in yolk globules or granules (42).

Because of the specific association between VTG synthesis and estrogen stimulation and because of the low background production of this protein in all but mature females, VTG is a highly specific biomarker for estrogen exposure in fish. Exposure to several classes of chemicals and chemical mixtures is known to alter fish vitellogenesis in vivo, including the alkylphenols nonylphenol and octylphenol, the steroidal estrogen ethinylestradiol, the pesticides methoxychlor and o,p'-DDT and their metabolites, phytoestrogens, and sewage effluent (34,35,39,43). Direct activation of vitellogenesis in hepatic cell culture also occurs in response to some environmental estrogens, including alkylphenols, o,p'-DDT, Aroclor 1254 (a polychlorinated biphenyl mixture), bisphenol A, chlordecone, lindane, and phytoestrogens, although sensitivity appears to vary depending upon the donor species (40,44-46).

Although alterations in vitellogenesis have been well documented in vivo and in vitro, the effects of environmental estrogens on sex differentiation in fish have only recently been investigated. Alkylphenol exposure caused feminization of the testis in medaka [Oryzias latipes (8,9)] and carp [Cyprinus carpio (7)] and reduced testis and ovary growth in juvenile rainbow trout [Oncorhynchus mykiss (47,48)]. o,p'-DDT also caused feminization in medaka, either by immersion exposure of fry (11) or by injection into fertilized eggs (10). However, neither the o,p' nor p,p' isomer of DDE altered sex differentiation in juvenile rainbow trout (49). Vinclozolin, a fungicide with antiandrogen action in mammals, showed no effect on fathead minnow (Pimephales promelas) ovarian or testicular development (50).

Recently, the effects of natural and environmental estrogens on reproductive success (number of offspring produced) have been investigated in laboratory exposures of adult males. Estradiol exposure of adult males caused decreased hatching success in medaka (51) and in fathead minnows (52). Octylphenol and bisphenol A also reduced male fertility (percent fertilized) and embryo survivorship in medaka mating trials (51,53). Very few studies in fish have examined the effects of developmental exposure to environmental estrogens on subsequent reproductive success, and no studies have yet addressed the link between vitellogenin induction, sex differentiation of exposed fish, and reproductive success.

This study addresses two issues: the effects of developmental estrogen exposure on individual fitness (number of offspring) and the utility of VTG as a predictive biomarker for altered sexual development and impaired reproduction. We predict that developmental exposure to environmental estrogens will have an organizational or permanent effect on gonad morphology and reproductive function, but that it will have an activational or transitory effect on VTG production (i.e., exposed animals will produce VTG only while the stimulus is present). If this is the case, VTG serves as an excellent biomarker of current estrogenic exposure, but it may not indicate organizational effects such as altered sex differentiation and impaired reproductive function.

We exposed developing medaka to o,p'-DDT for 2 or 8 weeks posthatch and examined the effects of exposure on VTG synthesis, sex differentiation, and reproductive success. We used medaka as a model because they are easily maintained in the laboratory and are known to be sensitive to environmental estrogens (8-11,53,54). We chose to use o,p'-DDT as a model environmental estrogen for several reasons. First, although DDT use was banned in the United States in 1973, DDT isomers and metabolites are extremely stable and are globally distributed at concentrations ranging from 0 to 10 ppm (55). Second, o,p'-DDT is known to be a relatively potent environmental estrogen in frogs (56), turtles (57), birds (58), and mammalian cells (59). Finally, recent work has shown that o,p'-DDT feminizes developing male medaka (10, 11).

In this study we show that o,p'-DDT is estrogenic in medaka: it stimulates VTG synthesis in juveniles and adults, feminizes developing males, and reduces reproductive success. However, VTG expression was the least sensitive physiologic response to estrogenic endocrine disruption.

Methods

Animals. Adult medaka were taken from the broodstock at the University of Southern Mississippi Institute of Marine Sciences. Broodstock were maintained in glass aquaria submerged in a central water bath and held at 25 [degrees] C with a 16 hr light:8 hr dark photoperiod. Fish were fed dry flake food three times daily and brine shrimp nauplii twice weekly. Mating groups were maintained at 27 [degrees] C in individual mating chambers within a raceway receiving a continuous flow of well water. Females were examined daily, and egg clusters were collected and placed in embryo rearing medium (0.1% NaCl, 0.003% KCl, 0.004% [CaCl.sub.2] [multiplied by] [2H.sub.2]O, and 0.016% [MgSO.sub.4] [multiplied by] [7H.sub.2]O; Carolina Biological, Burlington, NC). Upon hatching, fry were immediately transferred to exposure aquaria.

Experimental design. Gonadal differentiation in medaka occurs within the first 2 weeks after hatch and is sensitive to exogenous steroid hormones, including estrogens (60). To determine whether exposure to an environmental estrogen during the period of sex differentiation is sufficient to alter gonadal development and reproductive capacity, we treated fry throughout the period of sex differentiation (2 weeks posthatch) and then transferred them to well water. At 2, 4, and 8 weeks posthatch, 12 fish were sacrificed from each treatment, 6 for analysis of VTG expression and 6 for examination of gonad histology. Because sampling required several hours, treatments were processed in random order, and time of sampling was recorded in order to avoid confounding time-of-day effects with treatment effects. At sexual maturity (16 weeks posthatch), fish were placed in mating pairs. Three categories of mating pairs were established for each dose of DDT: exposed female x solvent control male (n = 6 pairs per dose), exposed male x solvent control female (n = 6 pairs per dose), and exposed male x exposed female (n = 6 pairs per dose). At the end of a 7-day mating trial, adults were sacrificed for analysis of VTG expression and gonad histology. As above, treatments were processed in random order.

To more closely approximate the lifelong exposure that nonmigratory fish potentially experience in the natural environment, fry were treated from hatch through early puberty (8 weeks posthatch), then transferred to well water. As in the previous experiment, 12 fish were sacrificed at 2, 4, and 8 weeks posthatch for analysis of VTG expression and gonad histology. At sexual maturity (12 weeks posthatch), adults were placed in mating pairs as described above. Adults were sacrificed for analysis of VTG and gonad histology at the end of the mating trial.

Fish care and treatment were in accordance with all guidelines of the Southeastern Louisiana University and University of Southern Mississippi Animal Care and Use Committees.

Exposure conditions. In both treatment paradigms, fry were exposed to well water, solvent (triethylene glycol), or 0.5, 1, 2.5, or 7.5 mg/L (ppb) o,p'-DDT in a flow-through system. Water was particle and carbon filtered, temperature adjusted, and aerated before entering test aquaria. The flow rate was maintained at 100 L/aquarium/day in an intermittent flow-through chamber similar to that described by Walker et al. (61). Aquaria were housed in a heated recirculating water bath at 27 [+ or -] 1 [degrees] C on a 16 hr light:8 hr dark photoperiod. The time weighted mean and SD of temperature, dissolved oxygen, and pH were 27.1 [+ or -] 0.5 [degrees] C, 6.5 [+ or -] 1.7 mg/L, and 9.0 [+ or -] 0.2, respectively.

Treated and water control fry were exposed in duplicate 20-L aquaria (45 fry/aquarium), and solvent control fry were exposed in quadruplicate 20-L aquaria (45 fry/aquarium). Within each aquarium, fry were housed in a 1.5-L cylindrical mesh container to protect against physical damage and to allow more efficient foraging until 3 weeks of age, when they were released into the aquarium. Fry were fed microworms until day 3, microworms once and brine shrimp nauplii twice daily until day 6, and AquaTox Special dry flakes (Ziegler Bros, Gardner, PA) once and brine shrimp nauplii twice daily from day 7 to day 58. From day 57 to termination, fish were fed dry flakes three times and brine shimp nauplii once daily.

Chemical analysis. We purchased DDT from Lancaster Synthesis Inc. (Windham, NH) and measured DDT concentrations using gas chromatography with electron capture detection (GC/ECD). DDT was concentrated by solid phase extraction before analysis. Extraction efficiency ranged from 91 to 104%. Actual doses were 50-80% of the nominal dose (Table 1) and are shown in all figures and tables.
Table 1. Nominal and measured doses of o,p'-DDT
in exposure aquaria (mean [+ or -] SEM).

 Actual dose ([micro]g/L)
Nominal 2-Week 8-Week
dose ([micro]g/L) exposure exposure

0.5 0.23 [+ or -] 0.02 0.30 [+ or -] 0.02
1.0 0.50 [+ or -] 0.03 0.69 [+ or -] 0.03
2.5 1.37 [+ or -] 0.12 1.94 [+ or -] 0.09
7.5 4.32 [+ or -] 0.23 5.19 [+ or -] 0.18


Vitellogenin analysis. Fish smaller than 90 mg were euthanized in ice-cold MS-222 (0.1 mg/mL) and homogenized in ice-cold phosphate-buffered saline (pH 7.3) supplemented with 20 [micro]M leupeptin, 1 mM phenylmethyl sulfonyl fluoride (PMSF), 5 mM dithiothreitol, and 5 [micro]g/mL aprotinin. The homogenate was immediately mixed with aprotinin [0.021 trypsin-inhibiting units (TIU)/100 [micro]L homogenate]. Fish larger than 90 mg were bled by cutting a gill arc and collecting the blood into a heparinized microcapillary tube. Aprotinin (1 [micro]L of 4.2 TIU/mL) was immediately added to whole blood samples. Both homogenates and blood were centrifuged at 13,800 x g for 5 min at 4 [degrees] C, and the supernatant was aspirated and stored at -80 [degrees] C until analysis.

We diluted homogenate and plasma samples in Laemmli sample buffer (100-fold for plasma samples and to 0.5 [micro]g total protein per well for homogenates) and separated proteins by SDS-PAGE at 120 V for 2 hr. Proteins were electroblotted (45 V for 2 hr) to a polyvinylidene difluoride membrane. We detected VTG using a monoclonal fish vitellogenin antibody obtained from Nancy Denslow (University of Florida, Gainesville, FL) (62). VTG was visualized using the Vectastain ABCAmP kit (Vector Laboratories, Burlingame, CA) and quantified by densitometry using a BioRad gel documentation system and Quantity One software (BioRad, Hercules, CA). The density of all samples was normalized to micrograms protein per well (homogenates) or microliter equivalents of plasma per well. We then calculated the relative VTG score as the ratio of normalized sample density to normalized standard density. The standard consisted of pooled plasma from vitellogenic female medaka. Both microliter equivalents and microgram protein were known for the standard, allowing comparison with plasma samples and homogenate samples.

Histologic examination. Fish were fixed in 10% buffered formalin, embedded in paraffin, sectioned longitudinally, and stained with hematoxylin and eosin for analysis of gonad structure. We categorized a gonad as an ovotestis if both sperm tubules and oocytes were present. Gonad maturity scores were assigned to adult male and female gonads. Scores were based on stages of oogenesis and spermatogenesis defined by Wallace and Selman (42) and Grier (63), respectively. Males were scored as follows: 1 if only spermatogonia were present; 2 if mostly spermatogonia were present, with some cysts of spermatids; 3 if sperm-filled cysts and tubules occupied [is less than] 50% of sectioned area; or 4 if sperm-filled cysts and tubules occupied [is greater than] 50% of section area. Females were scored as follows: 1 if only primary oocytes were present; 2 if primary oocytes and early yolk vesicle stage oocytes were present; 3 if primary oocytes, early yolk vesicle oocytes, and approximately 50% late yolk vesicle oocytes were present; or 4 if mostly late yolk vesicle oocytes and vitellogenic oocytes were present.

Quantification of reproductive success. The two groups of fry used in the 2- and 8-week exposures differed in time to reach sexual maturity, taking 16 and 12 weeks, respectively. Maturity was judged by the presence of distinct secondary sex characteristics. In both experiments, sex ratio at maturity was determined by examination of secondary sex characteristics, and fish were divided into three types of mating groups: female exposed x control male (female), male exposed x control female (male), and female exposed x male exposed (both). This design allowed us to determine whether DDT had differential effects on female and male reproductive success and whether exposure of both partners caused more or less damage than exposure of only one partner.

We quantified reproductive success of each pair during a 7-day mating trial. We used three parameters to assess reproductive success: number of eggs per pair, percentage of eggs fertilized, and percentage of embryos that hatched and survived 72 hr. Number of eggs is a measure of fecundity and serves as an estimate of the effects of both male and female exposure on female reproductive success. Male exposure could potentially alter male pheromone production and responsiveness, thereby altering the pheromonal and behavioral cues received by females. Females could possibly respond by changing egg production. The percentage of fertilized eggs serves as a measure of male fertility (when the male is exposed) and female fertility (when the female is exposed). Finally, the percentage of embryos that hatch serves as an estimate of individual fitness (number of offspring produced). At the end of the reproductive trials, adults were sacrificed for analysis of VTG and examination of the gonads.

Statistics. We compared survival (percent that survived) of treated fish to survival in triethylene glycol and water control groups by [chi square] analysis. We analyzed size (milligrams wet weight) relative to dose and age and VTG score relative to dose and age by two-way analysis of variance (ANOVA). To examine time-of-day effects, we analyzed adult female VTG scores over the course of the sampling day by one-way ANOVA. To evaluate the effects of developmental DDT exposure on adult VTG synthesis, adult male and female VTG scores relative to dose were analyzed by separate one-way ANOVAs. Because of the small subsample taken at each time point (n = 6), statistical analysis of the ratio of ovaries, testes, undifferentiated gonads, and ovotestes could not be performed. However, this cross-sectional sampling allowed investigation of the process of gonad differentiation in 2- to 8-week-old fish. These results were supported by histologic and statistical analyses of adult sex ratio. Differences between the sex ratio of exposed adults and the expected 1:1 sex ratio were identified by [chi square] analysis. We analyzed changes in gonad maturity scores relative to time of day and dose by the Kruskal-Wallis test. Changes in reproductive parameters within a type of mating group (female only treated, male only treated, both treated) were analyzed by one-way ANOVA (main effect = DDT dose) followed by Dunnett's post hoc test to identify treatments that differed significantly from solvent controls. Correlations between percent hatched and VTG score were examined via simple regression. All values expressed as percentages were arcsine (square root) transformed before analysis. In all tests, [Alpha] was set at 0.05.

Results

Survival and growth. Solvent (triethylene glycol) had no effect on survival, but DDT treatment significantly reduced survival to sexual maturity in both experiments (Figure 1). DDT doses [is greater than or equal to] 0.50 [micro]g/L significantly reduced survival in the 2-week exposure, whereas doses of 0.30, 1.94, and 5.19 [micro]g/L, but not 0.69 [micro]g/L, reduced survival in the 8-week exposure. DDT treatment appeared to significantly alter growth in both the 2- and 8-week exposures (two-way ANOVA, 2-week [F.sub.time] = 862.36, p [is less than] 0.0001; 8-week [F.sub.time] = 471.66, p [is less than] 0.0001; 2-week [F.sub.DDT] = 5.49, p [is less than] 0.0001; 8-week [F.sub.DDT] = 12.18, p [is less than] 0.0001; 2-week [F.sub.time x DDT] = 2.876, p = 0.0003; 8-week [F.sub.time x DDT] = 5.112, p [is less than] 0.0001). In both exposures, fish were larger in DDT treatment groups where survivorship was lower, suggesting that density, not DDT, directly affects size. However, the highest dose of DDT in the 8-week exposure drastically decreased both survivorship and size, suggesting that long-term exposure to 5.19 [micro]g/L DDT is extremely toxic.

Vitellogenin synthesis. DDT did not cause any significant change in VTG production in juvenile (2 to 8 weeks posthatch) or adult fish (17 weeks posthatch) exposed for 2 weeks posthatch (Figure 2). VTG expression did increase over time, as expected with the onset of sexual maturity. When fry were continuously exposed to DDT for 8 weeks posthatch, VTG production was induced in a dose- and time-dependent manner (Figure 3). Once exposure ended at 8 weeks posthatch, VTG production was attenuated. Sexually mature fish (13 weeks posthatch) produced VTG, but not at the same levels as during DDT stimulation. Neither 2- nor 8-week developmental exposure to DDT induced significant VTG production in adult males, nor did it alter adult female VTG production (Figure 2B and Figure 3B). VTG synthesis in adult females did not change significantly over the 8-hr sampling period, indicating that vitellogenesis is a constant process in this daily spawning fish.

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Sex differentiation. Developmental exposure to DDT caused a female-skewed sex ratio in adults (Figure 4). When exposure occurred during the first 2 weeks posthatch, only the highest dose (4.32 [micro]g/L) caused feminization (Figure 4). When fry were exposed for 8 weeks posthatch, both the 1.94 and 5.2 [micro]g/L doses caused a significantly female-skewed sex ratio (Figure 4). Cross-sectional sampling of exposed fry (n = 6 individuals per dose per sampling time) suggested that feminization was a progressive process. In fry exposed for 2 weeks posthatch (Figure 5), gonadal differentiation was not clearly distinguishable by light microscopy until 4 weeks posthatch. By 4 and 8 weeks, we observed a disproportionate number of ovaries in fry exposed to the highest doses of DDT (Figure 5). In some fry exposed for 8 weeks posthatch (Figure 6), ovotestes appeared after 2 and 4 weeks of exposure to the highest doses of DDT, whereas after 8 weeks only ovaries were observed (Figure 6). However, two males exposed to 1.94 [micro]g/L DDT and sampled at sexual maturity (13 weeks) had ovotestes, suggesting that incomplete feminization occurred in these fish. These observations strongly suggest that o,p'-DDT-induced feminization is due to gonadal reorganization and not to differential mortality of DDT-exposed male fish.

[GRAPHS OMITTED]

Gonadal condition of adults. Although DDT caused a significantly female-skewed sex ratio at the highest doses, ovarian and testicular morphology of adults did not differ between DDT-treated fish and control fish. Neither testis nor ovary maturity scores varied significantly with DDT treatment in either the 2- or 8-week exposure (data not shown). Essentially, adult ovaries and testes appeared to be normal. However, two "males" exposed to 1.94 [micro]g/L DDT for 8 weeks had ovotestes. In one of these individuals, a few primary oocytes were scattered throughout the testis, but no mature sperm were present and this fish did not fertilize any eggs. In the other animal, approximately 50% of the gonad contained both primary and early yolk vesicle oocytes, but a few cysts of mature sperm were present (Figure 7) and this individual was able to fertilize eggs.

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Reproductive success. Developmental exposure to DDT had a relatively small impact on female fecundity (egg number). After a 2-week developmental exposure, the highest doses of DDT (1.37 and 4.32 [micro]g/L) reduced fecundity of exposed females, but not of control females mated with exposed males (Table 2). The highest dose also reduced fecundity of pairs with both partners exposed, indicating that the effect on female fecundity is probably due to a direct action of DDT on ovaries. After an 8-week developmental exposure, so few individuals (n = 2 females) survived the highest DDT dose (5.19 [micro]g/L) that no mating pairs could be tested. Regardless of whether the female, male, or both partners were exposed, doses [is less than or equal to] 1.94 [micro]g/L did not reduce female fecundity (Table 2). Instead, 0.69 [micro]g/L DDT significantly enhanced egg number in exposed females mated with control males.
Table 2. Effect of DDT exposure of females and males on female
fecundity (number of eggs).

 No. of eggs
Exposure DDT Exposed
duration ([micro]g/L) female

2 Weeks 0 59.0 [+ or -] 6.3
 0.23 52.8 [+ or -] 5.5
 0.50 41.3 [+ or -] 5.2
 1.37 34.0 [+ or -] 9.3(*)
 4.32 35.8 [+ or -] 4.7(*)
8 Weeks 0 33.3 [+ or -] 4.6
 0.30 52.7 [+ or -] 5.4
 0.69 58.0 [+ or -] 7.8(*)
 1.94 47.6 [+ or -] 8.1

 No. of eggs
Exposure Exposed Both
duration male exposed

2 Weeks 59.0 [+ or -] 6.3 59.0 [+ or -] 6.3
 81.7 [+ or -] 11.5 34.2 [+ or -] 5.6
 44.8 [+ or -] 8.7 59.5 [+ or -] 10.9
 46.7 [+ or -] 5.6 45.7 [+ or -] 10.3
 --(a) 9.0 [+ or -] 6.0(*)
8 Weeks 33.3 [+ or -] 4.6 33.3 [+ or -] 4.6
 32.3 [+ or -] 4.7 45.3 [+ or -] 6.2
 32.0 [+ or -] 4.0 34.3 [+ or -] 6.7
 16.5 [+ or -] 8.5 21.5 [+ or -] 2.8

Exposed females were mated with control males, and exposed males were
mated with control females.

(a) There were no pairs due to small number of individuals.
(*) Significantly different from the control (ANOVA followed by
Dunnet's post hoc test, p [is less than or equal to] 0.05).


Female and male fertility (percent fertilized) were significantly reduced by developmental exposure to DDT. After 2- or 8-week developmental exposure, female fertility was significantly reduced by doses of DDT [is greater than or equal to] 0.23 [micro]g/L (Figures 8 and 9). Male fertility was significantly decreased by doses [is greater than or equal to] 0.5 [micro]g/L after a 2-week developmental exposure and by doses [is greater than or equal to] 0.3 [micro]g/L after an 8-weeks developmental exposure (Figures 8 and 9). Interestingly, when both partners were exposed, fertility of fish exposed for 2 weeks was only reduced at the highest dose (4.32 [micro]g/L), whereas fertility of fish exposed for 8 weeks was reduced at doses [is greater than or equal to] 0.69 [micro]g/L (Figures 8 and 9).

[GRAPHS OMITTED]

Female and male fitness (percent hatched) were drastically reduced by developmental exposure to DDT (Figures 8 and 9). After a 2-week developmental exposure, doses from 0.23 to 1.37 [micro]g/L significantly reduced hatching of embryos from exposed females. Oddly, the highest dose, 4.32 [micro]g/L, had no effect on hatching. Hatching was also reduced for males exposed to doses [is greater than or equal to] 0.5 [micro]g/L and mated with control females (Figure 8). When both parents were exposed, hatching was significantly reduced at all doses except 0.5 [micro]g/L. After an 8-week developmental exposure of females or males or both to any dose of DDT, embryo hatching was catastrophically reduced (Figure 9). In most cases, [is less than] 20% of embryos hatched. The pronounced reduction in hatching success and the significant reduction in fertility suggest that DDT has genotoxic effects on germ cells.

Because hatching success was most sensitive to DDT exposure, we examined correlations between hatching success and adult VTG expression. Hatching success was not significantly correlated with VTG expression in adult fish in either the 2- or 8-week exposed fish (data not shown).

Discussion

Exposure of developing medaka to the environmental estrogen o,p'-DDT caused both time- and dose-dependent effects. Short-term developmental exposure (2 weeks) caused feminization at the highest dose and reduced fertility and hatching success at much lower doses, but it did not alter VTG synthesis in juveniles or in adults (Table 3). Long-term developmental exposure (8 weeks) feminized males at doses [is greater than or equal to] 1.94 [micro]g/L and drastically reduced fertility and hatching success at doses [is greater than or equal to] 0.3 [micro]g/L (Table 3). Long-term exposure also induced VTG synthesis in juveniles and adults at the lowest dose, but VTG production was attenuated once the estrogenic stimulus was removed so that the adult pattern of VTG synthesis in males and females was unchanged. Both experiments indicate that DDT had permanent organizational effects on sexual development and reproductive function, but transitory activational effects on VTG production. Organizational responses were more sensitive to disruption than were activational responses; relative sensitivities were: hatching success [is greater than] fertility [much greater than] gonad differentiation [much greater than] VTG production.
Table 3. Sensitivity of various physiologic parameters to estrogenic
disruption by o,p'-DDT. Doses ([micro]g/L) represent the lowest dose
that caused significant alteration at any age.

 2-Week 8-Week
Parameter Male Female Male Female

VTG --(a) --(a) 0.30 0.30
Gonadal feminization 4.32 --(b) 1.94 --(b)
No. of eggs --(a) 1.37 --(a) --(a)
Percent fertilized 0.50 0.23 0.30 0.30
Percent hatched 0.23 0.23 0.30 0.30

Gonadal feminization refers to both ovotestis formation and complete
feminization resulting in a female-skewed sex ratio.

(a) No dose had an effect, (b) No change in ovarian structure.


Our data show that VTG, as detected by Western blotting with a highly specific antibody, is a moderately sensitive indicator of current exposure to an environmental estrogen. Although ELISA quantification of VTG concentration is frequently considered the most sensitive method, Western blotting was chosen as the most appropriate and consistent means to provide accurate, specific detection in both types of sample matrices--plasma and whole body homogenates. In our detection system, VTG-immunoreactive bands migrated identically in plasma, homogenates, and the female standard plasma. This detection system proved to be quite sensitive, requiring 100-fold dilution of plasma samples and dilution of whole body homogenates to 0.5 lag total protein per well.

The sensitivity of the vitellogenic response to environmental estrogens may be species and compound specific. For instance, DDT stimulates VTG synthesis in vivo in mosquitofish [Gambusia affinis (64)], medaka (11), and rainbow trout (65), but not in catfish [Ictalurus punctatus (66)]. In vitro, DDT stimulates VTG synthesis in rainbow trout hepatocytes (40), but fails to bind the seatrout (Cynoscion nebulosus) estrogen receptor (67). Crews et al. (68) suggested that such species-typical sensitivities to endocrine-disrupting compounds may depend on differences in circulating levels of sex steroid hormones and on receptor affinities.

Our data clearly show that developmental exposure to an environmental estrogen can have profound negative impacts on individual fitness. Most obviously, sexual development can be redirected from a male to female pathway, changing the population sex ratio and thus the number of available partners. More insidiously, testes may be partially feminized, reducing spermatogenic capacity. Most insidiously of all, fertility of eggs and sperm and hatching success of embryos can be severely impaired, even in individuals with histologically normal ovaries and testes.

Other studies that exposed medaka to DDT during development have also shown pronounced effects on gonadal development and sex ratio. Injection of a 227-ppm dose into eggs caused 86% sex reversal of genetic males (10), and immersion doses as low as 2.3 ppb (micrograms per liter) caused a significantly female-skewed sex ratio in medaka exposed for 3 months posthatch (11). In the present study, immersion doses of 2-4 ppb caused a female-skewed sex ratio, with efficacy depending on exposure duration. In contrast, sex differentiation in juvenile rainbow trout was completely unaltered by injection exposure to the DDT metabolites o,p'-DDE or p,p'-DDE (49). As mentioned above, sensitivity to particular environmental estrogens may depend on the hormone and receptor physiology of each species.

In medaka, other environmental estrogens appear to have less potent effects on sex differentiation than does DDT. Nonylphenol induced ovotestes in males exposed to approximately 25 ppb and induced sex reversal in fish exposed to 50 ppb for 3 months posthatch (69). In a separate study, lower, more environmentally relevant doses of nonylphenol (0.54-2 ppb) had no feminizing effect, but did appear to cause a male-skewed sex ratio at 0.77 ppb (70). [Beta]-Hexachlorocyclohexane ([Beta]-HCH; an isomer of the pesticide lindane) was less potent still, requiring a 3-month exposure to doses [is greater than] 0.18 ppm to feminize medaka (71). Finally, methoxychlor at low doses (0.18-2.31 ppb) was completely ineffective, failing to alter sex ratio after developmental exposure (70).

Alterations in sex differentiation have not been as thoroughly examined in other fish species. In a laboratory study, Gimeno et al. (7) found that genetically male carp were feminized by exposure to relatively high doses of 4-tert-pentylphenol (0.1-1ppm) for 90 days posthatch. In field collections, Jobling et al. (33) observed a high proportion of intersex roach (Rutilus rutilus, a cyprinid fish) downstream from sewage treatment facilities. The authors defined intersex fish as having both male and female gonadal characteristics and assumed that the fish were feminized males because the percentage of males sampled at a site decreased as the percentage of intersex fish increased. Although alkylphenols and synthetic steroidal estrogens are possible feminizing agents in sewage effluent, the specific estrogenic component(s) of these effluents is currently unknown. Currently, analysis of the reproductive capacity of these feminized wild fish has not been reported.

In the present study, fertility and hatching success were quite sensitive to estrogenic disruption in both sexes, with significant impairment occurring at doses as low as 0.23 ppb DDT. DDT is probably transferred from the parent to the gametes as are other lipophilic contaminants in fishes (72-75). Parentally transferred DDT may directly or indirectly inhibit the ability of sperm to fertilize eggs and the capacity of eggs to be fertilized. Female fertility was more sensitive to developmental DDT exposure than was male fertility. The reduction in female fertility was not due to decreased egg production because fecundity was only slightly reduced by DDT exposure (Table 2).

Because both male and female fertility were compromised, one would predict that exposure of both parents would catastrophically reduce fertilization. Interestingly, exposure of both parents appeared to rescue the fertility reduction (Figures 8 and 9). For instance, 2-week exposure to 1.37 [micro]g/L DDT reduced fertilization when either the female or the male alone was exposed, but it did not reduce fertility when both parents were exposed (Figure 8). Although intriguing, the biological basis of these results is unclear. Several possibilities exist, including changes in fertilization systems at the molecular level and alterations in courtship initiation and consummation. Alternatively, the rescue effect observed may be a statistical artifact due to the relatively small sample size (n = 6 pairs per mating group). However, the consistency of the effect across both experiments suggests a biological basis.

[GRAPHS OMITTED]

Other environmental estrogens reduce fertility and hatching success in medaka, but with apparently lower potency. Developmental exposure to di(n-butyl) phthalate (776 mg/kg/day) reduced fecundity at doses approximately 1,000-fold greater than the effective dose of DDT (76), whereas doses of nonylphenol and methoxychlor in the same range as DDT (0.2-2 ppb) had no effect on fecundity or hatching success (70). Exposure of adult male medaka to DDT also reduces reproductive success, but much higher doses are required in adults than those that were effective during development. Octylphenol and bisphenol A significantly reduced fertility and hatching success at doses of approximately 20 ppb and 2.28 ppm, respectively (51,53). Neither nonylphenol nor di(2-ethylhexyl)phthalate affected male fertility or hatching success (51,70).

Very little work has examined the effects of environmental estrogens or other endocrine-disrupting compounds on reproductive success in other fish species. In fathead minnows, exposure of paired adult males and females to estradiol reduced egg production (52), and exposure of sexually mature males reduced the size of the fat pad and the breeding tubercles, a prominent male secondary sex characteristic (77). Adult exposure to nonylphenol (1-10 ppb) also reduced fat pad size in males and egg production in females, whereas exposure to butylbenzyl phthalate (100 ppb) had no effect (78). Developmental exposure to the presumed antiandrogen vinclozolin and its metabolites had no effect on sex ratio or fecundity in fathead minnows (50).

The differential potency of estrogenic compounds is probably due to differences in bioaccumulation. Medaka readily accumulate DDT: eggs collected from females exposed to 2.5 ppb DDT for 3 or 6 weeks contained an average of 3,600 ppm DDT (11). Although bioaccumulation studies of alkylphenols have not been performed in medaka, nonylphenol is rapidly metabolized and excreted via the bile in rainbow trout (79), suggesting that bioaccumulation is limited. Little is known about the kinetics of bisphenol A and phthalate metabolism in fish, but these compounds may be metabolized more rapidly or accumulated more slowly than DDT.

Conclusion

The purpose of this study was to examine the effects of an environmental estrogen on individual fitness and to evaluate the effectiveness of VTG as a predictor of impaired reproduction in fish. Because a short-term developmental exposure to DDT feminized medaka and impaired reproductive function in the absence of abnormal VTG expression at any age, we suggest that VTG measurement cannot serve as the the definitive test for predicting reproductive impairment. VTG synthesis is an activational response to estrogen or environmental estrogen stimulation and disappears once the stimulus is removed. Therefore, absence of VTG expression can be a false negative if fish have not been recently exposed. However, because VTG expression is less sensitive to environmental estrogen action than gonadal development and reproductive function, its presence in adult males can reasonably be interpreted as a signal that embryos produced in a similar environment may suffer organizational effects such as gonadal feminization and reduced fertility as adults.

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Address correspondence to A.O. Cheek, Department of Biological Sciences, Southeastern Louisiana University, Hammond, LA 70402 USA. Telephone: (504) 549-2493. Fax: (504) 549-3851. E-mail: acheek@selu.edu

We thank S. Barnes for fish care, D. Barnes for performing chemical analyses, N. Brown-Peterson for preparation of tissue sections and consultation on gonad morphology, and A. Karels for assisting with fish sampling.

This study was supported by National Science Foundation grant IBN9815883 (A.O.C.).

Received 4 December 2000; accepted 30 January 2001.

Ann Oliver Cheek,(1) Thea Hoexum Brouwer,(2) Suzanne Carroll,(2) Steve Manning,(2) John A. McLachlan,(3) and Marius Brouwer(2)

(1) Department of Biological Sciences, Southeastern Louisiana University, Hammond, Louisiana, USA; (2) Department of Coastal Sciences, Institute of Marine Sciences, University of Southern Mississippi, Ocean Springs, Mississippi, USA; and (3) Tulane-Xavier Center for Bioenvironmental Research, Tulane University, New Orleans, Louisiana, USA
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