Relationship between sex steroid and vitellogenin concentrations in flounder (Platichthys flesus) sampled from an estuary contaminated with estrogenic endocrine-disrupting compounds.

High concentrations of vitellogenin (VTG; egg yolk protein) have previously been found in male flounder (Platichthys flesus) from several UK estuaries; these levels have been ascribed to the presence of estrogenic endocrine-disrupting compounds (EDCs). Gonadal abnormalities, including intersex, have also been recorded in these estuaries. However, there is no firm evidence to date that these two findings are causally linked or that the presence of estrogenic EDCs has any adverse population effects. In the present study, we examined the relationship between concentrations of VTG and sex steroids (11-oxo-testosterone in males and 17beta-estradiol in females) in specimens of flounder captured from the estuary of the River Mersey. We first questioned whether the high concentrations of VTG in male and immature female flounder were indeed caused by a direct effect of exogenous EDCs and not indirectly via the endogenous secretion of 17beta-estradiol. The data favored the direct involvement of estrogenic EDCs. We then questioned whether the presence of estrogenic EDCs not only stimulated inappropriate VTG synthesis but whether it might also have had a negative effect on endogenous steroid secretion. It should be noted that the predicted consequences of a drop in steroid secretion include smaller gonads, smaller oocytes, fewer numbers of sperm, and depressed spawning behavior. This question was more difficult to answer because of the strong effect of the seasonal reproductive cycle and stage of maturation on steroid concentrations. However, matched by month of capture and stage of maturation, both 17beta-estradiol in females and 11-keto-testosterone in males were in most cases significantly lower in those years when VTG concentrations were higher.

Surveys of vitellogenin (VTG; egg yolk) induction in male flounder (Platichthys flesus) in the United Kingdom (Allen et al. 1999a, 1999b; Kirby et al. 2004a; Kleinkauf et al. 2004c; Lye et al. 1997, 1998; Matthiessen et al. 2002) and Dutch (Vethaak et al. 2002) estuaries; in male flounder (Pleuronectes yokohamae) in Tokyo Bay, Japan (Hashimoto et al. 2000); and in male common goby (Acanthogobius flavimanus) and grey mullet (Mugil cephalus) in coastal areas of Japan (Hara et al. 2001; Ohkubo et al. 2003) have shown that these species have been and still are being exposed to estrogenic endocrine-disrupting compounds (EDCs). In the United Kingdom, France, and Japan as well, a small proportion of male flatfish (Allen et al. 1999b; Hashimoto et al. 2000; Kirby et al. 2004a; Minier et al. 2000) and shad (Konosirus punctatus) (Cho et al. 2003) have been shown to exhibit the intersex condition (presence of ovotestis). Over 7 years of survey in the United Kingdom, there have been some estuaries where male flounder have shown little or no sign of the presence of estrogenic EDCs and others where, in certain years, concentrations of VTG have approached and even exceeded those found in fully reproductively mature females. In the estuaries of the rivers Tyne and Mersey, there is also good evidence of a statistically significant decrease in the presence of estrogenic EDCs over the 7-year sampling period (Kirby et al. 2004a; Kleinkauf et al. 2004c), a finding in line with improvements in water quality that occurred during that period. Male flounder with elevated VTG concentrations in their plasma have also been caught in coastal (as opposed to estuarine) waters (Allen et al. 1999b). However, all evidence suggests these fish have migrated from contaminated estuaries rather than receiving their exposure in the open sea. The half-life of VTG in plasma of male flounder is 14 days (Allen et al. 1999b; George et al. 2004).

In 2002 it was stated by Matthiessen et al. (2002), in relation to the evidence for estrogenic EDCs and ovotestis induction in flounder in some UK estuaries [obtained during the Endocrine Disruption in the Marine Environment (EDMAR) program], that “although reproductive success may be impaired in some cases, implications for fish populations are still unclear.” This statement is still true today. Marine fish are not easy to study in the field. The closest we can get to answering the question about population effects in flounder is to examine whether overtly important reproductive parameters, such as fecundity and fertility, are related to the presence of EDCs in estuaries. Few such studies have been carried out in the rivers Tyne, Dee, and Mersey in the United Kingdom (Gill et al. 2002; Kleinkauf et al. 2004a, 2004b; Lye et al. 1997, 1998; Simpson et al. 2000). They all show that flounder from contaminated estuaries (i.e., where fish have consistently high VTG concentrations) also exhibit more signs of disrupted gonadal development (listed in “Discussion”) than flounder from uncontaminated estuaries.

The only aspect of gonadal development examined in any detail as part of the EDMAR program was the presence or absence of intersex. In an effort to obtain further evidence for possible adverse effects of estrogenic EDCs in fish collected during the course of EDMAR, we decided to investigate sex steroid concentrations in plasma. In another species, the white sucker (Catostomus commersoni) living in polluted waters, the circulating concentrations of sex steroids are significantly lower than circulating concentrations in the same fish living in unpolluted waters (Munkittrick et al. 1991). These sex steroid concentrations also appear to be related to increased age, maturation, reduced secondary sexual characteristics, and reduced gonadal development (all important “population effects”). Several other researchers have examined sex steroid concentrations specifically in relation to EDCs (Ankley et al. 1998; Kime 1995; McMaster et al. 2001). These studies support a decrease in sex steroid concentrations in response to the presence of EDCs, although none of the studies indicate whether this decrease is a result of EDCs acting directly on the activity of steroidogenic enzymes, indirectly through effects on feedback regulation within the hypothalamo–pituitary–gonadal axis, or by affecting the catabolism and excretion of the organism. Whatever the mechanism, sex steroid concentrations do appear to be sensitive to pollutants (Folmar et al. 1996; Jobling et al. 1996; Kime 1995; Munkittrick et al. 1998), especially in fish exposed to sewage treatment works or pulp mill effluents.

Most of the publications cited above highlight a major problem in interpreting sex steroid concentrations; that is, that they are highly dependent on the reproductive state of the fish. Thus, if fish from the same site are to be compared in different years, sampling has to be conducted at exactly the same point of their reproductive cycle and the fish have to be of a matching reproductive status. Because of this constraint, we decided in the present study to examine sex steroid concentrations in flounder caught only in the Mersey estuary, where seven sampling trips (six of which could be paired for month of sampling) were made between 1997 and 2003. Another major advantage of using this estuary as a case study was that the amount of apparent estrogenic contamination was different from year to year (Kirby et al. 2004a). Without such differences, it would have been difficult to test any association between sex steroid concentrations and VTG concentrations in a field situation. The steroids we have chosen to measure are 17β-estradiol (E2, the main estrogen of female fish) and 11-oxotestosterone [also known as 11-ketotestosterone (11-KT), the major androgen of male fish]. In addition to asking the question as to whether high estrogenic EDC levels mean low steroid concentrations, we also ask the question as to whether the estrogenic EDCs induce VTG directly or via stimulation of endogenous E2 secretion.

Materials and Methods

The site of capture of flounder in the Mersey estuary (and in nearby Liverpool Bay), the method of capture, and the method of sample collection are described in previous articles (Allen et al. 1999a, 1999b; Kirby et al. 2004a, 2004b). Data on VTG concentrations used in the present study were taken from these previous studies. However, the analysis of data by stage of maturation in the present article is new. The histological sections of gonads were also prepared during the course of the previous studies (Allen et al. 1999a). We re-examined these sections for stage of maturity. This determination was based upon the presence of the most advanced stage of gamete development that could be seen in histological sections of the gonads described below.

Ovaries: F1, primary oocytes only; F2, cortical alveoli-stage oocytes as well as primary oocytes; F3a, a mixture of cortical alveoli-stage and secondary (i.e., vitellogenic) oocytes; F3b, predominantly secondary oocytes.

Testes: M1, spermatogonia only; M2a, secondary spermatogonia; M2b, primary spermatocytes through to spermatids; M3a, some spermatozoa in addition to spermatocytes and spermatids; M3a, spermatozoa only.

To increase the numbers of fish in each grouping (for statistical purposes), we combined the subcategories (i.e., a and b) for the analyses of VTG, E2, and 11-KT concentrations.

For steroid assay, plasma aliquots (100 μL) were shaken vigorously with 50 μL distilled water and 4 mL diethyl ether for 2 min. The aqueous layer was allowed to settle, then frozen in liquid nitrogen. The solvent phase was poured into a glass tube (12 mm × 75 mm), then evaporated in a water bath at 45ºC. The residue was redissolved in 400 μL radioimmunoassay (RIA) buffer and measured as described previously for E2 and 11-KT (Scott et al. 1980, 1984). Two 100-μL aliquots were used for assay of E2, and an additional two 50-μL aliquots were used for assay of 11-KT. A plasma sample “spiked” with 2 ng/mL E2 was included in every E2 assay. The coefficient of interassay variation was < 10%. Sixty plasma samples from flounder collected in 1997 were also assayed twice (and by two different people) 4 years apart. The correlation coefficient between values generated by the two assays was 0.93, and the slope of the relationship was 1.03.

All data are expressed as means ± SE. Data were statistically analyzed by analysis of variance followed by comparison of means using Duncan’s multiple range test at a significance level of 0.05. Logarithmic transformation was performed when necessary to ensure homogeneity of variance.

Results

The numbers of fish caught at each maturation stage and at each sampling time in the Mersey estuary between 1996 and 2003 are shown in Table 1. For the purpose of analyzing steroid and VTG concentrations, we divided fish of both sexes into three groups that roughly equated to “immature,” “on the borderline between immaturity and maturity,” and “mature.” This last category encompassed the whole period of time from the first appearance of secondary oocytes and secondary spermatocytes up until the fish were ready to spawn. The histological and sex steroid data indicate that the secondary maturation phase in flounder lasts from September until March.

Table 1

Numbers of flounder at each stage of maturation caught in the Mersey estuary at each sampling time.

Year/month	F1	F2	F3a	F3b	M1	M2a	M2b	M3a	M3b	Intersex
1996 December	2	1	9	24	4	–	–	13	8	–
1997 September	41	19	22	–	56	–	4	–	–	5
1999 September	10	–	–	–	1	–	–	–	–	–
2000 November	13	1	5	4	8	5	4	1	–	–
2001 February	13	1	–	6	5	–	1	3	4	3
2001 September	18	3	3	–	14	2	–	–	–	–
2002 December	4	–	–	21	1	–	–	–	25	–
2003 February	6	–	1	24	3	–	–	–	8	1
1997 Marcha	–	–	–	–	8	–	–	–	16	–

–, no fish.

Caught in Liverpool Bay.

Mean concentrations of E2, 11-KT, and VTG in males and females, categorized by sampling date and stage of maturation, are summarized in Tables 2 and 3. When only one or two fish were at a particular stage of maturation, the data were not included in the tables. Data from intersex fish (n = 9) were also not included. The data in Tables 2 and 3 were used to explore the relationship between sex, stage of maturation, and time of year versus VTG and sex steroid concentrations in flounder.

Table 2

Mean ± SE concentrations of E2 (ng/mL), 11-KT (ng/mL), and VTG (μg/mL) in male flounder from the Mersey estuary by year, month, and stage of maturity.

Year/month	Stage	n	E2	11-KT	VTG
Mersey estuary
1997 September	M1	56	0.09 ± 0.01a	0.89 ± 0.11a	780 ± 339a
	M3	4	0.08 ± 0.01a	0.57 ± 0.05a	1307 ± 614a
2001 September	M1	14	0.07 ± 0.01	0.79 ± 0.2	0.32 ± 0.3
2000 November	M1	8	0.12 ± 0.01a	0.37 ± 0.05a	192 ± 76a
	M3	9	0.20 ± 0.03b	2.65 ± 0.45b	527 ± 380a
1996 December	M1	4	0.13 ± 0.03a	0.18 ± 0.07a	10,847 ± 6,533a
	M3	19	0.22 ± 0.02a	3.29 ± 0.49b	20,262 ± 9,133a
2002 December	M3	25	0.16 ± 0.01	7.48 ± 1.48	1107 ± 603
2001 February	M1	5	0.09 ± 0.01a	0.54 ± 0.4a	2,842 ± 2373a
	M3	7	0.10 ± 0.01a	15.2 ± 11.7b	601 ± 421a
2003 February	M1	3	0.22 ± 0.01a	0.61 ± 0.11a	283 ± 259a
	M3	8	0.22 ± 0.01a	19.1 ± 5.6b	47 ± 46a
Liverpool Bay
1997 March	M3	16	0.09 ± 0.01	52.9 ± 12.5	780 ± 750

Values with the same letters within year/month are not significantly different from each other.

Table 3

Mean ± SE concentrations (ng/mL) of E2, 11-KT, and VTG in female flounder from the Mersey estuary by year, month, and stage of maturity.

Year/month	Stage	n	E2	11-KT	VTG
Mersey estuary
1997 September	F1	41	0.15 ± 0.02a	0.24 ± 0.02a	1,080 ± 342a
	F2	19	0.32 ± 0.04b	0.33 ± 0.12a	900 ± 400a
	F3	22	0.34 ± 0.05b	0.24 ± 0.03a	5,797 ± 1,009b
1999 September	F1	10	0.14 ± 0.02	0.35 ± 0.04	292 ± 196
2001 September	F1	18	0.21 ± 0.06a	< 0.5*	29 ± 16a
	F2	3	0.87 ± 0.15b	< 0.5	8,096 ± 2,159b
	F3	3	1.41 ± 0.28b	< 0.5	4,443 ± 1,199b
2000 November	F1	13	0.19 ± 0.02a	0.27 ± 0.03a	312 ± 202a
	F3	8	1.2 ± 0.23b	0.37 ± 0.01a	4,795 ± 629b
1996 December	F3	33	2.79 ± 0.4	0.17 ± 0.03	18,319 ± 3,139
2002 December	F1	4	0.18 ± 0.02a	< 0.5	32 ± 31a
	F3	21	5.64 ± 1.2b	< 0.5	6,186 ± 2,161b
2001 February	F1	13	0.15 ± 0.01a	0.53 ± 0.05a	1,208 ± 822a
	F3	6	5.92 ± 0.83b	0.71 ± 0.09a	2,831 ± 1,719b
2003 February	F1	6	0.22 ± 0.02a	0.26 ± 0.06a	581 ± 323a
	F3	25	19.9 ± 4.5b	1.02 ± 0.10b	7,239 ± 921b
Liverpool Bay
1997 March	F3	8	22.3 ± 6.6	0.59 ± 0.1	8,081 ± 1287

Values with the same letters within year/month are not significantly different from each other.

A high detection limit of 0.5 ng/mL was set in some of the 11-KT assays; all values less than this are shown.

Mean E2 concentrations in males were low (between 0.08 and 0.22 ng/mL, Table 2) and displayed no obvious relationship to the time of year or stage of sexual maturity. Most important, there was no evidence that high VTG concentrations were caused by high E2 concentrations; in fact, there was no relationship (r2 = 0.03; n = 158) between E2 and VTG concentrations in males (Figure 1). We found no obvious trend in VTG concentrations of either mature or immature males throughout the year (Figure 2) and no statistical difference between fish at different stages of maturation (Table 2). In contrast, mean 11-KT concentrations in males showed a regular month-on-month increase between September and March (Figure 3) and were also different between mature and immature fish (see statistics in Table 2).

Figure 1

Lack of correlation between VTG concentrations and E2 concentrations in individual male flounder captured in the Mersey estuary between 1996 and 2003.

Figure 2

Mean concentrations (± SE) of VTG in male flounder by month of capture in the Mersey estuary.

Figure 3

Mean concentrations (± SE) of 11-KT in male flounder by month of capture in the Mersey estuary.

Mean E2 concentrations in females were strongly influenced by stage of maturation (Table 3). E2 concentrations in immature females were never higher than those concentrations in either immature or mature males. In mature females, however, concomitant with the beginning of secondary oocyte development in September, E2 concentrations started to rise and reached a peak of 20 ng/mL at spawning time in March (Figure 4). As with males, we saw no obvious trend or pattern in VTG concentrations between September and March (Figure 5). Values fluctuated between 2,800 and 18,000 μg/mL. These concentrations were, nevertheless, in all cases higher than those found in immature females sampled at the same time (Table 3). Also, VTG concentrations in immature females were never at any sampling time significantly different from VTG concentrations in mature or immature males (analysis not shown).

Figure 4

Mean (± SE) concentrations of E2 in female flounder by month of capture in the Mersey estuary.

Figure 5

Mean concentrations of VTG (± SE) in female Mersey estuary flounder by month of capture.

Mature males caught in December 1996 had significantly lower mean 11-KT concentrations than mature males caught in December 2002 (Table 4). However, there was no significant difference between mean 11-KT concentrations in males caught in February 2001 and those caught in February 2003 (Table 4). Mature females caught in December 1996 had significantly lower E2 concentrations than mature females caught in December 2002 (Table 4). We also observed a significant difference between E2 concentrations in mature females caught in February 2001 and those caught in February 2003 (Table 4). In all cases, the lower E2 concentrations were found in the years when VTG concentrations in males were higher, which suggests that the presence of EDCs is associated with lower endogenous steroid synthesis.

Table 4

Matching mean ± SE (n) concentrations of VTG in male, E2 in mature female (F3), and 11-KT in mature male (M3) Mersey estuary flounder by month and year.

Year/month	VTG in all males (μg/mL)	E2 in mature females (ng/mL)	11-KT in mature males (ng/mL)
1997 September	794 ± 318a (6)	0.34 ± 0.05a (22)	—
2001 September	0.3 ± 0.3b (14)	1.41 ± 0.28b (3)	—
1996 December	18,625 ± 7,614a (23)	2.79 ± 0.40a (33)	3.29 ± 0.49a (19)
2002 December	1,107 ± 603b (25)	5.64 ± 1.20b (21)	7.48 ± 1.48b (25)
2001 February	1,463 ± 940a (12)	5.92 ± 0.83a (6)	15.2 ± 11.7a (7)
2003 February	103 ± 53b (11)	19.9 ± 4.5b (25)	19.1 ± 5.6a (8)

—, absence of M3 males in September. Values with the same letters within month are not significantly different from each other.

Discussion

We firmly concluded from this study that the VTG found in the plasma of male flounder in the Mersey estuary is not induced by endogenous E2. Although this conclusion seems naïve, substantial concentrations of E2 (> 1 ng/mL) have been found in blood plasma of reproductively mature males of a closely-related species, the North Sea plaice (Pleuronectes platessa) (Scott et al. 2000; Wingfield and Grimm 1977). The concentrations of E2 in male flounder in the present study, however, were < 0.22 ng/mL, never higher than those found in immature females, and thus were unlikely to be a trigger for VTG synthesis. Exogenous compound(s), acting directly on the estrogen receptor, are the more likely cause.

The number of fish caught at each maturity stage, plus steroid concentration data, in each month clearly indicates that the maturity cycle in both males and females begins about September and culminates in spawning (in the open sea) in March and April. The same conclusion can be reached by examining VTG concentrations (Kleinkauf et al. 2004c) and gonadosomatic indices (Kleinkauf et al. 2004a) of females caught in both the river Mersey and the river Dee estuaries between 1998 and 2000. Unlike in those studies, VTG concentrations in mature females in the present study showed no relationship to month of capture. The reason for this finding is probably that our samples have been collected over a period of 7 years, during which the level of estrogenic contamination has varied dramatically from a high in 1996 to a relative low in 2003 (Kirby et al. 2004a). This high variability in contamination has probably obscured the cycle. A previous observation that estrogen-induced VTG concentrations in male flounder also have a seasonal cycle (Kirby et al. 2004a; Kleinkauf et al. 2004c) was also obscured by the high year-to-year variations in estrogenic EDCs in the Mersey.

If, as seems likely, elevated VTG concentrations are mainly caused by estrogenic EDCs, then one might hypothesize that these same EDCs have a negative feedback effect on the secretion of gonadotropin from the pituitary and, hence, on 11-KT secretion by the testis in the males. The high dependence of 11-KT concentrations on stage of maturation and month of capture meant that, despite the large overall number of observations, it was only possible to examine this hypothesis via two pairs of data with the same month of capture and with a sufficient number of mature males for statistical analysis (Table 4). In December 1996, when VTG concentrations were high, 11-KT concentrations were significantly lower than in December 2002, when VTG concentrations were 20 times lower. In February 2001 and 2003 though, when VTG concentrations were much closer together (although still significantly different), 11-KT concentrations were not significantly different from each other. In females in September, December, and February, mean E2 concentrations were significantly lower in the years when mean VTG concentrations were higher.

Although supported by statistical analysis, the finding that mean steroid concentrations are in most cases lower in the years when the effects of exogenous estrogens are higher must be interpreted with caution. At the moment, it is an association only and needs to be tested in a laboratory experiment. There is no evidence yet of cause and effect. There are many other factors that could be the cause of 2- to 3-fold differences in steroid concentrations between years. These possibilities include water temperature (Onuma et al. 2003), diet (Cerda et al. 1995, 1997), and time of day. The sampling in the present study covered 7 years; therefore, another possible reason is that the differences were caused by deterioration of steroids during long-term storage. However, as indicated in “Materials and Methods,” there was no evidence of any deterioration of immunoreactivity of E2 in plasma samples that were stored for 4 years.

Bearing in mind that in no case is there necessarily a causal link, high plasma concentration of VTG in flounder have so far been associated with higher incidences of testicular malformation (Gill et al. 2002; Lye et al. 1997, 1998), higher amounts of oocyte malformation (Lye et al. 1998), more sperm abnormalities (Gill et al. 2002), more pathological lesions in the liver and kidney (Simpson et al. 2000), higher sperm motility (Kleinkauf et al. 2004b), lower gonadosomatic index (Kleinkauf et al. 2004a), and lower sex steroid concentrations (this study). However, there has been no clear link with degree of intersex (Allen et al. 1999a; Kirby et al. 2004a; Simpson et al. 2000), estrogen receptor concentrations in the liver (Kleinkauf et al. 2004b), hepatocyte proliferation markers (Kleinkauf et al. 2004b), ethoxyresorufin O-deethylase induction (Kirby et al. 2004b), or even with VTG mRNA (Craft et al. 2004; George et al. 2004). We stress the lack of a causal link because there are many other xenobiotics in estuaries (not just estrogens) that work through different mechanisms. These other compounds could cause the observed changes (without themselves affecting VTG concentrations).

An important practical outcome of the present study was that VTG concentrations in immature females (i.e., those shown by histological examination to possess only primary oocytes) were not statistically different from those found in males. This finding confirms the results of an earlier study (Kleinkauf et al. 2004c). The importance of this finding is that, until now, estuary surveys (Kirby et al. 2004a) have largely ignored data on VTG concentrations in females because of the uncertainty about the possible role of endogenous E2. However, our data suggest that, provided females can be proved immature by histological examination, their VTG concentrations can be pooled with those of males to increase the overall number of observations at each site.

Finally, an important lesson we have learned from the present study is that future field surveys should, if possible, be rigidly planned to catch flounder at the same places and at the same times each year. Only by ensuring such consistency is there any point in measuring sex steroid concentrations in flounder. We have also already concluded that only with rigid scheduling of field surveys is it possible to obtain clear-cut data on long-term trends in estrogenic EDC contamination in estuaries (Kirby et al. 2004a).

Conclusions

Few studies have been conducted on the population consequences of estrogenic EDCs on marine species. In the present article, we show that high VTG concentrations in male and female flounder caught in the Mersey estuary are not caused by endogenous E2. Rather, evidence indicates that elevated VTG concentrations are associated with a reduction in the synthesis of E2 by females and of 11-KT by males. Several mechanisms are possible, but the most likely is that the exogenous estrogenic EDCs not only enhance the production of VTG by the liver but also lower sex steroid production by negative feedback on the hypothalamic–pituitary axis. Work on other species suggests that reductions of sex steroid levels may have an adverse effect on fecundity and fertility. Any such causal link in flounder remains to be established, however.