Assessment of xenoestrogenic exposure by a biomarker approach: application of the E-Screen bioassay to determine estrogenic response of serum extracts
© Rasmussen et al; licensee BioMed Central Ltd. 2003
Received: 25 April 2003
Accepted: 15 October 2003
Published: 15 October 2003
Epidemiological documentation of endocrine disruption is complicated by imprecise exposure assessment, especially when exposures are mixed. Even if the estrogenic activity of all compounds were known, the combined effect of possible additive and/or inhibiting interaction of xenoestrogens in a biological sample may be difficult to predict from chemical analysis of single compounds alone. Thus, analysis of mixtures allows evaluation of combined effects of chemicals each present at low concentrations.
We have developed an optimized in vitro E-Screen test to assess the combined functional estrogenic response of human serum. The xenoestrogens in serum were separated from endogenous steroids and pharmaceuticals by solid-phase extraction followed by fractionation by high-performance liquid chromatography. After dissolution of the isolated fraction in ethanol-DMSO, the reconstituted extract was added with estrogen-depleted fetal calf serum to MCF-7 cells, the growth of which is stimulated by estrogen. After a 6-day incubation on a microwell plate, cell proliferation was assessed and compared with the effect of a 17-beta-estradiol standard.
Results and conclusions
To determine the applicability of this approach, we assessed the estrogenicity of serum samples from 30 pregnant and 60 non-pregnant Danish women thought to be exposed only to low levels of endocrine disruptors. We also studied 211 serum samples from pregnant Faroese women, whose marine diet included whale blubber that contain a high concentration of persistent halogenated pollutants. The estrogenicity of the serum from Danish controls exceeded the background in 22.7 % of the cases, while the same was true for 68.1 % of the Faroese samples. The increased estrogenicity response did not correlate with the lipid-based concentrations of individual suspected endocrine disruptors in the Faroese samples. When added along with the estradiol standard, an indication of an enhanced estrogenic response was found in most cases. Thus, the in vitro estrogenicity response offers a promising and feasible approach for an aggregated exposure assessment for xenoestrogens in serum.
Epidemiological research on endocrine disruption is hampered by difficulties in assessment of mixed exposures. A limited number of environmental chemicals have been characterized with regard to hormonal effects, but the effect of complex mixtures is virtually unknown. A promising approach to assess the combined functional estrogenic response in a serum sample was published by Sonnenschein, Soto and coworkers in 1995 . This approach has been further developed and refined by research groups in the US , in Denmark  and in Spain .
Although logical and highly attractive, methodological difficulties must be overcome. Endogenous and pharmaceutical estrogens must be removed to avoid interference with effects caused by environmental chemicals. However, any pretreatment procedure must at the same time preserve the environmental chemicals of interest. Due to similar characteristics of the exogenous compounds that may bind to the estrogen receptor, this conflict is unlikely to be resolved in an ideal way. Pretreatment procedures are limited to physicochemical procedures that will not necessarily reflect the origin of the compounds and their physiological properties. Fortunately, many xenoestrogens identified so far are generally lipophilic, thus suggesting that a separation based on lipophilicity may constitute a feasible compromise.
We have refined and modified the original biomarker method  by i) introducing solid-phase extraction (SPE) of the serum sample with a newly developed SPE-polymeric sorbent that exhibits both hydrophilic and lipophilic retention characteristics , thereby ensuring extraction of a wider range of compounds according to polarity, ii) using a modified high-performance liquid chromatography (HPLC) gradient that covers the mid-polar area for collection of the early lipophilic fraction before elution of endogenous estrogens, oral contraceptives and metabolites, and iii) applying a modified E-Screen bioassay  that requires smaller amounts of serum extract and exhibits an increased ability to detect low-potency estrogenic compounds.
This methodology was applied on a substantial number of endogenous hormones, oral contraceptives, and a wide range of environmental pollutants known to be present in human serum. The information on specific retention times was used to optimize the HPLC separation procedure to include major xenoestrogens, while excluding interfering substances.
The biomarker method was used to assess the xenoestrogenic response of serum samples from 211 pregnant Faroese women (34th week). This group had a high level of endogenous estrogens due to pregnancy, and, at the same time, a complex, mixed dietary exposure to xenoestrogens, including PCBs and other persistent halogenated pollutants that mainly originate from pilot whale blubber and fish [7, 8]. A large number of halogenated organic pollutants are known to occur in biological matrices [9–13], but the quantitatively dominating environmental pollutants identified in human samples are the major p,p'-DDT metabolite, p,p'-DDE, and the PCB congeners 2,2',3,4,4',5'-hexachlorobiphenyl (PCB138), 2,2',4,4',5, 5'-hexachlorobiphenyl (PCB153), and 2,2',3,4,4',5,5'-heptachlorobiphenyl (PCB180), whereas the hydroxylated metabolites of PCBs are dominated by 4-OH-2,2',3,4',5,5', 6-heptachlorobiphenyl (4-OH-CB187) [8, 9, 12, 14].
All media ingredients were purchased from In Vitro A/S (Fredensborg, Denmark) except insulin, sulforhodamine B (SRB), 2-amino-2-(hydroxymethyl)-1,3-propanediol (Tris base), trichloroacetic acid (TCA), dimethylsulfoxide (DMSO) Hybri-Max® (99.7 % purity) that were purchased from Sigma (St. Louis, MO, US) and gentamicin sulfate (DuraScan, Odense, Denmark). The charcoal/dextran-treated fetal calf serum (CT-FCS) batch originated from the same lot (Lot No. 416632) as the untreated batch (Biological Industries, Beit Haemek, Israel), and was used in all experiments. The estrogen antagonist ICI 182,780 (ICI) was kindly provided by Astra Zeneca (Cheshire, UK). 17-beta-estradiol (E2), o,p'-DDT, p,p'-DDE, estrone, estriol, 16α-hydroxyestrone, progesterone, cholesterol, 5α-dihydroprogesterone, 17α-hydroxypregnenolone, androstenedione, dehydroepiandrosterone, 17α-hydroxyprogesterone were provided by Sigma (St. Louis, MO, US). Androsterone and 5α-dihydrotestosterone were obtained from Steraloids Inc (Newport, RI, US). Testosterone and ethanol 96 % were obtained from Fluka (Buchs, Switzerland). β-HCH was provided by NSI Solutions Inc (Research Triangle Park, NC, US), methoxychlor, dieldrin, hexachlorobenzene (HCB), PCB105, PCB118, PCB138, PCB153, and PCB180 were provided from Dr. Ehrenstorfer GmbH (Augsburg, Germany). The hydroxylated PCBs, 4-OH-CB107, 4-OH-CB146 and 4-OH-CB187, were kindly provided by Dr. Aa. Bergman (Stockholm, Sweden). Methanol, n-heptane, ethyl acetate and isopropanol were of CHROMASOLV® quality and obtained from Riedel-de Häen (Seelze, Germany), and 2,2,4-trimethylpentane was from Aldrich (Steinheim, Germany).
A cohort of 547 mother-child pairs was established consecutively at the National Hospital in Torshavn, Faroe Islands, and included women with a wide variation in exposure to persistent environmental pollutants due to differences in age and dietary habits. Maternal serum was collected at the last antenatal hospital visit at the 34th week of pregnancy. Levels of individual exposures to PCBs and related compounds were characterized by analyses of milk collected from the same women 3–5 days after parturition; 211 women were then selected to represent the full range of exposures, with oversampling of subjects with low and high exposure levels.
As the women in this cohort had the same source of exposure (frequent marine food dinners, including pilot whale meat and blubber), the ratios between PCB congeners and related lipophilic pollutants would be expected to vary only little between the samples. The correlation coefficients between lipid-based concentrations of PCB105, PCB118, PCB138, PCB153, PCB156 or PCB180 and o,p'-DDT, p,p'-DDE, HCB or trans-nonachlor were 0.90–0.95 (as also observed previously ), but milk lipid concentrations were used in this paper, as the higher fat content of milk would render these analyses more precise.
The cohort of Danish women consisted of 30 pregnant (12th – 38th week) and 60 non-pregnant anonymous volunteers. Although we did not have exposure information for these women, the absence of whale blubber from the diet and the low-level exposures to persistent organohalogen compounds in Scandinavia suggest that they be considered controls for comparison with the Faroese cohort.
Serum extraction method
Solid-phase extraction was used to extract xenoestrogens from serum. Four mL serum was applied to an OASIS HLB 6 cc 500 mg extraction cartridge (Waters, Milford, MA, US) placed in a Vac Elute SPS 24 Vacuum Manifold (Varian, Harbor City, CA, US). Each cartridge was conditioned with 3 mL methanol followed by 3 mL Milli-Q water prior to application of the serum. The serum was allowed to elute slowly (without applied vacuum) through the cartridges and dried with applied vacuum. The extracted compounds were eluted by 3 mL of methanol followed by 2 mL ethyl acetate into an extraction tube, and evaporated at 40°C under a gentle nitrogen stream. The remaining aqueous phase in the extraction tube was further extracted three times by 1 mL n-heptane/ethyl acetate (1:1, vol/vol) and centrifuged at 1000 g in 10 min. Following extraction, the three supernatants were pooled in a new centrifuge tube, evaporated and reconstituted in 125 μL n-heptane/ethyl acetate (9:1, vol/vol). An aliquot of 100 μL was injected into the HPLC system.
Apparatus and chromatographic conditions (HPLC and GC)
High performance liquid chromatography separation of the extracted compounds was performed using a LaChrom HPLC system consisting of a L-7100 HPLC pump, a L-7200 Auto Sampler, a L-7400 UV-detector, a L-7450 Diode-array Detector, a L-7350 Column Thermostat and a D-7000 Interface Module (Merck, Darmstadt, Germany). Defined fractions of the mobile phase were collected by an L-7650 Fraction Collector (Merck, Darmstadt, Germany). The system was equipped with a LiChrospher Silica 60 (5 μm) 250 × 4.6 mm column (Merck, Darmstadt, Germany). Elution of the compounds was performed using the gradient system: 0 – 18 min: 90 % mobile phase A (100 % n-heptane) and 10 % mobile phase B (methanol/n-heptane/ isopropanol (45:40:15, vol/vol/vol)); 18 – 22 min: gradient to 50 % A and 50 % B; 22 – 26 min: gradient to 100 % B; 26 – 28 min: 100 % B; 28 – 33 min: gradient to 90 % A and 10 % B. 33 – 35 min: 90 % A and 10 % B.
Gas chromatography (GC) was performed on a Hewlett-Packard 6890 GC equipped with a μ-ECD and a 7683 series injector. Separation was performed on a HP-5MS capillary column (30 m × 0.25 mm, 0.25 μm film thickness).
Preparation of samples for E-Screen bioassay
Prior to each analysis the retention time of a standard mixture, including 5α-dihydroprogesterone, testosterone and estrone, was used to control and adjust time windows for collection of the HPLC fractions.
The fractions were collected in glass tubes and evaporated to dryness at 40°C under a gentle nitrogen stream. The dried sample was reconstituted in 20 μL EtOH/DMSO/Milli-Q water (50:10:40, vol/vol/vol) by vortexing for 30 sec. Then 200 μL CT-FCS was added and again the content was mixed by vortexing. The sample was divided in two aliquots of 100 μL in polypropylene tubes; tube A and B. To tube A, 900 μL estrogen-free medium was added. From this solution, aliquots of 200 μL and 100 μL were transferred to new polypropylene tubes containing 800 μL and 900 μL estrogen-free medium, respectively. To tube B, 900 μL estrogen-free medium supplemented with 10 pM E2 was added, after which aliquots of 200 μL and 100 μL were transferred to new polypropylene tubes containing 800 μL and 900 μL estrogen-free medium supplemented with 10 pM E2, respectively. Thus, all serum samples were analyzed as undiluted samples and as 5- and 10-fold dilutions as well as with and without E2. Prior to the analysis, it was confirmed that the solvent concentration (0.5 % ethanol and 0.1 % DMSO) in the final samples did not affect cell proliferation. Sterile filtering of the samples was unnecessary and the samples were prepared immediately prior to use.
Recovery of xenoestrogens after reconstitution
Stock solutions of PCB118, PCB153, o,p'-DDT and p,p'-DDE, either alone or in mixture, were diluted to a final concentration of 50 nM in 13 mL HPLC mobile phase (90 % A and 10 % B) in glass tubes. The sample was divided in two aliquots of 6.225 mL (equal to the volume of Fraction-1) in glass tubes; tube 1 and 2. Tube 1 was evaporated to dryness at 40°C under a gentle nitrogen stream. The dried sample was reconstituted in 20 μL EtOH/DMSO/Milli-Q water (50:10:40, vol/vol/vol) by vortexing for 30 sec. Then, 200 μL CT-FCS was added and again the content was mixed by vortexing. Finally, 1.8 mL estrogen-free medium was added to the vial, after which an aliquot of 2.0 mL was extracted as described for serum samples by Brock et al, 1996  using a Strata 500 mg trifunctional C18-e SPE column and a Strata 500 mg Florisil Pesticide Residue column (Phenomenex, Torrance, CA). The eluted solvents were collected in a tarred disposable centrifugation tube and evaporated at 30°C under a gentle nitrogen stream to about 0.5 mL. After weighing, the remaining amount was calculated and the volume adjusted to 1000 μL with 2,2,4-trimethylpentane. Tube 2 was evaporated at 40°C under a gentle nitrogen stream to about 0.25 mL. Again, the remaining amount was calculated, and the volume adjusted to 1000 μL with 2,2,4-trimethylpentane. The concentration was determined in an aliquot of 2 μL by GC analysis.
Microwell E-Screen bioassay
Stock cultures of MCF-7 BUS cells (passage 113–120) were grown in Dulbecco's modified Eagle's medium (DMEM) containing 10 % FCS supplemented with 4 mM glutamine, 15 mM 4-(2-hydroxyethyl)-1-piperazineethanesulfonic acid (HEPES) and 54 μg/L gentamicin sulfate in an atmosphere of 5 % CO2/95 % air under saturating humidity at 37°C. The microwell E-Screen was performed as described in Rasmussen and Nielsen, 2002 . Briefly, cells (4500 cells/well) were seeded in 96-well Nunclon Delta MicroWell plates (Nunc, Roskilde, Denmark) and after 24 hr, samples were added in estrogen-free medium (phenol red-free DMEM containing 10% CT-FCS supplemented with 4 mM glutamine, 20 mM HEPES, 0.1% sodium bicarbonate and 3 μg/L insulin). In each experiment, a standard curve for 1 pM – 10 nM E2 was included. After 6 days, cells were fixed with TCA and stained with SRB, after which bound dye was solubilized with 200 μL Tris base. The absorbance at 492 nm was determined directly in the microwell culture plate using a microplate reader (Dynatech MRX, Chantilly, VA, US).
Proliferative effect (PE)
The endpoint of the E-Screen bioassay is the number of cells after treatment compared to the number of cells in a negative control sample (cell treated with estrogen-free medium supplemented with solvent only). Thus, the PE was calculated as the ratio between the maximum cell proliferation achieved with the test sample and with the negative control:
Relative proliferative effect (RPE)
For each test sample the RPE was calculated as suggested by Sonnenschein, Soto and coworkers in 1995  from the PE of the test sample and the PE of 1 nM E2 in the same experiment:
Because 1 nM E2 induces maximum response in the E-Screen bioassay, the RPE describes the ability of the test sample to induce cell proliferation relative to maximum E2-induced cell proliferation. Thus, the RPE describes the efficacy of the test sample relative to that of E2.
However, the PE of 10 pM E2 was used to calculate the RPE of those experiments where mixture effects were studied because this concentration induce one-half of the maximum response. Thus, this RPE describes whether the test sample has enhancing or inhibiting effects on E2-induced cell proliferation, e.g., have RPE values above or below 100 %.
Relative proliferative potency (RPP)
For each individual compound, the RPP was calculated as suggested by Sonnenschein, Soto and coworkers in 1995  as the ratio between the lowest concentration of E2 that induce maximum response (MOECE2, maximum observed effect concentration) and the lowest concentration of test compound that induce maximum response (MOECtest compound):
Thus, the RPP describes the potency of the test compound relative to that of E2.
The estrogenic response of a serum sample was regarded positive when its RPE value was significantly above background noise, i.e., the variability of negative control values. For the biomarker assay, the background was defined as the mean of solvent-treated controls plus three times the standard deviation.
Concentration-response relationships for individual compounds were based on at least three independent experiments. Homogeneity of variance between the experiments was tested by Bartlett's test. The data were logarithmically transformed if necessary before analysis of variance (ANOVA). If the ANOVA test showed a significant difference (P < 0.05), the Tukey's Multiple Comparisons Test was used to identify differences between means. Associations between the biomarker response determined in serum and the concentration of environmental pollutants determined in milk were calculated using Pearson correlation coefficients. The data were logarithmically transformed before conducting the analysis.
Establishment of HPLC fractions
The advantage of using normal phase chromatography (NPC), where apolar substances are eluted prior to more polar substances, is obvious for many reasons. A range of identified endocrine disrupters are by nature more lipophilic than the endogenous hormones, and elute therefore prior to the range of hormones and their metabolites in a NPC system. Furthermore, this system utilizes water free eluents, thereby allowing evaporation of solvents at relative low temperatures and thus minimizing the risk of a loss of compounds with low vapor pressure. The use of a gradient system is essential to elute the most hydrophilic substances prior to the next injection.
Recovery (%) of supplemented organochlorines from CT-FCS after HPLC separation
Retention time and estrogenic response of indicative compounds
RPE ± SD
58 ± 3
16 ± 2
92 ± 6
97 ± 3
64 ± 5
16 ± 2
92 ± 2
34 ± 5
84 ± 8
7 ± 1
30 ± 1
100 ± 7
77 ± 2
103 ± 3
0.001 – 50
0.001 – 50
92 ± 2
0.001 – 50
0.001 – 50
96 ± 7
44 ± 9
2.29 + 2.88
57 ± 8
0.001 – 50
24 ± 4
0.001 – 50
61 ± 2
Recovery of organochlorines after reconstitution
Comparison of the recovery (%) of organochlorines (50 nM each) from reconstituted samples supplemented with a single compound or a mixture of four.
Functional estrogenic response of selected environmental pollutants
These results therefore indicate that the parent PCB congeners that constitute the main part of the PCBs present in serum do not cause an estrogenic effect but rather an antiestrogenic effect, though other persistent pollutants usually occurring along with the PCBs may cause an estrogenic effect.
Functional estrogenic response of serum from women
To avoid false positive results, both subfractions s4 and s8 were removed to exclude possible pregnancy-related estrogens present in serum from pregnant women. The estrogenic response of the resulting Fr-1 extracts (Figure 2, purple bars) was not different from that of samples from non-pregnant women (Figure 2, blue bars) in this cohort, and the groups were therefore merged into one control cohort. Of this cohort, 22.7 % of the samples induced cell proliferation above the background level.
Functional estrogenic response of serum from PCB-exposed women
The serum estrogenicity was then determined from samples obtained from pregnant (34th week) Faroese women. After HPLC separation, subfractions s4 and s8 were removed as described above, and all samples were tested separately by E-Screen analysis as undiluted and as 5- and 10-fold dilutions; below we present the results from the undiluted samples.
Correlation between environmental pollutant concentration and biomarker response
The concentration of environmental pollutants in breast milk from the subjects examined had been determined by GC analyses (Heinzow B. Unpublished data). The biomarker results were compared with the lipid-based concentrations of PCBs and related pollutants. However, except for β-HCH, no statistically significant correlations were found between serum estrogenicity and any of the organochlorines analyzed (results not shown). The samples were then divided into two groups with high and low total PCB concentration, respectively, and the groups were compared with the pollutant levels individually. Again, no association with estrogenic response was observed. Correlation analyses between the serum antiestrogenic results and the lipid-based concentrations of PCBs and related pollutants were also performed but no statistically significant correlations were found between the biomarker response and any of the organochlorines analyzed.
Estrogenicity of environmental pollutants
The estrogenic activities of a range of individual compounds in this study confirm the reported estrogenicity of the persistent organochlorine insecticides, o,p'-DDT, methoxychlor and dieldrin [18–22]. The more stable metabolite of p,p'-DDT, p,p'-DDE, also induced cell proliferation in accordance with previous reports [20, 23]. p,p'-DDE and PCBs constitute the major part of organochlorine residues found in human adipose tissue, milk or blood . Depending on the position and number of chlorine substitutions, a range of endocrine disrupting properties has been reported for different classes of PCB congeners and their metabolites [24–32]. In the present study, the major congeners PCB138, PCB153 and PCB180 did not induce an estrogenic response in the E-Screen bioassay, but they weakly inhibited E2-induced cell proliferation when analyzed in combination with E2 indicating that these compounds might antagonize the activity of endogenous estrogen. Some of the effects previously ascribed to parent PCB congeners may rather be caused by more potent metabolites, e.g., hydroxylated metabolites . We examined the estrogenicity of the three most abundant hydroxylated metabolites of PCBs in human serum, and 4-OH-CB187 was found to be weakly estrogenic at the highest concentration tested. The environmental pollutant β-HCH was also found to be a potent xenoestrogen, thus confirming earlier reports . Additionally, the observed responses when cells were treated with β-HCH, p,p'-DDE or methoxychlor in combination with E2, were larger than the response of E2 alone, thereby indicating that these xenoestrogenic compounds act together with endogenous estrogen to produce an enhanced estrogenic effect. Thus, our results indicate that mixtures of estrogenic compounds seem to cause additive effects and thus support reports of additive effects of estrogenic compounds in vitro [34, 35]. The data available are, however, too limited to allow a prediction of the combined estrogenic potential from a conventional chemical concentration profile of a serum sample.
Establishment of the biomarker assay
The HPLC method was optimized to allow extraction, separation and collection of mixtures of compounds in serum samples based on their polarity. The SPE columns used for the extraction in this study constitute a "universal" polymeric sorbent that is unique due to its balanced ratio of two monomers, the lipophilic divinylbenzene, and the hydrophilic N-vinylpyrrolidone, and allows extraction of acidic, basic, and neutral compounds in a wide range of polarities on a single SPE column. Furthermore, this mixed type of sorbent has a larger surface area and a greater capacity for a wide range of compounds than do silica-based materials .
Our HPLC gradient system differs from that proposed by Sonnenschein, Soto and coworkers , because we implement a relatively long isocratic elution period prior to applying the gradient. By doing so, the lipophilic hormone-free elution period is condensed, and the elution period for midpolar compounds is expanded. This approach was chosen to increase the ability to separate compounds in the mid-polar region where endogenous hormones elute, thus allowing us to eliminate the endogenous hormones without loosing too many of the exogenous compounds.
A caveat that needs to be addressed is that the exclusion of specific fractions, equivalent to a certain range of polarities, will potentially also exclude some exogenous compounds with retention times (polarities) identical to the endogenous hormones. This is, of course, mainly a problem when separating unknown mixtures, as individual retention times of known compounds would otherwise be available. The wide range of compounds included in this study with individual retention times demonstrates the potential of this semi-preparative method. Thus, this method will allow the user to collect fractions for specific compounds, mixtures of compounds with known polarity, or to a total serum sample after exclusion of endogenous hormones. The HPLC separation may in principle be followed by a range of different effect monitoring assays depending on the compounds separated and the focus of the research. Our focus in this study was mixtures of exogenous compounds potentially acting as xenoestrogens.
The ability to separate, collect and analyze mixtures of exogenous compounds instead of individual chemicals is a significant feature allowing evaluation of combined effects of chemicals present below their individual no-observed-effect concentrations. To test estrogenic as well as anti-estrogenic effects of mixtures of chemicals in human serum, our improved in vitro E-Screen bioassay  is an effect monitoring system well suited to HPLC-separated extracts. Together, the semi-preparative separation and the E-Screen bioassay act as a biomarker that will allow us not only to test individual compounds, but also to address the problems related to environmental or occupational exposure to mixtures of xenoestrogens each present at low concentrations .
We have used this biomarker assay to study the combined functional estrogenic response in serum from pregnant women exposed to mixtures of PCBs and other persistent organochlorines. These compounds are lipophilic to an extent that allowed us to apply the HPLC-fraction eluting within the initial 5.5 minutes (after exclusion of two minor subfractions) for E-Screen analysis. In addition, this group of women had a high level of endogenous estrogens due to pregnancy, thus making the elimination of the endogenous hormones without loosing too many of the exogenous chemicals a challenging task.
Evaluation of Fraction-1 from PCB-exposed women
The biomarker analysis showed large variations in serum estrogenicity within the cohort of PCB-exposed Faroese women and more than two samples out of three induced a positive estrogenic response. In the presence of E2, an increased induction of cell proliferation compared to that of E2 alone was observed in most of these samples, thus indicating additive mixture effects.
Although it was not a main objective of this study to search for individually causative chemicals, efforts were made to assess relationships between the biomarker data and the concentrations of major environmental pollutants present in milk fat from the same subjects. Except for β-HCH, we did not find any significant correlations between the functional estrogenic response and total PCB, PCB105, PCB118, PCB138, PCB153, PCB156 or PCB180, or other environmental pollutants such as o,p'-DDT, p,p'-DDE, HCB, or trans-nonachlor. These chemicals were analyzed as part of a routine battery of compounds that were selected for other reasons than endocrine disruption. However, because concentrations of persistent lipophilic compounds show collinearity, these pesticide residues and persistent industrial chemicals are likely to represent the overall body burden of persistent organohalogen compounds.
A likely explanation for the lack of significant correlation between concentrations of these chemicals and our biomarker results could be that the chemical analysis did not include the chemicals primarily responsible for the biomarker effect. In addition, the concentration of the individual compounds in human serum may be below the concentration that is needed to elicit effects in our in vitro cell proliferation assay. The combined response of the mixture present in serum might, however, be significantly enhanced, even when each single compound is present below its detectable effect limit. Kortenkamp and coworkers have shown that the combined effect of a mixture of xenoestrogens can produce a significant estrogenic response even when each individual xenoestrogen is present at a concentration that alone does not produce a detectable effect [34, 35]. As a result, an explanation in terms of single causative compounds may not be expected, because humans are exposed to complex mixtures of environmental pollutants. A number of compounds, each present at low, perhaps ineffective concentrations, may act together to produce effects that are statistically significant in the biomarker assay. Thus, the lack of correlation speaks in favor of the biomarker assay, rather than against, as the method allows detection of the combined and functional xenoestrogenic response.
This biomarker assay is recommended as an appropriate and useful tool for assessing the functional estrogenic potential of complex mixtures present in human serum. Because of the limited insight into the endocrine disrupting effects of single chemicals and their mixtures, it may provide a more accurate prediction of the endocrine disrupting impact than even the most detailed chemical analysis. Thus, even if the estrogenic activity of all compounds were known, the combined effect of possible additive and/or inhibiting interaction of xenoestrogens in a biological sample may be difficult to predict from chemical analysis of single compounds alone.
Our finding of an increased average estrogenicity of serum extracts obtained from an exposed population merits attention and should inspire further studies into the causes of this response. Our results do not necessarily indicate an increased risk of adverse effects, but it should lead to further efforts to characterize this exposure and its possible effects. For such studies, this biomarker approach may serve as a useful supplement to standard exposure assessment.
List of abbreviations used
hydroxylated metabolites of polychlorinated biphenyls
charcoal/dextran-treated fetal calf serum
Dulbecco's modified Eagle's medium
fetal calf serum
high-performance liquid chromatography
maximum observed effect concentration
normal phase chromatography
relative proliferative effect
relative proliferative potency
- Tris base:
We thank Ana Soto for providing MCF-7 BUS cells, Aake Bergman for hydroxylated PCBs, Astra Zeneca for ICI 182,780, Birger Heinzow for unpublished data on milk lipid concentrations, Ranja Bjerring and Vibeke K. Pedersen for technical assistance. We are grateful to the cohort families for their loyal support and to the competent staff at the Faroese Hospital System.
The study received its main financial support from the Danish Environmental Research Programme via the Danish Centre for Environmental Estrogen Research. Additional support was obtained from the Danish Health Research Council, from the National Institute of Environmental Health Sciences (ES 11681) and from the Danish Environmental Protection Agency as part of the environmental support program, Dancea – Danish Cooperation for Environment in the Arctic. The authors are solely responsible for all results and conclusions presented in this article, and do not necessarily reflect the position of the Danish Environmental Protection Agency.
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