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Expression profiling of estrogenic compounds using a sheepshead minnow cDNA macroarray. (Article).

A variety of anthropogenic compounds are capable of binding to the estrogen receptor (ER) of vertebrate species. Binding of these chemicals to the ER can interfere with homeostasis by altering normal gene expression patterns. The purpose of this study was to characterize the expression of 30 genes using a sheepshead minnow (Cyprinodon variegatus) cDNA macroarray. Many of the genes on the array were previously identified by differential display reverse transcriptase-polymerase chain reaction to be upregulated or downregulated in sheepshead minnows treated through aqueous exposure to known or suspected estrogenic chemicals. The results of this study show that 17[beta]-estradiol (E2), 17[alpha]-ethinyl estradiol (E[E.sub.2]), diethylstilbestrol (DES), and methoxychlor (MXC) have similar genetic signatures for the 30 genes examined. The genetic signature of fish treated with p-nonylphenol was identical in pattern to that in fish treated with [E.sub.2], E[E.sub.2], DES, and MXC except for the additional upregulation of a cDNA done that shares similarity to ubiquitin-conjugating enzyme 9. Endosulfan produced results that resembled the gene expression patterns of untreated control fish with exception of the upregulation of estrogen receptor [alpha] and the downregulation of a cDNA clone that shares similarity to 3-hydroxy-3-methylglutaryl-coenzyme A reductase. We show that our estrogen-responsive cDNA macroarray can detect dose-dependent changes in gene expression patterns in fish treated with E[E.sub.2]. Key words: array, biomarkers, endocrine disruption, estrogen, fish, macroarray. Environ Health Perspect 111:839-846 (2003). doi:10.1289/txg.5752 available via [Online 6 November 2002]


Endocrine-disrupting compounds (EDCs) that mimic estrogens come from a variety of sources, including byproducts from manufacturing, effluent from wastewater treatment plants, and pesticides (Nimrod and Benson 1996a, 1996b; Solomon and Schettler 2000; Sumpter 1998). Exposure to these estrogenic EDCs may lead to a variety of physiologic problems in humans, including vaginal cancer, reproductive tract abnormalities, cryptorchidism, semen abnormalities, and hypospadias (Carlsen et al. 1993; Giusti et al. 1995; Giwercman et al. 1993; Sharpe and Skakkebaek 1993; Toppari 1996; Toppari et al. 1996).

A principal role of the native estrogen 17[beta]-estradiol ([E.sub.2]) in the liver of adult female fish is to activate the synthesis of specific gene transcripts that encode proteins required for reproduction by binding to the estrogen receptor (ER). Several genes known to be activated by this process include those that encode the ER itself, vitellogenins (Vtgs), and choriogenins (Arukwe et al. 2001; Bowman et al. 2000; Celius et al. 2000; Denslow et al. 2001a, 2001b; Flouriot et al. 1995, 1996, 1997; Folmar et al. 2000; Funkenstein et al. 2000; Hemmer et al. 2001; Lattier et al. 2001; Le Guellec et al. 1988; Lim et al. 1991; Murata et al. 1997). Vtgs, the egg yolk precursor proteins, and choriogenins, which are required for making the inner covering of the egg, normally increase in the circulation of females during oogenesis (Mommsen and Walsh 1988; Oppen-Berntsen et al. 1992; Specker and Sullivan 1994; Tyler and Sumpter 1996). However, in males, the normal endogenous levels of [E.sub.2] are sufficient to induce only very small amounts of plasma Vtgs and choriogenins (Arukwe et al. 2001; Copeland et al. 1986). When males are exposed to natural or anthropogenic estrogens, which can either enhance the steady-state concentrations of endogenous [E.sub.2] or bind directly to the ER, the result is an increase in the circulating levels of Vtg and choriogenin proteins. Vtg and choriogenin synthesis in male fish have therefore become accepted assays for measuring exposure to estrogenic chemicals (Arukwe et al. 1997; Bevans et al. 1996; Celius et al. 1999; Celius and Walther 1998; Denslow et al. 1996; Folmar et al. 1996, 2000; Hemmer et al. 2001; Heppell et al. 1996; Jobling et al. 1995; Orlando et al. 1999; Sumpter and Jobling 1995).

A number of natural and synthetic chemicals in the environment are estrogenic in in vitro and in vivo assays, including 17[alpha]-ethinyl estradiol (E[E.sub.2]), diethylstilbestrol (DES), p-nonylphenol (PNP), methoxychlor (MXC), and endosulfan (ES) (Bowman et al. 2000; Bulger et al. 1978; Coldham et al. 1997; Denslow et al. 2001a, 2001b; Folmar et al. 2000; Hemmer et al. 2001; Larkin et al. in press; Nimrod and Benson 1997; Petit et al. 1997; Schlenk et al. 1998; Shelby et al. 1996; Soto et al. 1995; Vonier et al. 1996). E[E.sub.2] is currently used in oral contraceptives, and DES was once prescribed to prevent spontaneous abortion in early pregnancy (Herbst et al. 1971). PNP is the primary microbial degradation product of alkylphenol ethoxylates (Naylor et al. 1992), which are used as surfactants and emulsifiers in numerous industrial and commercial applications (Nimrod and Benson 1996a, 1996b). MXC and ES, which are both organochlorine pesticides, are used to control a variety of insects on food crops (Solomon and Schettler 2000).

There is emerging evidence that some estrogenic compounds may have additional modes of action independent of the ER. PNP, for example, enhances pregnane-X receptor-mediated transcription in COS-7 cells (Masuyama et al. 2000). Pregnane X is a nuclear receptor that regulates the expression of several genes, including cytochrome P450 3A (Bertilsson et al. 1998; Kliewer et al. 1998; Lehmann et al. 1998; Masuyama et al. 2000; Pascussi et al. 1999). Moreover, MXC induces gene expression in mice via a signaling pathway that does not involve ER[alpha] or ER[beta] (Ghosh et al. 1999; Waters et al. 2001). These studies suggest some genes may be differentially regulated by various estrogenic compounds and raises the possibility of specific genetic markers for some of the different EDCs that mimic [E.sub.2]. Using differential display reverse transcriptase-polymerase chain reaction (DD RT-PCR), we previously isolated 30 genes, several of which were upregulated or downregulated in sheepshead minnows (Cyprinodon variegatus) exposed to [E.sub.2]. Other genes that appeared to be constitutive were added to the array for normalization purposes. In this study we have characterized the expression of these genes by macroarray analysis, using RNA from livers of male sheepshead minnows receiving an aqueous exposure to environmentally relevant concentrations of [E.sub.2], E[E.sub.2], DES, PNP, MXC, or ES.

Materials and Methods

Amplification of cDNA to Be Spotted on Macroarrays

Minipreps of 30 cDNA clones derived from DD RT-PCR analysis (Denslow et al. 2001a, 2001b) were PCR-amplified in a 300-[micro]L reaction containing 1x PCR Buffer A (Promega, Madison, WI, USA), 2 mM Mg[Cl.sub.2] (Promega), 160 [micro]M each deoxynucleotide triphosphate (Stratagene, La Jolla, CA, USA), 0.4 [micro]M M13 primers (5'-GTT TTC CCA GTC ACG ACG TTG and 5'-GCG GAT AAC AAT TTC ACA CAG GA), and 1.25 units Taq polymerase (Promega). The PCR reaction conditions were as follows: 1 cycle at 80[degrees]C (1 min); 1 cycle at 94[degrees]C (2 min); 32 cycles at 94[degrees]C (1 min), 57[degrees]C (1 min), and 72[degrees]C (2 min); 1 cycle at 72[degrees]C (10 min), and then hold at 4[degrees]C. After completion of the PCR, the products were purified in a spin column (Qiagen, Chatsworth, CA, USA), then concentrated in a speed vacuum (Savant SVC100; Axon Instruments, Inc., Farmingdale, NY, USA). Aliquots of the PCR products were run on a 1.2% agarose gel containing 0.3 mM ethidium bromide. The gels were digitally imaged using a UVP Bio Doc-It camera (Ultra-Violet Laboratory Products, Upland, CA, USA), and the concentration of each PCR product was determined by comparing the intensity of each band to a standard curve derived from a low DNA mass ladder (Invitrogen Corp., Carlsbad, CA, USA). The PCR products were adjusted to a concentration of 160 ng/[micro]L cDNA template.

Thirty unique clones were spotted on the array. Of these, 19 were identified based on ,their similarity to sequences in the National Center for Biotechnology Information (NCBI) database as determined by the Basic Local Alignment Search Tool (BLAST X) (Altschul et al. 1997). The highest expectation (E) value obtained is shown in parentheses. The 30 unique genes spotted include [alpha]-microglobulin/bikunin precursor protein (AMBP) (E = 1e-11), [beta]-actin (GenBank accession no. AF253319), choriogenin 2 (E = 1e-45), choriogenin 3 (E = 4e-43), coagulation factor XI (E = 3e-12), ER[alpha] (E = 1e-71), glycosylate reductase (E = 3e-14), hepatic lipase precursor (E = 7e-6), 3-hydroxy-3-methylglutaryl-coenzyme A (CoA) reductase (E = 9e-51), low-molecular-mass protein 2 (E = 2e-12), transferrin (E = 8e-26), ubiquitin-conjugating enzyme 9 (the cDNA clone is 87% identical at the 5' end to an EST clone (GenBank accession no. BJ028023) that has an E value of 1e-11 with ubiquitin-conjugating enzyme 9), unknown protein (E = 4E-23), Vtg 1 (GenBank accession no. AF239720), Vtg 2 (GenBank accession no. AF239721), ribosomal protein L8 (E = 7e-56), ribosomal protein S8 (E = 5e-29), and two unique genes similar to ribosomal protein S9 (E = 2e-45 and 4e-5). The remaining 11 clones, designated NDN1-A, ND1-E, ND9C-D2, ND10C-A, ND13C-E, ND15-B3, ND-17E3, ND96-C, ND98-E, ND102-A, and ND103-B, do not match any sequences in the database.

Array Controls

Various controls were also spotted onto the membranes, which provided information about cDNA labeling efficiency, blocking at the prehybridization step, and nonspecific binding. These controls included three Arabidopsis thaliana cDNA clones, Cot-1 repetitive sequences, poly A sequence (SpotReport 3; Stratagene), and an M13 sequence (vector but no cDNA insert). We also assessed the consistency of our technique by spotting on the array multiple cDNA products from the same genes amplified in separate PCR reactions. Genes spotted multiple times on different parts of the array include 3-hydroxy-3-methylglutaryl-CoA reductase, glycosylate reductase, choriogenin 2, a clone that shares homology to Unknown protein (GenBank accession no. AAH10857), and several unidentified clones (ND98-E, ND1-E, ND2C-A, ND62-B2, and ND102-A). In all, each membrane had 62 spots in duplicate that included the 30 unique genes described above, the multiple spotted genes, and the procedural controls.

Spotting of the Macroarrays

The PCR products were loaded into 96-well plates (Fisher Scientific, Pittsburgh, PA, USA), denatured with 3 M NaOH, heated to 65[degrees]C for 10 min, then immediately quenched on ice. Twenty times saline sodium citrate (SSC) (3 M NaCl, 0.3 M sodium citrate, pH 7.0) containing 0.01 mM bromophenol blue was added to the samples to yield a final concentration of 0.3 M NaOH, 6x SSC, and 100 ng/[micro]L cDNA template. The PCR products were robotically spotted (Biomek 2000; Beckman Coulter, Fullerton, CA, USA) in duplicate onto 11.5 x 7.6 cm neutral nylon membranes (Fisher Scientific) using 100-nL pins. Membranes were ultraviolet cross-linked at 1 x [10.sup.5] [micro]J (UV Stratalinker 1800; Stratagene) and stored under vacuum at room temperature until hybridization.

Sample Extraction

Total hepatic messenger ribonucleic acid (mRNA) was extracted using affinity columns (Qiagen) from adult male sheepshead minnows treated by aqueous exposure to either 65.14 ng/L [E.sub.2], 109 ng/L E[E.sub.2], 100 ng/L DES, 11.81 [micro]g/L PNP, 590.3 ng/L ES, 5.59 [micro]g/L MXC, or triethylene glycol (vehicle control) using a flow-through dosing apparatus as described previously (Folmar et al. 2000; Hemmer et al. 2001). All animals used in the research were treated humanely according to institutional guidelines (U.S. Environmental Protection Agency), with due consideration for the alleviation of distress and discomfort. Three fish were used per treatment group. Criteria for selection of samples from each compound tested were based on previously generated dose-response curves (Folmar et al. 2000; Hemmer et al. 2001) and chosen to give similar levels of expression of Vtg mRNA, a well-established estrogenic biomarker (Bowman et al. 2000; Sumpter and Jobling 1995). By selecting the concentration and length of exposure to yield similar Vtg mRNA expression levels, we accounted for differing potencies among the chemicals tested. On the basis of this criterion, length of exposure was 4 days for E[E.sub.2] and DES, 5 days for [E.sub.2] and PNP, and 13 days for MXC. ES treatment levels ranging from 68.8 ng/L to 788.33 ng/L failed to induce Vtg mRNA. We chose a treatment of 590.3 ng/L of ES for these analyses. This level of ES was slightly below the maximum acceptable toxicant concentration (MATC) derived for ES for sheepshead minnows (Hansen and Cripe 1991). ES is available commercially as a mixture of two ES isomers, ct and [beta], which are typically supplied at the ratios of 65-70% [alpha] and 30-35% [beta].

Labeling of RNA and Hybridization

Radiolabeled probes were generated by random primer labeling of DNase-treated (DNA-free; Ambion, Inc., Austin, TX, USA) total RNA from male sheepshead minnow livers with [[alpha]-[sup.33]P]dATP (2'-deoxyadenosine 5'-triphosphate) (Strip-EZ RT, Ambion). The blots were prehybridized with ULTRAArray hybridization buffer (Ambion) at 64[degrees]C for 3 hr. After prehybridization, each probe was diluted 20-fold with 10 mM disodium ethylenediaminetetraacetate, pH 8.0, to yield 1 x [10.sup.6] cpm incorporated [sup.33]P/mL hybridization solution. The diluted probes were heated to 95[degrees]C for 5 min, quenched on ice for 1 min, and added directly to the prehybridization buffer. The blots were then hybridized overnight at 64[degrees]C. After hybridization, the blots were washed 4 x 15 min each with low (2x SSC, 0.5% sodium dodecyl sulfate [SDS]) and high (0.5x SSC and 0.5% SDS) stringency washes (Ambion) at 64[degrees]C.

Detection and Normalization

The membranes were exposed to a phosphor screen (Molecular Dynamics, Piscataway, NJ, USA) at room temperature for 48 hr. The blots were quantitatively evaluated using a Typhoon 8600 imaging system (Molecular Dynamics). For each cDNA clone the general background of each membrane was subtracted from the average value of the duplicate spots on the membrane. The values were normalized to the average value of 11 cDNA clones. These genes include ribosomal proteins L8 and S8, two unique genes similar to ribosomal protein S9, and several clones (designated NDN1A, ND9C-D2, ND10C-A, ND13C-E, ND17-E3, ND102-A, and D103-B) that do not match any sequences in the NCBI database. These genes were chosen to normalize the data because they were equally expressed in control and treated fish by differential display analysis (data not shown) and/or they did not fluctuate more than 1.3-fold on macro arrays from [E.sub.2]-treated and control fish (Larkin et al. 2002).

Gene array data were analyzed using linear regression and 1-way analysis of variance, with Tukey post hoc analysis (SPSS, Jandel, CA, USA).


The advent of array technology has enabled researchers to analyze hundreds to thousands of genes on a single array. As a first step toward using array technology to assess exposure to environmental estrogens, we determined the variability between our macroarrays. To accomplish this, aliquots of identical RNA samples were hybridized onto two separate membranes (Figure 1A). Figure 1B illustrates a scatter plot correlating the intensity values from each spot from the two membranes. The data points in the graph cluster along a slope of one for all of the spots, including both the low and highly expressed cDNA clones. Similar values were observed in four replicate experiments (mean [R.sup.2] 0.93, range 0.88-0.97).


cDNAs corresponding to 30 unique genes were spotted on the macroarrays. These genes were originally isolated from DD RT-PCR experiments by comparing gene expression profiles from control and [E.sub.2]-treated fish. Hepatic mRNAs from exposed fish were converted to cDNAs and radiolabeled. The samples were individually hybridized to separate membranes to determine if fish treated with [E.sub.2], E[E.sub.2], DES, PNP, MXC, and ES shared similar expression profiles. Three separate fish were used for each treatment. Figure 2 contains representative membranes from the different treatments; Figure 3 shows a graphic representation of the data. Figure 3A illustrates the mean [+ or -] SEM intensity values for each of the cDNA clones arranged in order of their expression. Figure 3B illustrates the mean intensity values for each of the cDNA clones for [E.sub.2], E[E.sub.2], DES, PNP, MXC, or ES divided by the mean intensity values of the respective cDNA clones from the untreated control fish.


Several of the genes spotted on the array were upregulated or downregulated in [E.sub.2]-treated fish compared with controls. The genes were identified on the basis of the intensity values of the 11 constitutively expressed cDNA clones used to normalize the data (see "Materials and Methods"). To identify differentially regulated genes, the 11 reference genes were numerically ranked with respect to each other within a treatment. The upper confidence limit was set as the mean plus one standard deviation of the highest ranked value across the treatment groups (mean 1.38 [+ or -] 0.28). Likewise, the lower confidence limit was set as the mean plus one standard deviation of the lowest ranked value across the treatment groups (mean 0.63 [+ or -] 0.21). On the basis of these criteria, any cDNA clones in the macroarray experiments above a 1.66-fold induction were designated as upregulated with respect to control fish, and any cDNA clones that had a value below 0.42 were designated as downregulated. These expression levels of 1.66 and 0.42 are similar to the 2-fold change in expression used as cutoffs by other investigators (Coller et al. 2000; Wang et al. 2001). The upper (1.66) and lower (0.42) confidence limits used for these experiments are conservative, based on the observation that several genes whose expression levels fell within these values were identified as differentially regulated by DD RT-PCR (data not shown).

Of the 30 genes used on our array, six genes were found to be upregulated by [E.sub.2], including Vtgs 1 and 2, choriogenins 2 and 3, ER[alpha], and coagulation factor XI. Three genes found to be downregulated by [E.sub.2] were transferrin, [beta]-actin, and AMBP. The remaining genes did not appear to be differentially regulated by [E.sub.2] when compared with controls. All the genes identified as upregulated or downregulated on the arrays showed identical expression patterns by DD RT-PCR (data not shown).

The 9 genes upregulated or downregulated by E[E.sub.2], DES, PNP, and MXC exposures showed a pattern of expression similar to that of the [E.sub.2] treatment. Interestingly, a cDNA clone that shares similarity to ubiquitin-conjugating enzyme 9 was significantly (p < 0.05) upregulated only in the PNP treatments. Eight of the 9 genes upregulated or downregulated for [E.sub.2], E[E.sub.2], DES, PNP, and MXC did not fluctuate for ES-treated fish but instead resembled the pattern observed in control fish. The only exception was ER[alpha], which appeared to be upregulated for all the compounds, including ES. An additional cDNA clone that shares similarity to 3-hydroxy-3methylglutaryl-CoA reductase appeared to be slightly downregulated (decrease of 2.9fold) in fish treated with ES compared with all the other treatments and the controls.

To determine if the gene expression profiles on the array could be verified by other techniques that monitor mRNA expression, we compared the expression profiles of several genes on the arrays (Vtg 2, choriogenin 2, and transferrin) to their profile by Northern blots and DD RT-PCR. Figure 4A, B shows that both Vtg 2 and choriogenin 2 mRNA levels increase in fish treated with [E.sub.2], as measured by Northern blots and DD RT-PCR. Figure 4C illustrates that transferrin decreases with [E.sub.2] treatment. We have not quantified the response by DD RT-PCR and Northern blot analysis compared with the arrays because limited amounts of samples required the use of different RNA samples in these experiments.


To assess whether the arrays could be used as a quantitative tool to measure the expression of multiple genes at varying concentrations of an estrogenic chemical, we examined male sheepshead minnows exposed for 4 days to nominal concentrations of 0, 20, 100, or 1000 ng/L E[E.sub.2] (Folmar et al. 2000; Hemmer et al. 2001). The measured concentrations were 24, 109, or 832 ng/L, respectively. Figure 5 contains representative arrays from the three E[E.sub.2] treatments. Figure 6 contains graphic illustrations of genes whose expression levels significantly changed by more than 2-fold in one or more of the three E[E.sub.2] concentrations examined (p < 0.05). Vtgs 1 and 2, choriogenins 2 and 3, ER[alpha], and coagulation factor XI increased in a concentration-dependent manner in the E[E.sub.2]-exposed fish (Figure 6A). Three other genes, transferrin, AMBP, and [beta]-actin, appeared to decrease in a dose-dependent manner (Figure 6B). These genes were the same genes that were upregulated or downregulated in the fish exposed to [E.sub.2], DES, PNP, and MXC (Figure 3).



The goal of this study was to determine the expression profile of 30 estrogen-responsive genes in sheepshead minnows treated with both strong and weak estrogenic chemicals in a flow-through aquatic exposure system. The 30 genes arrayed were a subset of all genes inducible by [E.sub.2]. These genes were isolated by DD RT-PCR in screening experiments where approximately 18% of RNA messages expressed in the livers of sheepshead minnows were tested (Denslow et al. 2001a, 2001b). In addition to genes that were upregulated and downregulated by [E.sub.2], the array also contained several constitutive genes. Although most of the genes on the array have been identified, we are continuing to screen our sheepshead minnow cDNA libraries to identify the remainder.

We evaluated the reproducibility of our printing process for the cDNAs by comparing the spot intensity for each of the duplicate spots for each gene on a membrane. The spot intensity varied on average by 6.5% between paired spots on a single membrane. When aliquots of RNA from identical samples were evaluated on membranes printed at the beginning, middle, and end of the printing process, we observed similar expression patterns on all membranes (data not shown). The inter-assay variability was minimal, as determined by the high [R.sup.2] value (mean 0.93) observed when aliquots of the same RNA samples were hybridized to independent membranes. Slightly more variability appeared to be associated with the lower intensity values during the self-self hybridization test, a condition previously observed (Richmond et al. 1999). The cDNA labeling efficiency, blocking at the prehybridization step, and nonspecific binding also were consistent between the different treatments, based on similar expression of the various procedural controls present on each membrane.

Our results show similar expression patterns for the estrogen-responsive genes on our array (Figure 3A, B). Fish exposed to [E.sub.2], E[E.sub.2], DES, and MXC had identical genetic signatures for the 30 genes examined, whereas fish exposed to PNP differed by the increased expression of one additional cDNA clone that shares similarity to ubiquitin-conjugating enzyme 9. Six genes (Vtgs 1 and 2, choriogenins 2 and 3, ER[alpha], and coagulation factor XI) were upregulated in sheepshead minnows exposed to [E.sub.2], E[E.sub.2], DES, PNP, or MXC. The upregulation of the first 5 of the 6 identified genes was expected, considering their involvement in the estrogen-regulated process of oogenesis. The Vtgs, choriogenins, and ER[alpha] gene transcripts are induced by these chemicals in a variety of species (Arukwe et al. 2001; Bowman et al. 2000; Celius et al. 2000; Denslow et al. 200la, 200lb; Folmar et al. 2000; Hemmer et al. 2001; Larkin et al. in press; Lattier et al. 2001). Because the ubiquitin-conjugating enzyme was not significantly upregulated to the same levels by the natural or pharmaceutical estrogens, its regulation may be related to another detoxification or metabolic pathway specific to alkylphenols. Ubiquitinated proteins are targets for proteolysis and other cellular functions, including protein trafficking and kinase activation. The different expression pattern for PNP may be valuable when trying to identify specific estrogenic agents in mixed effluents such as sewage treatment plant discharges.

Three genes (transferrin, [beta]-actin, and AMBP) were downregulated in sheepshead minnows exposed to [E.sub.2], E[E.sub.2], DES, PNP, or MXC. Transferrin, a protein involved with iron transport, is downregulated by [E.sub.2] and other estrogenic compounds in the livers of largemouth bass (Larkin et al. in press); however, it is upregulated by [E.sub.2] in livers of chickens (Lee et al. 1978; McKnight et al. 1980). These observations suggest that transferrin may be regulated differently across vertebrate classes. [beta]-Actin, a housekeeping gene commonly used to normalize gene expression assays, was also downregulated on our arrays for fish treated with [E.sub.2], E[E.sub.2], DES, PNP, and MXC. These results suggest that [beta]-actin may not be a good housekeeping gene for estrogen-responsive arrays. The AMBP gives rise to two proteins, [[alpha].sub.1]-microglobulin and bikunin. The exact function of [[alpha].sub.1]-microglobulin is unknown. However, this protein is thought to be involved in immunoregulation (Akerstrom et al. 2000). Bikunin is the active subunit of protein/carbohydrate complexes that together comprise the inter-[alpha]inhibitor protein family, which plays a major role in extracellular matrix stability and integrity (Bost et al. 1998). It is of interest to note that both [beta]-actin and the precursor protein for bikunin, two proteins involved with the formation of the cytoskeleton, were both downregulated in fish treated with estrogenic chemicals. These data are consistent with the observations that several estrogenic compounds disrupt cytoskeleton components in vitro (Bocca et al. 2001; Chaudoreille et al. 1991; Sakakibara et al. 1991).

The gene expression profile of fish treated with ES did not resemble that of the fish treated with the other test chemicals but instead resembled more the expression pattern of the control fish. Several laboratories have shown that micromolar (or greater) concentrations of ES can induce MCF-7 cells to proliferate (Soto et al. 1995), interact with the trout ER (Petit et al. 1997), and induce Vtg mRNA in trout hepatocytes (Petit et al. 1997). However, in other studies, micromolar concentrations of ES were unable to interact with a mouse ER to transactivate a reporter construct in HeLa cells (Shelby et al. 1996) or compete well for binding to the mouse ER (Shelby et al. 1996). The doses used in the above in vitro assays would be considered pharmacological in a live animal (Hansen and Cripe 1991). Therefore, to determine whether ES was estrogenic in a live animal, we exposed sheepshead minnows to 590.3 ng/L ES, a concentration within the MATC of 0.58-1.2 [micro]g/L for aquatic animals. ES appears not to regulate (up or down) the same set of genes regulated by the other estrogenic compounds, with the exception of ER[alpha], which was upregulated to a similar level in all treatment groups. This observation suggests the cascade of events downstream of the ER in the ES-exposed fish differs from that observed in the fish exposed to the natural and pharmaceutical estrogens and PNP. A second cDNA clone, 3-hydroxy-3-methylglutaryl-CoA reducrase, appeared to be slightly downregulated in the ES-treated fish compared with all the other exposure groups and controls. This gene is involved in cholesterol and steroid biosynthesis. It will be important to confirm this downregulation by other methods. We are developing real-time PCR assays to do this.

Although in this study we saw no differences in gene expression between estradiol and MXC, we expect that we would see such differences in a larger array, as it has been noted by others that in mice MXC may stimulate some genes through pathways that do not involve ER[alpha] and ER[beta] (Ghosh et al. 1999; Waters et al. 2001).

Additionally, we investigated the sensitivity of array technology to detect and quantitate differences in gene expression by examining the expression profiles of the 30 arrayed genes in sheepshead minnows exposed to environmentally relevant (24 and 109 ng/L) and high (832 ng/L) doses of E[E.sub.2]. The 24-ng/L dose represents the threshold concentration for Vtg protein induction in sheepshead minnows (Folmar et al. 2000). Our results show that estrogen-responsive genes vary in expression in a dose-dependent manner with increasing concentrations of E[E.sub.2] (Figures 5, 6). These genes include Vtgs 1 and 2, choriogenins 2 and 3, ER[alpha], coagulation factor XI, transferrin, AMBP, and [beta]-actin. These findings demonstrate the potential for use of this assay in screening programs (to establish lowest observable effect concentrations and no observed effect concentrations) and toxicologic mode of action studies for estrogenic chemicals.

In summary, our results indicate that gene arrays have potential as screening assays for new and existing chemicals to determine their potential estrogenic potency. Although the array used in this study was limited in the number of genes queried, our preliminary findings suggest EDCs that mimic estrogen will exhibit unique genetic fingerprints, indicating the usefulness of this technology to identify specific classes of chemicals capable of eliciting estrogenic responses in wild populations of fish.


Akerstrom B, Logdberg L, Berggard T, Osmark P, Lindqvist A. 2000. [alpha] (1)-Microglobulin: a yellow-brown lipocalin. Biochim Biophys Acta 1482:172-184.

Altschul SF, Madden TL, Schaffer AA, Zhang J, Zhang Z, Miller W, et al. 1997. Gapped BLAST and PSI-BLAST: a new generation of protein database search programs. Nucleic Acids Res 25:3389-3402.

Arukwe A, Knudsen FR, Goksoyr A. 1997. Fish zona radiata (eggshell) protein: a sensitive biomarker for environmental estrogens. Environ Health Perspect 105:418-422.

Arukwe A, Kullman SW, Hinton DE. 2001. Differential biomarker gene and protein expressions in nonylphenol and estradiol-17[beta] treated juvenile rainbow trout (Oncorhynchus mykiss). Comp Biochem Physiol C Toxicol Pharmacol 129:1-10.

Bertilsson G, Heidrich J, Svensson K, Asman M, Jendeberg L, Sydow-Backman M, et al. 1998. Identification of a human nuclear receptor defines a new signaling pathway for CYP3A induction. Proc Natl Acad Sci U S A 95:12208-12213.

Bevans HE, Goodbred SL, Miesner JF, Watkins SA, Gross TS, Denslow ND, et al. 1996. Synthetic organic compounds and carp endocrinology and histology in Las Vegas wash and Las Vegas Callville Bays of Lake Mead, Nevada, 1992 and 1995. U.S. Geological Survey, Water-Resources Invest Rep 96-4266, 12 pp.

Bocca C, Gabriel L, Miglietta A. 2001. Cytoskeleton-interacting activity of geiparvarin, diethylstilbestrol and conjugates. Chem Biol Interact 137:285-305.

Bost F, Diarra-Mehrpour M, Martin J. 1998. Inter-[alpha]-trypsin inhibitor proteoglycan family--a group of proteins binding and stabilizing the extracellular matrix. Eur J Biochem 252:339-346.

Bowman CJ, Kroll KJ, Hemmer MJ, Folmar LC, Denslow ND. 2000. Estrogen-induced vitellogenin mRNA and protein in sheepshead minnow (Cyprinodon variegatus). Gen Comp Endocrinol 120:300-313.

Bulger WH, Muccitelli RM, Kupfer D. 1978. Studies on the in vivo estrogenic activities of methoxychlor and its metabolites. Role of hepatic mono-oxygenase in methoxychlor activation. Biochem Pharmacol 27:2417-2423.

Carlsen E, Giwercman A, Skakkebaek NE. 1993. Declining sperm counts and increasing incidence of testicular cancer and other gonadal disorders: is there a connection? Ir Med J 86:85-86.

Celius T, Haugen TB, Grotmol T, Walther BT. 1999. A sensitive zonagenetic assay for rapid in vitro assessment of estrogenic potency of xenobiotics and mycotoxins. Environ Health Perspect 107:63-66.

Celius T, Matthews JB, Giesy JP, Zacharewski TR. 2000. Quantification of rainbow trout (Oncorhynchus mykiss) zona radiata and vitel-logenin mRNA levels using real-time PCR after in vivo treatment with estradiol-17[beta] or [alpha]-zearalenol. J Steroid Biochem Mol Biol 75:109-119,

Celius T, Walther BT. 1998. Differential sensitivity of zonagenesis and vitellogenesis in Atlantic salmon (Salmo salar L.) to DDT pesticides. J Exp Zool 281:346-353.

Chaudoreille MM, Peyrot V, Braguer D, Codaccioni F, Crevat A. 1991. Qualitative study of the interaction mechanism of estrogenic drugs with tubulin. Biochem Pharmacol 41:685-693.

Coldham NG, Dave M, Sivapathasundaram S, McDonnell DP, Connor C, Sauer MJ. 1997. Evaluation of a recombinant yeast cell estrogen screening assay. Environ Health Perspect 105:734-742.

Coller HA, Grandori C, Tamayo P, Colbert T, Lander ES, Eisenman RN, et al. 2000. Expression analysis with oligonucleotide microarrays reveals that MYC regulates genes involved in growth, cell cycle, signaling, and adhesion. Proc Natl Acad Sci U S A 97:3260-3265.

Copeland PA, Sumpter JP, Walker JP, Croft M. 1986. Vitellogenin levels in male and female rainbow trout (Salmo gairdneri Richardson) at various stages of the reproductive cycle. Comp Biochem Physiol 83:487-493.

Denslow ND, Bowman CJ, Ferguson RJ, Lee HS, Hemmer MJ, Folmar LC. 2001a. Induction of gene expression in sheepshead minnows (Cyprinodon variegatus) treated with 17[beta]-estradiol, diethylstilbestrol, or ethinylestradiol: the use of mRNA fingerprints as an indicator of gene regulation. Gen Comp Endocrinol 121:250-260.

Denslow ND, Chow MM, Folmar LC, Monomelli S, Heppell SA, Sullivan CV. 1996. Development of antibodies to teleost vitellogenins: potential biomarkers for environmental estrogens. In: Environmental Toxicology and Risk Assessment (Bengston DA, Henshel DS, eds). Vol ASTM STP 1306 5. Philadelphia:American Society for Testing and Materials, 23-36.

Denslow ND, Lee HS, Bowman CJ, Hemmer M J, Folmar LC. 2001b. Multiple responses in gene expression in fish treated with estrogen. Comp Biochem Physiol B Biochem Mol Biol 129:277-282.

Flouriot G, Pakdel F, Ducouret B, Ledrean Y, Valotaire Y. 1997. Differential regulation of two genes implicated in fish reproduction: vitellogenin and estrogen receptor genes. Mol Reprod Dev 48:317-323.

Flouriot G, Pakdel F, Ducouret B, Valotaire Y. 1995. Influence of xenobiotics on rainbow trout liver estrogen receptor and vitellogenin gene expression. J Mol Endocrinol 15:143-151.

Flouriot G, Pakdel F, Valotaire Y. 1996. Transcriptional and post-transcriptional regulation of rainbow trout estrogen receptor and vitellogenin gene expression. Mol Cell Endocrinol 124:173-183.

Folmar LC, Denslow NO, Rao V, Chow M, Crain A, Enblom J, et al. 1996. Vitellogenin induction and reduced serum testosterone concentrations in feral male carp (Cyprinus carpio) captured near a major metropolitan sewage treatment plant. Environ Health Perspect 104:1096-1101.

Folmar LC, Hemmer M, Hemmer R, Bowman C, Kroll K, Denslow ND. 2000. Comparative estrogenicity of estradiol, ethinyl estradiol and diethylstilbestrol in an in vivo, male sheepshead minnow (Cyprinodon variegatus), vitellogenin bioassay. Aquat Toxicol 49:77-88.

Funkenstein B, Bowman C, Denslow ND, Cardinali M, Carnevali O. 2000. Contrasting effects of estrogen on transthyretin and vitellogenin expression in males of the marine fish, Sparus aurata. Mol Cell Endocrinol 167:33-41.

Ghosh D, Taylor JA, Green JA, Lubahn DB. 1999. Methoxychlor stimulates estrogen-responsive messenger ribonucleic acids in mouse uterus through a non-estrogen receptor (non-ER) [alpha] and non-ER[beta] mechanism. Endocrinology 140:3526-3533.

Giusti RM, Iwamoto K, Hatch EE. 1995. Diethylstilbestrol revisited: a review of the long-term health effects. Ann Intern Med 122:778-788.

Giwercman A, Carlsen E, Keiding N, Skakkebaek NE. 1993. Evidence for increasing incidence of abnormalities of the human testis: a review. Environ Health Perspect 101:65-71.

Hansen DJ, Gripe GM. 1991. Interlaboratory comparison of the early life-stage toxicity test using sheepshead minnows (Cyprinodon variegatus). In: Aquatic Toxicology and Risk Assessment (Mayes MA, Barron MG, eds). Vol 14. Philadelphia:American Society for Testing and Materials, 354-375.

Hemmer M J, Hemmer BL, Bowman C J, Kroll KJ, Folmar LC, Marcovich D, et al. 2001. Effects of p-nonylphenol, methoxychlor, and endosulfan on vitellogenin induction and expression in sheepshead minnow (Cyprinodon variegatus). Environ Toxicol Chem 20:336-343.

Heppell SA, Denslow ND, Folmar LC, Sullivan CV. 1996. Universal assay of vitellogenin as a biomarker for environmental estrogens. Environ Health Perspect 103:9-15.

Herbst AL, Ulfelder H, Poskanzer DC. 1971. Adenocarcinoma of the vagina. Association of the maternal stilbestrol therapy with tumor appearance in young women. N Engl J Med 284:878-881.

Jobling S, Reynolds T, White R, Parker MC, Sumpter JP. 1995. A variety of environmentally persistent chemicals, including some phthalate plasticizers, are weakly estrogenic. Environ Health Perspect 103:582-587.

Kliewer A, Moore JT, Wade L, Staudinger JL, Watson MA, Jones SA, et al. 1998. An orphan nuclear receptor activated by pregnanes defines a novel steroid signaling pathway. Cell 92:73-82.

Larkin P, Folmar LC, Hemmer MJ, Poston AJ, Lee HS, Denslow ND. 2002. Array technology as a tool to monitor exposure of fish to xenoestrogens. Marine Environ Res 54:395-399.

Larkin P, Sabo-Attwood T, Kelso J, Denslow ND. In press. Gene expression analysis of largemouth bass exposed to estradiol, nonylphenol, and p,p'-DDE. Comp Biochem Physiol.

Lattier DL, Gordon DA, Burks DJ, Toth CP. 2001. Vitellogenin gene transcription: a relative quantitative exposure indicator of environmental estrogens. Environ Toxicol Chem 20:1979-1985.

Le Guellec K, Lawless K, Valotaire Y, Kress M, Tenniswood M. 1988. Vitellogenin gene expression in male rainbow trout (Salmo gairdneri). Gen Comp Endocrinol71:359-371.

Lee DC, McKnight GS, Palmiter RD. 1978. The action of estrogen and progesterone on the expression of the transferrin gene. A comparison of the response in chick liver and oviduct. J Biol Chem 253:3494-3503.

Lehmann JM, McKee DD, Watson MA, Willson TM, Moore JT, Kliewer SA. 1998. The human orphan nuclear receptor PXR is activated by compounds that regulate CYP3A4 gene expression and cause drug interactions. J Clin Invest 102:1016-1023.

Lim EH, Ding JL, Lam TJ. 1991. Estradiol-induced vitellogenin gene expression in a teleost fish, Oreochromis aureus. Gen Comp Endocrinol 82:206-214.

Masuyama H, Hiramatsu Y, Kunitomi M, Kudo T, MacDonald PN. 2000. Endocrine disrupting chemicals, phthalic acid and nonylphenol, activate pregnane X receptor-mediated transcription. Mol Endocrinol 14:421-428.

McKnight GS, Lee DC, Hemmaplardh D, Finch CA, Palmiter RD. 1980. Transferrin gene expression. Effects of nutritional iron deficiency. J Biol Chem 255:144-147.

Mommsen TP, Walsh PJ. 1988. Vitellogenesis and oocyte assembly. In: Fish Physiology (Hoar WS, Randall DJ, eds). New York:Academic Press, 347-406.

Murata K, Sugiyama H, Yasumasu S, Iuchi I, Yasumasu I, Yamagami K. 1997. Cloning of cDNA and estrogen-induced hepatic gene expression for choriogenin H, a precursor protein of the fish egg envelope (chorion). Proc Natl Acad Sci U S A 94:2050-2055.

Naylor CC, Mieure JP, Adams W J, Weeks JA, Castaldi FJ, Ogle LD, et al. 1992. Alkylphenol ethoxylates in the environment. J Am 0il Chem Soc 69:695-703.

Nimrod AC, Benson WH. 1996a. Environmental effects of alkylphenol ethoxylates. Grit Rev Toxicol 26:335-364.

--. 1996b. Estrogenic responses to xenobiotics in channel catfish (Ictalurus punctatus). Marine Environ Res 42:155-160.

--. 1997. Xenobiotic interaction with and alteration of channel catfish estrogen receptor. Toxicol Appl Pharmacol 147:381-390.

Oppen-Berntsen DO, Hyllner SJ, Haux G, Helvik JV, Walther BT. 1992. Eggshell zona radiata-proteins from cod (Gadus morhua): extra-ovarian origin and induction by estradiol-17[beta]. Int J Dev Biol 36:247-254.

Orlando EF, Denslow ND, Folmar LC, Guillette LJ. 1999. A comparison of the reproductive physiology of largemouth bass, Micropterus salmoides, collected from the Escambia and Blackwater Rivers in Florida. Environ Health Perspect 107:199-204.

Pascussi JM, Jounaidi Y, Drocourt L, Domergue J, Balabaud G, Maurel P, et al. 1999. Evidence for the presence of a functional pregnane X receptor response element in the CYP3A7 promoter gene. Biochem Biophys Res Commun 260:377-381.

Petit F, Le Goff P, Cravedi JP, Valotaire Y, Pakdel F. 1997. Two complementary bioassays for screening the estrogenic potency of xenobiotics: recombinant yeast for trout estrogen receptor and trout hepatocyte cultures. J Mol Endocrinol 19:321-335.

Richmond CS, Glasner, JD, Mau R, Jin H, Blattner FR. 1999. Genome-wide expression profiling in Escherichia coli K-12. Nucleic Acids Res 27:3821-3835.

Sakakibara Y, Saito I, Ichinoseki K, Oda T, Kaneko M, Saito H, et al. 1991. Effects of diethylstilbestrol and its methyl ethers on aneuploidy induction and microtubule distribution in Chinese hamster V79 cells. Mutat Res 263:269-276.

Schlenk D, Stresser DM, Rimoldi J, Arcand L, McCants J, Nimrod AC, et al. 1998. Biotransformation and estrogenic activity of methoxychlor and its metabolites in channel catfish (Ictalurus punctatus). Mar Environ Res 46:159-162.

Sharpe RM, Skakkebaek NE. 1993. Are oestrogens involved in falling sperm counts and disorders of the male reproductive tract? Lancet 341:1392-1395.

Shelby MD, Newbold RR, Tully DB, Chae K, Davis VL. 1996. Assessing environmental chemicals for estrogenicity using a combination of in vitro and in vivo assays. Environ Health Perspect 104:1296-1300.

Solomon GM, Schettler T. 2000. Environment and health. 6: Endocrine disruption and potential human health implications. CMAJ 163:1471-1476.

Soto AM, Sonnenschein C, Chung KL, Fernandez MF, 0lea N, Serrano FO. 1995. The E-SCREEN assay as a tool to identify estrogens: an update on estrogenic environmental pollutants. Environ Health Perspect 103:113-122.

Specker JL, Sullivan CV. 1994. Vitellogenesis in fishes; status and perspectives. In: Perspectives in Comparative Endocrinology (Davey KG, Peter RE, Tobe SS, eds). Ottawa:National Research Council of Canada, 304-315.

Sumpter J. 1998. Xenoendocrine disrupters--environmental impacts. Toxicol Lett 102-103:337-342.

Sumpter JP, Jobling S. 1995. Vitellogenesis as a biomarker of estrogenic contamination of the aquatic environment. Environ Health Perspect 103:173-178.

Toppari J. 1996. Is semen quality declining? Andrologia 28:307-308.

Toppari J, Larsen JC, Christiansen P, Giwercman A, Grandjean P, Guillette LJ, et al. 1996. Male reproductive health and environmental xenoestrogens. Environ Health Perspect 105:163-163.

Tyler CR, Sumpter JP. 1998. Oocyte growth and development in teleosts. Rev Fish Biol Fisher 6:287-318.

Vonier PM, Crain DA, McLachlan JA, Guillette LJ, Arnold SF. 1996. Interaction of environmental chemicals with the estrogen and progesterone receptors from the oviduct of the American alligator. Environ Health Perspect 12:1318-1322.

Wang W, Yang L, Suwa T, Casson PR, Hornsby PJ. 2001. Differentially expressed genes in zona reticularis cells of the human adrenal cortex. Mol Cell Endocrinol 173:127-134.

Waters KM, Safe S, Gaido KW. 2001. Differential gene expression in response to methoxychlor and estradiol through ER[alpha], ER[beta], and AR in reproductive tissues of female mice. Toxicol Sci 63:47-56.

This article was previously published in the inaugural Toxicogenomics Section of EHP.

Address correspondence to P. Larkin, EcoArray LLC, Sid Martin Biotechnology Development Institute, Department Unit 12085, Research Dr., Alachua, FL 32615 USA. Telephone: (386) 418-1400. Fax: (386) 462-0875. E-mail:

This study was funded by U.S. Environmental Protection Agency (U.S. EPA) contract OD-5378-NTGX, U.S. EPA cooperative agreement CR826357-10, and the Interdisciplinary Center for Biotechnology Research, University of Florida.

The contents of this article are solely the responsibility of the authors and do not necessarily represent the official views of the U.S. EPA. N. Denslow and P. Larkin are inventors of the technology discussed in this publication and hold equity in EcoArray LLC, a company commercializing the technology. They may benefit from this technology by receiving royalties and equity growth.

Received 2 May 2002; accepted 25 October 2002.

Patrick Larkin, (1,3) Leroy C. Folmar, (2) Michael J. Hemmer, (2) Arianna J. Poston, (1) and Nancy D. Denslow (1)

(1) Department of Biochemistry and Molecular Biology and Center for Biotechnology, University of Florida, Gainesville, Florida, USA;

(2) National Health and Environmental Effects Research Laboratory, Gulf Ecological Division, U.S. Environmental Protection Agency, Gulf Breeze, Florida, USA; (3) EcoArray LLC, Alachua, Florida, USA
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Author:Denslow, Nancy D.
Publication:Environmental Health Perspectives
Date:May 15, 2003
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