Go to: Background

Objectives

Methods and results

Conclusions Environ Health Perspect. 2008 Feb; 116(2): 165–172. Published online 2007 Oct 26. doi: 10.1289/ehp.10131 PMCID: PMC2235215

Research 

### Arsenic as an Endocrine Disruptor: Arse nic Disrupts Retinoic Acid Receptor–and Thyroid Hormone Receptor–Mediated Gene Regulation and Thyroid Hormone –Mediated Amphibian Tail Metamorphosis Jennifer C. Davey , Athena P. Nomikos , Manida Wungjiranirun , Jenna R. Sherman , Liam Ingram , Cavus Batki , Jean P. Lariviere , and Joshua W. Hamilton Department of Pharmacology & Toxicology, and Center for Environmental Health Sciences, Dartmouth Medical School, Hanover, New H ampshire, USA Address correspondence to J.W. Hamilton, Department of Pharmacology & Toxicology, 7650 Remsen Building, Room 514, Dartmouth Med ical School, Hanover NH 03755-3835 USA. Telephone: (603) 650-1316. Fax: (603) 650-1129. E-mail: u d e

. h t u o m t r a d @ n o t l i m a h

. h s o j The authors declare they have no competing financial interests. Received 2007 Feb 1; Accepted 2007 Oct 25. Copyright notice Publication of EHP lies in the public domain and is therefore wit hout copyright. All text from EHP may be reprinted freely. Use of materials published in EHP should be acknowledged (for example, ?Reproduced with permission from Environmental Health Perspectives?); pertinent refere nce information should be provided for the article from which the material was reproduced. Articles from EHP, especially the News section, may contain photographs or illustrations copyrighted by other commercial organizations or individuals that may not be used without obtaining prior approva l from the holder of the copyright.

This article has been cited byother articles in PMC.

Abstract Chronic exposure to excess arsenic in drinking water has been stro ngly associated with increased risks of multiple cancers, diabetes, h eart disease, and reproductive and de velopmental problems in humans. We previously demonstrated that As, a potent endocrine disruptor at low, environmentally relevant levels, alters steroid signaling at the level of receptor-mediated gene regulation for all five st eroid receptors. The goal of this study was to determine whether As can also disrupt gene regulation via the retinoic acid (RA) receptor (RAR) and/or the thyr oid hormone (TH) receptor (TR) and whether these effects are similar to previously observed effects on steroid regulation. Human embryonic NT2 or rat pituitary GH3 cells were treated with 0.01–5 μM sodium arsenite for 24 hr, with or without RA or TH, respectively, to examine effects of As on receptor-mediated gene transcription. At low, noncytotoxic doses, As signif icantly altered RAR-dependent gene transcription of a transfected RAR response element–luciferase cons truct and the native RA-inducible cytochrome P450 CYP26A gene in NT2 cells. Likewise, low-dose As significantly altered expression of a tran sfected TR response element –luciferase construct and the endogenou s TR-regulated type I deiodinase ( DIO1 ) gene in a similar manner in GH3 cells. An amphibian ex vivo tail metamorphosis assay was used to examine whether endocrine disruption by low-dose As could have specific pathophysiologic consequenc es, because tail metamorphosis is tightly controlled by TH through TR. TH-dependent tail shrinkage was inhibited in a dose-dependent manner by 0.1– 4.0 μM As. As had similar effects on RAR- and TR-mediated ge ne regulation as those previously observed for the steroid receptors, suggesting a common mechanism or action. Arse nic also profoundly affected a TR

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9 /25 /201 5 http://www.ncbi.nlm.ni h.gov/pmc/articles/PMC2235215 /dependent developmental process in a model animal system at very low concentrations. Because RAR and TH are critical for both normal human development and adult func tion and their dysregulation is associated with many disease processes, disruption of these hormone receptor–dependent processes by As is also potentially relevant to human developmental problems and disease risk. Keywords: arsenic (As), CYP26A , deiodinase ( DIO1 ), endocrine, retinoic acid (RA), steroid, thyroid (TH)

Exposure to excess arsenic, principally from contaminated drinking water, is considered one of the top environmental healththreats both in the United States and worldwide [ Abernathy et al. 2003 ; Mukherjee et al. 2006 ; National Research Council (NRC) 1999 , 2001 ; Smith et al. 2002 ; Watanabe et al. 2003 ]. The majority of this exposure is from natural geological sources of As that contaminate groundwater. Epidemiologic studies have linked chronic exposure to drinking-wat er As with increased risks of various cancers, including those of the lung, bladder, skin, and liver, as well as numerous other n oncancer illnesses including vascular and cardiovascular disease, diabetes, developmental and reproductive problems, and neurologic and cognitive problems ( Abernathy et al. 2003 ; NRC 1999 , 2001 ; Smith et al. 2002 ; Tapio and Grosche 2006 ; Wasserman et al. 2004 ; Watanabe et al. 2003 ). Public water supplies in the United States and Europecurrently have a regulatory limit of 10 ppb As (0.13 μM). However, a large segment of the population in the Un ited States and worldwide obtains its drinking water from private unregulated wells. Also , many other areas of the world have higher regulatory limits or water supplies that are unregulate d. Thus, As contamination continues to be a serious, ongoing public environmental health problem affecting hundreds of millions of people. There are a number of proposed mechanis ms for the ability of As to influenc e so many diverse disease processes. These include alterati ons in cell signaling, cell cycle control, oxidative stress, DNA repair, and others ( Abernathy et al. 1999 ; Aposhian and Aposhian 2006 ; Kitchin 2001 ; Rossman 2003 ). Moreover, it is becoming clear that there are important dose-, time-, and tissue-specific differences in effects of As, as well as important gene –environment and co-exposure interactions that complicate how As alters disease risk under any particular exposure circumstance ( Andrew et al. 2003 , 2006 ; Bodwell et al. 2004 , 2006 ; Karagas et al. 2004 ; Waalkes et al. 2003 ). We previously reported that As is a potent endo crine disruptor, altering steroid hormone receptor (SR) -mediated gene regulation at very low, environmentally relevant concentrations in cell culture and in wholeanimal models ( Bodwell et al. 2004 , 2006 ; Davey et al. 2007 ; Kaltreider et al. 2001 ). We have demonstrated that all five steroid receptors (SRs) [i.e., the receptors fo r glucocorticoid (GR), androgen (AR), progesterone (PR), mineralocorticoid (MR), and estrogen (E R) hormones] are affected in a similar manner, suggesting a broad effect on these pathways and also suggesting a common mechanism for these effects ( Bodwell et al. 2004 , 2006 ; Davey et al. 2007 ; Kaltreider et al. 2001 ). Given this strong disruption on this entire class of nuclear hormone receptors, we were interested in whether thes e effects extend to other members of the larger nuclear hormone receptor superfamily. In this study we examined the effects of As on gene regulation by two related class II receptors, the retinoic acid (RA) receptor (RAR) and the thyroid hormone (TH) receptor (TR). Both re ceptors normally partner with the retinoid X receptor (RXR) to form heterodimers that act as transcription factors, binding to the RA-response element (RARE) of RA-inducible genes or the TH-responsi ve element (TRE) of TH-inducible genes, respectively ( Mark et al. 2006 ; Tsai and O’Malley 1994 ; Wong and Shi 1995 ; Zhang and Lazar 2000 ). We report here that As has significant effects on both RAR- and TR-mediated gene regulation at very low doses (0.01–2 μM), and that these effects are striki ngly similar to those previously observed with the SRs, suggesting a common mechanism. We also investigated whether such As-induced alteration s in hormone signaling would lead to pathophysiologic consequences, using amphibian tail metamorphosis as a model system. Anuran metamorphosis is highly dependent on TH- and TR-mediated processes ( Buchholz et al. 2006 ; Buckbinder and Brown 1993 ; Wong and Shi 1995 ; Yaoita and Brown 1990 ) and is known to be perturbed by agents that interfere with TH or TR signaling ( Buchholz et al. 2003 ; Lim et al. 2002 ). Because TH is also important fo r many aspects of mammalian embryonic development ( Galton 2005 ; Oppenheimer and Samuels 1983 ; Porterfield and Hendrich 1993 ), this is a useful 

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9 /25 /201 5 http://www.ncbi.nlm.ni h.gov/pmc/articles/PMC2235215 /Go to:
NT2 cell culture and transfections

Clonogenic cell survival assay for NT2 cells

GH3 cell culture and transfections

Clonogenic cell survival assay for GH3 cells model for understanding possible effects on human development. Arsenic had profound effects on TH-mediated ex vivo tail metamorphosis at very low, environmentally relevant concentrations, suggesting that there are likely to be other developmental and pathophysiologic effects of low dose As endocrine disruption in vivo

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Methods NT2 [NTERA-2; American Type Cultur e Collection (ATCC), Manassas, VA] human embryonic carcinoma cells were maintained in Dulbecco ’s Modification of Eagle’s Medium (DMEM; Invitrogen, Carlsbad, CA) plus 10% fetal bovine serum (FBS; Atlanta Biologicals, Norcross, GA). Cells were split into 6-well plates at 1.5 × 10 cells/well and grown in phenol red–free DMEM plus 10% charcoal-stripped FBS overnight for transfection experiments. The constr uct used was generously provided by James DiRenzo (Dartmouth Medical School). Briefly, the construc t contains two canonical tandem RARE sequences (5 ′ -AGGTCA-(N) -AGGTCA-3 ′ ) upstream of a thymidine kinase promoter and the firefly luciferase coding region with a pBR322 backbone (RARE-LUC) ( Kurokawa et al. 1994 ). Cells were transfected with 250 ng of the RARE-LUC construct using Fugene (Invitrogen) accord ing to the manufacturer’s recommended protocol. Alltrans-retinoic acid (ATRA; Sigma Chemical Co., St. Louis, MO), reconstituted in DMSO and stored at –20°C, was used as ligand at concentrations indicated. Arsenic (As, As , sodiumarsenite, NaAsO ; Sigma Chemical Co.) was dissolved in water and kept frozen until th e day of use. Treatments were performed 24 hr after transfection. ATRA and As were added simultaneously at the doses and for the durations described in “Results.” NT2 cells were grown in phenol red–free DMEM media plus 10% FBS and split into 6-well plates with approximately 100 cells/well and allowed to grow overnight. Cells were then exposed to 1.0–7.0 μM As plus 10 nM ATRA for 24 hr. Next, fresh media without As but including 10 nM ATRA was added, and cell growth wa s checked daily. When colonies of ≥25 cells were formed in control wells, the media was removed and the cells were fixed in 1% form aldehyde for 1 hr and then exposed to 100% methanol for 5 min. Methanol was removed and cells were stained with 0.3% Giemsa stain (in 70% methanol) for 15 min. Colonies were rinsed twice with phosphate-buffered saline(PBS) and counted. Results are given as a percent of control, and each condition wa s repeated in triplicate. GH3 rat pituitary tumor cells (ATCC) were cultured in F-12 Nutrient Mixture (Ham) (Invitrogen) supplemented with 15% horse serum (Atlanta Biologicals) and 2.5% FBS. For triiodothyronine (T )/As treatments, 6-well plates were seed ed at 350,000–750,000 cells/well and cultured in F-12 medium for 3 days. Cells were then put into phenol red–free DMEM supplemented with 10% char coal-stripped FBS for 18 hr prior to treatments. The TR response elem ent–luciferase (TRE-luc) cons truct used for transfections was created by exchanging the glucocorticoid response element (GRE) sequen ce with two canonical TRE direct repeats in the pXP2-GRE–luciferase construct kindly c ontributed by J. Bodwell (Dartmouth Medical School). The final construct was sequenced to verify successful insertion. Tr ansfections were performed with Lipofectamine Plus (Invitrogen) with the following opti mizations. Twenty-four hours after plating, media was changed to unsupplemented Opti-MEM (Invitrogen), th en transfection fo llowed using the manufacturer’s protocol. Three hours later, Opti-MEM was replaced wi th phenol red–free DMEM plus 10% charcoal-stripped FBS for the duration of the experiment. Cells were treated with As as indicated. T (CAS 55-06-1; Sigma) was reconstituted to 1 mM in 45% propylene glycol (1,2-propanediol; Aldrich, St. Louis, MO), 45% water, and 10% 0.1 N sodium hydroxide and stored at 4°C covered. Clonogenic assays were performed by plating approximately 5,000 cells/well in a 6-well plate an d allowing them to grow in F-12 Nutrient Mixture for a total of 3–4 days. After an 18-hr treatment in phenol red–free DMEMwith 10% charcoal-stripped serum, cells were treated for 24 hr with various doses of As, with or without T . Arsenic was removed and the cells were allowed to grow for approximately 5 days in phenol red–free DMEM plus 10% charcoal-stripped serum wi th or without T . Cells were trypsinized, resuspended in PBS, and counted in azi de-free isotonic diluent (V altech Diagno stics, Inc., Brackenridge, PA) using a Coulter Counter Z1 (Beckman Coulter, Fullerton, CA). Cells were counted 5

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9 /25 /201 5 http://www.ncbi.nlm.ni h.gov/pmc/articles/PMC2235215 /ICP-MS analysis of total arsenic in cell culture media

Luciferase and protein assays

Semiquantitative real-time polymerase chai n reaction (PCR) for CYP26A or DIO1

Xenopustadpole culture individually rather than via colony formation (as with the NT2 cells) because GH3 cells would not adhere under the conditions necessary for staining the colonies.
Total arsenic levels in cell culture media were measured by the Dartmouth Superfund Trace Metal Core Facility using collision cell inductively coupled plasma mass spectroscopy (ICP-MS; Agilent octopole/reacti on cell 7500c ICP-MS; Agilent, Pa lo Alto, CA), employing helium as the collision gas. The media was diluted and analyzed by the method of standard additions. Method detection limits were 0.005 μM, and the overall method uncertainty was 8%. Al l media used contained undetectable levels of As or levels well below any of the exogenously added effective doses (i.e., < 0.01 μM). Cells were rinsed twice with cold PBS, covered with 150 μ l of Promega lysis buffer, and scraped from the plate. Celllysates were frozen at –80°C, thawed, vortexed for 30 sec, and spun at 12,000 x g for 5 min; supernatants were then transferred to a new tube and stored at –80°C. Each experimental condition in each experiment was done in replicates of six. Transfection e fficiency was consis tent, with little variability among the biological rep eats in each treatment group and low st andard deviations between 3 to 4 replicate experiments. We used Prism software (GraphP ad Software Inc., San Dieg o, CA) for all statistical analyses. Luciferase assays were performed with the Pr omega Luciferase Assay System kit (Promega, Madison, WI) following the manufacturer’s recommended protocol. We used a luminometer (Dynatech Laboratories, Chantilly, VA) to determine the light units per sample . Protein assays were performed with the Pierce BCA Protein Assay Reagent Kit (Pierce, Rockford, IL) follow ing manufacturer’s recommended protocol to normalize the total level of protein in samples. Results of protei n assays were determined using a Thermomax microplate reader (Molecular Devi ces, Sunnyvale, CA).
We isolated total RNA from the cells after indicated treatment times using the Qiashredder and RNeas y Mini Kits (Qiagen, Valencia, CA) or Trizol (Invitrogen) according to the manufacturer’s recommended protocols. Co ntaminating genomic DNA was removed using DNA-free kits (Ambion, Austin, TX), an d total RNA was quantified with a NanoDrop ND-1000 Spectrophotometer (NanoDrop Technologies, Rockland, DE). RNA (1–2 μ g) was reverse-transcribed (genespecific primer) with Omniscript Reve rse Transcriptase (Qiagen), and primer s were synthesizedto specifically amplify either the rat type I deiodinase ( DIO1 ) gene from the GH3 cells (GenBank accession no. BC083557 ; National Library of Medicine 2007 ) or the human cytochrome P450 26A ( CYP26A ) gene from the NT2 cells (GenBank accession no. NM000783) [see Supplemental Material ( http://www.ehponline.org/m embers/2007/10131/suppl.pdf ) for details]. We performed semiquantitative real-time PCR (RT-PCR) to assess relative quantities of each transcript with the 7500 Real-Time PCR System (Applied Biosystems, Foster City, CA). Negative controls, including samples that would either detect contaminating genomic DNA in the RNA samples or contamination of P CR reagents, were always included. On each plate we included an internal standard curve for each transcript, which consisted of a serial dilution of cDNA known to contain the transcript in question. Th e curve generated from the plate was then used to quantify the level of transcript for all the experimental samples on the same plate. RT-PCR for 18S levels was performed to normalize total RNA levels. Results were unaltered by 18S normalization. We purchased Xenopus laevistadpoles from Nasco (Fort Atkinson, WI). Animals were treated humanely and with regard to alleviation of su ffering; all studies were pe rformed in compliance with institutional animal care and use guidelines approve d by Dartmouth Medical School (Protocol 04-03-11). Animals were acclimated to COMB O culture media (8.7 mg/L K HPO 36.9 mg/L MgSO , 62.8 mg/L NaNO , 36.7 mg/L CaCl , 28.42 mg/L Na SiO , 24 mg/L H BO , 12.6 mg/L NaHCO plus 2.18 μ g/L H SeO , 16 μ g/L NaBr, 155 μ g/L LiCl, 70 μ g/L RbCl, 3.3 μ g/L KI, 150 μ g/L SrCl · 6H O, pH 7.7) and carefully stagedwhen they arrived. Animals were kept in COMBO media in 5-gal Na lgene buckets (Nalge Nunc International, Rochester, NY) at room temperature unti l they reached stage 58 of development. Stage 58 was determined using staging criteria determined by Nieuwkoop and Faber (1994) . At stage 58, Xenopus tadpoles have functional TR in tail 2 4, 4 3
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Go to: Effects of As on RAR-mediated transcription tissue, and the tail will metamorphose upon exposure to T whether or not it is attached to the animal ( Shi et al. 2002 ; Tata 1966 ). Tails were excised from stage 58 tadpoles, dipped in 70% ethanol, and immediately placed in a 6-well plate with 3.0 mL phenol red–free minimal e ssential media (MEM; Invitrogen) per well. Arsenic was added to the media immediately (doses indicated in the “Results”), and T was added to the media 18 hr later. Trial experiments in which arsenic and T were added simultaneously resulted in similar shrinkage patterns. Tail cultures were kept in the dark at approximately 2 0–23°C. Medium was changed da ily, and photographs were taken with a digital Nikon Coolpix camera (Nikon Inc., Me lville, NY). Experiments lasted approximately 5 days. Fins of tails treated with T only generally resorbed significantly or completely in 4 days. Digital photographs were analyzed with NIH Image software(National Institutes of Health, Bethesda, MD) to assess the area of tail fin each day. The area of the dorsal tail fin on day 4 was divided by the area of the dorsal tail fin on day 1 to determine the percent of resorption. Each treatment gr oup in each experiment cons isted of 6 tails, and the experiment was repeated fourto eight times. Occasionally tails would not resorb at all when given T alone, indicating that they did not have sufficient TR to metamorphose, most likely as a result of incorrect staging. In these cases, all tails in th e experiment that did not resorb at all when given T were removed from analysis regardless of treatment; 3%–10% of the 42 tails in an experiment were removed and they were evenly distributed between the groups. Statistical significance was determined with Prism software using an unpaired t-test and a p -value < 0.01 for the tail fin area, except when dete rmining the optimal T dose where the value shown is mean ± SE.
Results Ligand-activated RAR forms heterodimers with RXR and binds RAREs in RA-responsive gene promoters, which induces transcription ( Mark et al. 2006 ). Initial dose–response experiments ( Figure 1B ) demonstrated that 10 nM ATRA was an adequate and physiologically relevant dose of ligand that induces a significant increase in expression of the RARE-luc construct when transfected into these cells. Cytotoxicity, measured by colony-forming assays, de monstrated an LC (concentration lethal to 50%) of 3 μM for NT2 cells ( Figure 1A ). Very low concentrations of As (0.05–0.25 μM) enhanced RA-inducible RARE-luc expression comparedwith RA alone ( Figure 2 ). Conversely, a higher but still non-cytotoxic concentration of 2.0 μM As strongly repressed RAR-mediated induction of the construct (as did the higher but slightly cytotoxic dose of 5 μM). The CYP26A gene is endogenously expressed in NT2 cells, and a RARE in its promoter facilitates its induction by ATRA ( Loudig et al. 2000 ). The transcript level of the CYP26A gene was measured by RT-PCR in NT2 cells after exposure to 10 nM ATRA plus As ( Figure 3 ). Similar to the RARE-luc construct, hormone induction of CYP26A mRNA expression was enhanced by 10 nM ATRA plus As at a very low dose (0.01 μM), and its induction was repressed in a dose-dependent manner by As doses of ≥0.025 μM.
Figure 1 Dose–response curves for As, ATRA , and TH in NT2 and GH3 cells calculated using average va lues for each dose. Data points represent the mean ± SE of data from thre e separate experiments. ( A ) Cytotoxicity of As in NT2 cells exposed to As
... Figure 2 Effects of As on ATRA induction of RARE-luc expression in NT2 cells. Cells were transfected with the RARE-l uc construct 24 hr before treatment with 10 nM ATRA with or without simultaneous treatment with As for 24 hr. See “Methods” for
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TH-directed amphibian tail metamorphosis Effects of As on ATRA induction of CYP26A mRNA expression in NT2 cells. Cells were treated with 10 nM ATRA with or without simultaneous addition of As for 24 hr; mRNA expression was measured by RT-PCR. See “Methods” for details. Data are
... GH3 cells are a rat pituitary tumor cell li ne that expresses functional TRs and expresses genes directly induced by TH . We performed a series of initial dose–response experiments to determine an effective and physiologic dose of TH (administered as T ) and found that 1–2 nM T was sufficient to induce transcription ( Figure 1D ) of the DIO1 gene approximately 4-fold. This was also sufficient to induce the TRE-luc construct 4-fold. GH3 cells, like the NT2 cells, were moderately sensitive to the toxic effects of As, with an LC of 5–10 μM, as determined by a clonogenic cell survival assay ( Figure 1C ). Interestingly, the clonogenic assay results indicated an increase in proliferation rather than cytotoxicity when 0.1–1 μM As was combined with T (the proliferative effect was removed when T was removed). The LC was decreased to 0.9–2.0 μM if the cells were grown in stripped serum without T . The TRE-luc construct was repressed in a dose-dependent manner by 0.5–2.0 μM As ( Figure 4 ). We then examined the effects of As on TH induction of the endogenously expressed DIO1 ( Jakobs et al. 1997 ) by measuring mRNA levels by RT-PCR 6 or 24 hr after treatment. At 6 hr, concentrations of 0.01–2.0 μM As produced a biphasic dose response similar to the NT2 results with RA, with a significant super-induction at lower As concentrations (0.01–0.1 μM) and repression at 2 μM ( Figure 5A ). The response at 24 hr differed from the RAR-mediated genes inthat any repressive effects were gone, and 1.0 and 2.0 μM As enhanced hormone-stimulated expression. Arsenic doses > 2 μM produced significant cytotoxicity, so we could not determine whether As suppresses TH induction at 24 hr independent of general toxic mechanisms that might compromise mRNA expression.
Figure 4 Effects of As on T induction of TRE-luc expression in GH3 cells. Cells were transfected with the TRE-luc construct 24 hr before treatment with 2 nM T with or without simultaneous treatment with As for 24 hr. See “Methods” for details.
... Figure 5 Effects of As on T induction of DIO1 mRNA expression in GH3 cells. Cells were treated with 2 nM T with or without As, and DIO1 mRNA expression was measured 6 hr ( A ) or 24 hr (B ) after treatment. See “Methods” for details. Data are expressed
... Based on the effects of As on TR-mediated gene regulation described above, we were interested in whether there were specific path o-physiologic consequences of this endocrine disruption. We assessed T -dependent tail shrinkage by measuring the area of the tail fin over a 4-day period, which is generally the time it takes for the fin to completely resorb in our assay. Fin resorption is the first step in visible tail metamorphosis, is amenable to quantit ation by morphometric analysis , and is representative of the overall tail shrinkage process. A 10-nM dose of T in the tail culture media was consistently sufficient to induce tail fin resorption ( Figure 6 ); thus, we used this dose throughout the subsequent experiments. As shown in Figure 7 , treatment of tails ex vivo with T led to shrinkage of the tail fins that was readily apparent. Control tail fins not exposed to T or As normally shrank 10–20% during an experiment ( Figures 7 and 8 ). Tails exposed to As alone shrank slightly less than controls ( Figure 8 ). In the As plus T groups, the lowest As concentration used (0.05 μM) had little effect compared with T alone, and the tail fins resorbed approximately 58% in both groups ( Figures 7 and 8 ). However, concentrations of As above this (0.5–4 μM) decreased T -dependent tail fin resorption in a dose-dependent manner ( Figure 8 ). A concentration of 0.25 μM As slowed resorption by 4% compared with T alone, whereas 4 μM As decreased resorption by 20%. Interestingl y, the intermediate concentration of 0.1 μM 3 3

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9 /25 /201 5 http://www.ncbi.nlm.ni h.gov/pmc/articles/PMC2235215 /Go to: As did not follow the dose-dependent pattern of the higher As doses; this finding is discussed below. In summary, As significantly altered the T -an d TR-dependent metamorphosis of Xenopustails ex vivo , indicating that As disrupts T hormone signaling through its receptor, TR/RXR, and has the potential to affect hormone-regulated embryonic development at low physiologically and environmentally relevant concentrations in vivo

. Figure 6 Effects of T on tail fin shrinkage of Xenopus tadpole tails cultured ex vivo as described in “Methods.” Data are expressed as mean ± SE of values from six tails per treatment in three separate experiments.
Figure 7 Effects of As on T -mediat ed tail shrinkage in Xenopustadpole tails cultured ex vivo shown by representive samp les from tail resorption experiments. See “Methods” for detail s. Morphometric software was used to trace the tail fin area
... Figure 8 Effects of As on T -mediat ed tail shrinkage in Xenopustadpole tails cultured ex vivo . See “Methods” for details. Data are expressed as mean + SE of values from 5–6 individual tails per experiment and 4–8 individual experiments
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Discussion Based on our previous studies with SRs, we were interested in whether As could also disrupt other, less similar nuclear hormone receptors. Because we were interested in examining the effe cts of As on hormone regulation of both transiently transfected gene constructs as well as native hormone-responsive genes, we chose two different cell culture models, each optimal for the receptor system under study. Our previous results ( Davey et al. 2007 ), as well as those of others ( Kaltreider et al. 2001 ), strongly indicate that working in the appropriate cell line is critical to mimicking the effects of As on gene expression observed in vivo. Mann et al. (2005) reported that As had no effect on ER-mediated gene expression in heterologous systems such as COS1 cells, which do not normally express ER but require co-transfection of an ER-expressing plasmid. Lack of response in such systems, even when the receptor is reexpressed, may indicate that othe r critical aspects of the receptor machinery (e.g., key coregulators that are critical for the As response) may be missing. Also, the sensitivity of cultured cells to the cytotoxic effects of As is highly cell line specific; thus, it is important to know the dose response to As for a given cell line so the appropriate dose range can be selected and the toxic-e quivalent doses between lines can be compared. In the present study we found that NT2 cells are more sensitive to the toxic effects of As than other cell lines we have used. Also, in orde r to examine the pathophysiologic cons equences of endocrine disruption of one of these type II receptors by As, we chose another well-characterized system, amphibian tail metamorphosis, which is known to be highly TR-dependent ( Brown et al. 1996 ; Das et al. 2006 ; Dodd and Dodd 1976 ; Lim et al. 2002 ; Veldhoen and Helbing 2001 ). We observed significant effects of As at very low, noncytotoxic, environmentally relevant concentrations on both RAR- and TR-mediated gene expression in this study. Th ese As effects were very si milar to those previously observed for GR and the other SRs, s uggesting a common mechanis m of action. As with SR s, the effects of As exhibited a complex dose–resp onse pattern that was biphasic, with As significantly enhancing hormone-mediated gene expression at very low doses while strongly suppre ssing gene expression at higher , but still moderate, doses of As. Similar effects were observed for GR, MR, PR, AR, and ER, although the precise concentrations varied as a function of relative As to xicity in each cell system ( Bodwell et al. 2004 , 2006 ; Davey et al. 2007 ). Our previous studies with SRs strong ly suggest that the receptors themselves are not the actual targets for these As effects. 3
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9 /25 /201 5 http://www.ncbi.nlm.ni h.gov/pmc/articles/PMC2235215 /First, the SRs share little absolute homology, yet they respond almost identically to As ( Bodwell et al. 2006 ; Davey et al. 2007 ). Although GR, MR, AR, and PR share extensive similarity, ER is much more distally related and shares little absolute homology, but ER responds similarly to As ( Davey et al. 2007 ). Second, mutational studies with GR indicated that neither the N-terminal regulatory or C-terminal ligand-binding domains were necessary to elicit the effects of As ( Bodwell et al. 2004 , 2006 ). Likewise, extensive mutational analysis of the remaining central DNA-binding domain of GR failed to de monstrate any critical regionthat could serve as the likely target for As, nor is there sufficient homology among the SRs to explain a co mmon As effect. The present results show similar effects of As on TR and RAR in spite of their even greater divergence from the SRs; this further supports the hypothesis that it is some common aspect of their regulation that is the actual target. The mechanism of gene activation for TR and RAR differs from that of the SRs. Unlike the SRs, which form homodimers and bind to palindromic hormone-responsive elements (HREs) in promoters, TR and RAR each normally form obligate heterodimers with the RXR to form a functional transcription factor. The TR-RXRs and RAR-RXRs are also normally bound to their cognate response elements (TRE and RARE, respectively) in hormone-responsive promoters in the absence of ligand , unlike the SRs, which normally reside as quiescent monomers in the cytoplasm (GR, MR , PR, AR) or nucleus (ER) and then migrate to thei r respective HREs following hormone activation and dimerization. Co-represso rs normally prevent transa ctivation of TR or RAR until ligand binding occurs ( Bastien and Rochette-Egly 2004 ; Hermanson et al. 2002 ; McKenna and O’Malley 2002 ; Shi et al. 2002 ). Similar to what was observed for SRs, As produced a biphasic response to gene induction with RAR and TR. The suppressive effect of intermediate doses of As is seen universally and strongly with all of these nuclear hormone receptors under virtually all experimental conditions, and it appears to be most closely tied to transcription. In contrast, the low-dose As enhancement of hormone induction is more variable among receptors, is more susceptible to experimental manipula tion, and appears to be most closely associated with earlier steps of receptor activation, based on detailed studies with GR ( Bodwell et al. 2004 , 2006 ). For example, certain GR mutants lack the low-dose enhancement while retaining intermediate dose suppression by As. Similarly, the low-dose enhancement can be progressively dampened and eventually lost by progressively increasing the number of hormone-activated receptors in the cell, although higher dose suppression by As remains relatively constant ( Bodwell et al. 2004 ). We propose that the mechanism by which As enhances hormone-induced gene activation at very low doses is distinct, and can be separated experimentally, from the suppressive effects seen at the slight ly higher but still noncytotoxic intermediate doses. However, the precise mechanisms by which As elicits these two effects remains to be determined. RAR mediates RA signaling during embryonic development. Either excessive or de ficient levels of RA, a derivative of vitamin A, results in teratogenic effects ( Shenefelt 1972 ; Thompson et al. 1964 ; Wolbach and Howe 1978 ). RA signaling is also involved in tissue homeostasis, lipid metabolism, and cellular differentiation and proliferation in the adult ( Shenefelt 1972 ). The family of retinaldehyde dehydrogenases and Cyp26(A1,B1,C1) are RA-synthesizing and RA-cat abolizing enzymes, respectively. Transgenic mice without CYP26A1 result in embryonic lethal phenotypes, thus indicating a key role of CYP26A1 in embryogenesis ( Abu-Abed et al. 2001 ). The present study indicates that RA-d ependent CYP26A1 mRNA expression can be enhanced or repressed by As exposure, depending on the dose of As. CYP26A1 plays a key role in inactivating RA; therefore, its dysregulation could have important pathophysiogic consequences, including developmental processes, similar to those of the DIO1 gene ( White et al. 1996 , 1997 ). Because these effects were observedfor concentrations of As that are directly relevant to environmental levels of As in drinking water of concern throughout the United States and many other parts of the world, this has potentially important implications for human reproduction and development in exposed populations. TR is the mediator of critical TH-regulated processes in adults and during embryonic and fetal development ( Gothe et al. 1999 ). The active form of TH, T , is produced when type I or type II deiodinase removes a specific outer ring iodine of thyroxine (T ). T is the active TH ligand that binds TR, and therefore its production is a crucial step in TH-driven gene induction. The DIO1 gene has a TRE in its promoter and is directly induced by T through TR. The change in expression of DIO1 we observed at 6 or 24 hr of As exposure indicat es a transient 3
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9 /25 /201 5 http://www.ncbi.nlm.ni h.gov/pmc/articles/PMC2235215 /superinduction by As at very low doses and a transient repression by As at higher doses. Differential effects of acute versus chronic As exposure are of interest because TH levels—kept in equilibrium by deiodinases and T levels in the pituitary—are critical to thyroid function in the whole body. Thus, understanding how As alters T homeostasis will be an important aspectof understanding the overall effects of As on this hormone pathway, both for human development and in adult physiologic processes. The clonogenic assays with the GH3 cells indicated enhanc ement of proliferat ion at low-dose As in the presence of T . T activates growth hormone in GH3 cells, causing proliferation ( Kitagawa et al. 1987 ; Kitamura et al. 2002 ), and low-dose arsenic has also been shown to cause proliferation of cells ( Hwang et al. 2006 ; Vogt and Rossman 2001 ). Low-dose As appears to enhance the proliferative effect of T , demonstrating another type of Asinduced endocrine disruption (i.e., enhancement of proliferation that is hormone dependent). Metamorphosis of Xenopus laevishas been extensively characterized ( Buchholz et al. 2006 ; Buckbinder and Brown 1993 ; Gudernatch 1912 ; Wong and Shi 1995 ; Yaoita and Brown 1990 ). In vivo , the tadpole produces T in concert with induction of TR, leading to TH-dependent alterations in gene expression that regulate tail resorption ( Brown et al. 1996 ; Das et al. 2006 ; Dodd and Dodd 1976 ). This can be mimicked by culturing appropriately staged tadpole tails ex vivo and exposing them to exogenous TH, leading to tail shrinkage similar to that seen in vivo ( Das et al. 2006 ; Lim et al. 2002 ; Tata 1966 ; Veldhoen and Helbing 2001 ). Tadpole tails will respond to T in the culture media essentially as they would as part of the whole animal, by shrinking through what is thought to be a combination of apoptosis and necrosis ( Du Pasquier et al. 2006 ; Nakajima and Yaoita 2003 ). We assessed T -dependent tail shrinkage by measuring the area of the tail fin over a 4-day period, which is generally the time it takes for the fin to completely resorb in our assay. Fin resorption is the first step in visible tail metamorphosis, is amenable to quantitation by morphom etric analysis, and is repres entative of the overall tail shrinkage process. The ex vivo tail culture allows for the very controlled and T -driven metamorphosis of an entire tissue and, because the tadpole skin is so permeable, both T and As are able to diffuse into the tissue from the media ( Lim et al. 2002 ; Veldhoen and Helbing 2001 ). Tail resorption is completely dependent on T acting as a ligand for TR and trans-activating genes necessary for resorption, as shown in previous studies including those using an antagonist to TR, which blocks these processes ( Lim et al. 2002 ). The lowest As concentration that had an effect on tail fin resorption (0.1 μM) did not follow the dose-dependent pattern of all the higher As concentrations. ( Figure 8 ). This biphasic pattern was highly repeatable and statistically signi ficant, indicating two different dose responses over this range and suggesting perhaps two different mechanisms of action underlying these effects. Indeed, two different mech anisms of interference could lead to the same overt results (i.e., less fin shrinkage). Tail resorption is only one piece of the complete transf ormation of the aquatic tadpole into the terrestrial frog ( Das et al. 2006 ; Dodd and Dodd 1976 ). Tissues in the animalare completely remodeled to function on land. In the space of a few weeks, body parts are generated (limbs ) while others completely resorb (tail) ; cell death, growth, and differentiation can occur simultaneously in a single tissue (intestine, eye, blood, skin). All this transformation is directed by TH. If TH is removed, metamorphosis does not happen and a continuously growing tadpole will result ( Allen 1916 ; Dodd and Dodd 1976 ). When TR is expressed and T is produced, the program for the transcription of genes necessary for metamorphosis in any tissue is ready to proceed. This model has relevance to human development because the plasma levels of TH spike in humans during the perinatal period (6 months of gestation through several months postnatal) , which correlates temporally with the TH spike in amphibians during metamorphosis ( Shi et al. 2002 ). Extreme thyroid deficiency in humans at birth leads to cretinism, with characteristi c mental retardation, short stature, and h earing loss. These severe deficiencies are detected at birth and can be quickly treated with exogenous hormone, but subtler effect s may not be as evident at birth ( Galton 2005 ; Oppenheimer and Samuels 1983 ; Raz and Kelley 1997 ). Indeed, subtle effects on cognitive function have been noted in epidemiology studies of children exposed to excess As in drinking water ( Wasserman et al. 2004 ). Studies showing disruption of thyroid hormone functions after As exposure in rodents include an increase in thyroid cancer ( Yamamoto 1995 ), a synergistic effect between As and TH on oxidative stress ( Allen 3
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Go to: and Rana 2003 ), and a disregulation of deiodinase levels in fetal brain with concurrent As exposure and selenium depletion ( Miyazaki et al. 2005 ). In the present study we have demonstrated that As can act as a potent endocrine disrup tor not only for the entire SR family but also for two important members of the larger nuclear hormone receptor superfamily. It seems likely, based on the ubiquity of these effects and their likely common or shared mechan ism(s), that As will also have similar effects on other members of this large horm one receptor superfamily. It will be important to determine the extent to which this occurs and under what conditions, but also to investigate the biological consequences of such effects. In cluding the present study, we have demonstrated in two different in vivo systems that there are specific and predictable pathophysiologic effects of endocrine disruption by As. We previously reported that As has profound effects on the GR-dependent freshwater-to-saltwater transition of killifish ( Fundulus heteroclitus ) ( Shaw et al. 2007 ; Stanton et al. 2006 ). Exposure to excess As in drinking water has been associated with an extensive and growing list of disease risks. Given the important and myriad roles of hormones and their receptors in normal physiology and in the pathophysiology of these and other diseases, it is likely that endocrine disruption by As plays an important role. Previously, it was thought that because As does not si gnificantly accumulate in the body, unlike persistent organics or metals such as mercury and lead, and also does not cause DNA damage or mutations, its effects on disease risk might also be transient and reversible. However, such effects of As on hormone signaling at key developmental or differentiation points might be expected to result in long -term effects related to epi-genetic phenomena such as imprinting. In this regard, it is interest ing to note several recent st udies that support this idea ( Liu et al. 2006a ; Shen et al. 2006 ; Waalkes et al. 2004a ). Among other interesting changes, a profound upregulation of ER expression has been reported in livers of adult mice exposed in utero to As, in addition to their increased incidence of liver tumors ( Chen et al. 2004 ; Liu et al. 2006b ; Waalkes et al. 2004b ). Two recent epidemiology studies of humans exposed to As in drinking water were also provocative ( Smith et al. 2006 ; Wasserman et al. 2004 ). These studies suggest that there can be si gnificant long-term consequences of exposing young or developing individuals to As during critical periods of development. We propose that disruption of hormone signaling is likely to be an important component of these effects. Thus, understanding the role of As as an endocrine disruptor will be important for assessin g the overall impact of As on human health and in developing appropriate risk assessment paradigms that are protective of human health.
Footnotes Supplemental Material is available online at http://www.ehponlin e.org/members/2007 /10131/suppl.pdf We thank J. Bodwell, J. Gosse, and B. Stanton for their useful comments and suggestions. We also acknowledge the assistance of B. Jackson and A. LaCroix-Fralish of the Dartmouth Trace Elements Analysi s (TEA) Core Facility for their assistance in the trace analysis of our samples. This work was supported by grant P42 ES07373 to J.W.H. [Superfund Basic Research Program (SBRP) Project, Project 2; National Institute of Environmental Health Sciences, National Institutes of Health]. A.P.N. was supported by a graduate fellowship (P42 ES07373; SBRP, Training Core). The TEA Core is partially supported by grant P42 ES07373 (SBRP, Core B) and by an instrument grant from the National Science Foundation (MRI-0215913).
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