The in vitro estrogenic activities of polyfluorinated iodine alkanes.
OBJECTIVFS: High production volumes and potential environmental releases of PFIs might become a concern, but the exposure risk and toxicity of these chemicals are still unclear. In this study, we investigated the potential estrogenic effects of PFIs.
METHODS: We studied the estrogenic effects of fluorinated iodine alkanes (FIAs), fluorinated telomer iodides (FTIs), and fluorinated diiodine alkanes (FDIAs) using the E-screen and MVLN assays and the evaluation of estrogen-responsive genes in MCF-7 cells.
RESULTS: FIAs have an iodine atom at one end of the perfluorinated carbon chain. 1-Iodoperfluoro-hexane (PFHxI) and 1-iodoperfluorooctane (PFOI) promoted the proliferation of MCF-7 cells, induced luciferase activity in MVLN cells, and up-regulated the expression of TFF1 and EGR3. In these assays, other FIAs gave negative responses. FDIAs have an iodine atom at each end of the perfluorinated carbon chain, and all the FDIAs showed estrogenic effects. The estrogenic potencies of FIAs and FDIAs correlate well with the carbon chain length of the chemicals. The optimum chain length for estrogenic effects is six carbons, and then eight and four carbons. All FTIs have a single iodine atom at the end of a partially fluorinated carbon chain. None of the FTIs showed estrogenic effects in the tests.
CONCLUSIONS: The estrogenic effects of PFIs are dependent on the structural features of iodine substitution and chain length. This research will be helpful in further understanding the estrogenic effects of perfluorinated compounds.
KEY WORDS: endocrine disruptor, estrogenic effects, in vitro assay, perfluorinated chemicals, polyfluorinated iodine alkanes. Environ Health Perspect 120:119-125 (2012). http://dx.doi. org/10.1289/ehp.1103773 [Online 11 October 2011]
Perfluorinated chemicals (PFCs) have a broad range of applications in the manufacture of various industrial and commercial products, such as fluoropolymers, surfactants, emulsifiers, and nonstick coatings. PFCs have been of considerable scientific and public concern because some of them are environmentally persistent, bioaccumulative, and widely detected in humans, wildlife, and the environment (Giesy and Kannan 2001; Olsen et al. 2007).
Because of environmental concerns, the 3M company voluntarily phased out electrochemical fluorination-based Huorochemicals in 2001 (Duponc 2005). Consequently, the current production of fluorinated polymers and surfactant is mostly based on telomerization processes (Lehmler 2005). Polyfluorinated iodine alkanes (PFIs) are organic iodides composed of a fluorinated carbon backbone terminated by iodine substitution (Table 1) and are important intermediates in the synthesis of various fluorinated chemicals (Brace 1999; Prevedouros et al. 2006). In the telomerization process, PFIs are used to synthesize fluorotelomer alcohols (FTOHs) and other related PFCs. In turn, FTOHs are intermediates in the production of surfactants and fluoropolymers, and these volatile compounds have been detected in the atmosphere around the world (Ellis et al. 2004). The annual production of FTOHs increased to 11-13 x 103 metric tons in 2002 (Ellis et al. 2003). The annual world production of PFIs has been estimated to exceed 4,000 metric tons (Organisation for Economic Co-operation and Development 2004), and the increasing demand of fluorotelomer products might increase the risk of emission of volatile PFIs to the environment (Ruan et al. 2010a, 2010b). Fluorinated iodine alkanes (FIAs) and fluorinated telomer iodides (FTIs) have been detected in air and soil samples around a fluorochemical manufacturing plant in Shandong province in northern China (Ruan et al. 2010a). Residual FIAs and FTIs could also be incorporated into FTOH containing raw materials and fluorotelomer-based products during manufacturing. 1-Iodoperfluorooctane (PFOI) and 6:2 FTI have been detected in fluoroteiomer raw materials and selected fluorotelomer-based products, such as urethane polymer and phosphate surfactant (Larsen et al. 2006). Furthermore, unreacted residual FTOH has also been found in commercial and industrial products and could be released to the ambient environment as well (Dinglasan-Panlilio and Mabury 2006; Larsen et al. 2006). Likewise, residual PFIs in fluorinated polymers and surfactants can be released into the environment and degrade to other persistent PFCs. Abiotic or biotic transformation of FTIs could contribute to the environmental burden of FTOHs and perfluorocarboxylic acids (PFCAs) (Young et al. 2008). There is therefore a potential risk for release of PFIs to the environment due to direct emission during manufacturing and indirect emission from some fluorinated products.
Table 1. The structures of tested chemicals. Structure Chemical Fluorinated iodine PFBI, 1-iodoperfluorobutane alkanes (FIAs) (a=1) [MATHEMATICAL PFHxl, 1-iodoperfluorohexane EXPRESSION (a=3) NOT REPRODUCIBLE PFOI, 1-iodoperftuorooctane IN ASCII] (a=5) PFDI. 1-iodoperfluorodecane (a=7) PFDol, 1-iodoperfluorododecane (a=9) Fluorinated telomer 4:2 FTI, 1H, 1H, 2H, iodides (FTIs) 2H-perfluorohexyl iodide (b = 2) [MATHEMATICAL 6:2 FTI, 1H, 1H, 2H, EXPRESSION 2H-perfluorooctyl iodide (b = 4) NOT REPRODUCIBLE 8:2 FTI, 1H, 1H, 2H, IN ASCII] 2H-perfluorodecyi iodide (b = 6) 10:2 FTI, 1H, 1H, 2H, 2H-perfluorododecyl iodide (b = 8) Fluorinated diiodine PFBDI, Octafluoro-1, alkanes (FDIAs) 4-diiodobutane (c = 4) [MATHEMATICAL PFHxDI, Dodecafluovo-1, EXPRESSION 6-diiodohexane (c = 6) NOT REPRODUCIBLE PFODI, Hexadecafluoro-1, IN ASCII] 8-diiodooctane (c = 8) [MATHEMATICAL PFOC, 1H-perfluorooctane EXPRESSION (R = H) NOT REPRODUCIBLE PFOB, 1-bromoperfluorooctane IN ASCII] (R = Br) [MATHEMATICAL EXPRESSION PFOA, NOT REPRODUCIBLE IN ASCII] perfluorooctanoic acid [MATHEMATICAL EXPRESSION 1-lodohexane NOT REPRODUCIBLE IN ASCII] (a), (b), and (c) indicate the number of [CF.sub.2] units.
Increasing evidence has shown that some PFCs may have endocrine-disrupting potency. Some PFCs can disturb the thyroid system and neuroendocrine function, activate both peroxisome proliferator-activated receptors and estrogen receptors (ERs), and induce developmental toxicity in rodents (Lau et al. 2004). The estrogenic effects of some PFCs have been studied in many aspects. For example, Maraser al. (2006) demonstrated the estrogen-like properties of FTOHs in MCF-7 cells. Using yeast two-hybrid assays, Ishibashi et al. (2007, 2008) demonstrated that FTOHs can activate the male medaka (Oryzias latipes) and human ER. Liu et al. (2007) reported that vitellogenin expression was induced by perfluoro-octane sulfonate (PFOS), perfluorooctanoic acid (PFOA), and FTOHs in primary cultured tilapia hepatocytes, and they suggested that estrogenic effects may be mediated through the ER pathway. FTOHs also induced vitellogenin in male medaka fish through the activation of ER, whereas PFOS and PFOA did not (Ishibashi et al. 2008).
Little information is currently available regarding the estrogenic effects of PFIs. In the present study, we used three in vitro bioassays--E-screen assay, MVLN assay, and evaluation of an estrogen-responsive gene--to comprehensively evaluate the estrogenic potencies of PFIs. The structural features responsible for estrogenic effects were identified by the alternations in potency derived from specific structural changes.
Materials and Methods
Chemicals. The chemical structures of rested compounds are shown in Table 1. We purchased 1 -iodoperfluorobutane (PFBI; 98% pure), 1 -iodoperfluorohexane (PFHxI; 99% pure), 1 -iodoperfluoro-decane (PFDI; 97% pure), 1-iodopcrfluoro-dodecane (PFDol; 97% pure), 6:2 FTI (96% pure), 8:2 FTI (96% pure), hexadeca-fluoro-l,8-diiodooctane (PFODI; 98% pure), 1 H-perfluorooctane (PFOC; 99% pure), 1-bromoperfluorooctane (PFOB; 99% pure), 1-iodohexane (98% pure), and 4-hydroxy-tamoxifen (OHT; 98% pure) from Sigma Chemical Company (St. Louis, MO, USA); PFOI (98% pure), 4:2 FTI (93% pure), 10:2 FTI (95% pure), and PFOA (98% pure) from Fluka (Buchs, Switzerland); and octa-iluoro-l,4-diiodobutanc (PFBDI; 97% pure), dodecafluoro-1,6-diiodohexane (PFHxDI; 97% pure), and 17 [beta] -estradiol ([E.sub.2]; 99% pure) from Alfa Aesar (Ward Hill, MA, USA). We dissolved all the PFls, PFOB, [E.sub.2] and l-iodohexane in ethanol. PFOA and PFOC were dissolved in dimethyl sulfoxide as 100 mM and 10 mM scock solutions. All stock solutions were stored at -20[degrees] C.
Cell culture. Human MCF-7BUS breast adenocarcinoma cells and MVI.N cells were cultured in 100-mm culture dishes in a humidified atmosphere of 5% [CO.sub.2] at 37[degrees]C Cells were maintained in Dulbecco's modified Eagle's medium (DMEM)/F-12 (Hyclone, Logan, UT, USA) containing 10% fetal bovine serum, 100 U/mL streptomycin-penicillin, 2 mM L.-glutamine, and 1% insulin-transferrin-selenium supplement (all from Gibco, Grand Island, NY, USA).
E-screen assay. MCF-7BUS cells were kindly provided by A.M. Soto and C. Sonnenschein (Tufts University School of Medicine, Boston, MA, USA). In response to ER[alpha] agonists, the mitotic effect leads to the proliferation of MCF-7BUS cells. We performed the E-screen assay following a method modified from the protocol by Soto et al. (1995). Cells were trypsinized and plated into the interior 60 wells of 96-well plates at the density of 3,000 cells/well. Before each experiment, cells were starved in steroid-free (SF) medium for 48 hr to minimize the basal hormonal activity during assays. SF medium consisted of phenol red-free DMEM/F-12 (Hyclone) supplemented with 5% dextran-charcoal-trcatcd fetal bovine serum (Hyclone), 100 U/mL streptomycin-penicillin, and 2 mM L-glutamine. Cells were treated with serial dilutions of test chemicals (from 1 nM to 100 uM) in SF medium; a concentration range of 0.01-200 pM [E.sub.2] was used as the positive control. We used a WST-1. proliferation kit (Roche Diagnostics, Mannheim, Germany) to assess proliferation after 6 days of exposure according to the kit instructions. The WST-1 assay is based on the enzymatic cleavage of the tetrazolium salt WST-1 to formazan by cellular mitochondrial dehydrogenases present in viable cells. The absorbance of the WST-1 solution was detected by a microplate reader (Varioskan Flash, Thermo Fisher Scientific, Waltham, MA, USA) at 450 nm, with the reference wave length at 690 nm. The cell proliferation effect was calculated from the solvent control (0.1% ethanol) -corrccted absorbance and expressed as the percentage of maximal absorbance of the positive control. Three replicates were used in each experiment.
MVLN assay. The MVLN cell line was kindly provided by J.P. Giesy (Michigan Stare University, East Lansing, MI, USA). This cell line was stably transfected with the luciferase reporter gene and estrogen-responsive element derived from the Xenopus vitellogenin A2 gene. ER agonists can induce the production of luciferase in MVLN cells (Pons et al. 1990). Cells were seeded in the interior 60 wells of a 96-well ViewPlate (Packard Instrument Company, Boston, MA, USA) at a density of 7 x 104 cells/well, starved in SF medium for 48 hr, and exposed to test compounds for 2 days. A concentration range of 0.5 pM-1 nM [E.sub.2] was used as a positive control, whereas the exposure concentration range of test chemicals was 0.1 -- 100 uM. Luciferase activity was measured with the LucLite kit (Packard Instruments) according to the manufacturer's protocol. We measured luminescence by microplate reader (Varioskan Flash) and integrated the luminescence signal for 10 sec. Total protein content was measured by the Bradford assay (Tiangen, Beijing, China) to normalize luminescent units. The results are given as relative luminescent unit per microgram protein. The maximal induction of positive control (corrected lor solvent control, 0.1-0.2% ethanol) was set as 100%, and the responses of other chemicals were converted to a percentage of the maximum level. Three replicates were used in each experiment. The cytotoxicity of tested chemicals was examined by WST-1 kit in parallel and routinely observed under microscope to identify the exposure concentration range.
RNA isolation and reverse transcript Hon polymerase chain reaction (RT-PCR). MCF-7BUS cells were seeded in six-well plates at the density of 1.0 x 106 cells per well, starved in SF medium for 48 hr, and exposed to test compounds for 48 hr. First, cells were rinsed twice with cold phosphate-buffered saline, and total RNA was isolated using Trizol reagent (Invitrogen Inc., Carlsbad, CA, USA) following the manufacturer's protocol. The 260 nm and 280 nm absorbance reading of total RNA was performed using a Nanodrop spectrophotometer (Thermo Scientific, Waltham, MA, USA). The concentration of RNA was quantified by the reading at 260 nm. The 260:280 nm ratios were between 1.8 and 2.0, which indicates that the extracted RNA was sufficiently pure.
We used a two-step quantitative RT-PCR to quantify gene expression. Total RNA was converted to cDNA using M-MLV (Moloney murine leukemia virus) reverse transcriptase (Promega, Madison, WI, USA) with oligo dT (15), following the manufacturer's instructions. The final cDNA solution was diluted five times with DNase/RNase-free water (Gibco). Quantitative PCR was performed with a Stratagene MX3005 thermal cycler (Stratagene, La Jolla, CA, USA). PCR reaction mixtures (25 [micro] L) contained 12.5 [micro] L GoTaq Green Master Mix (Promega), 2 [micro] L diluted cDNA, and 0.2 [micro] M sense/antisense primers. The thermal cycle was 5 min at 95 [degrees] C, followed by 45 cycles of 15 sec at 95 [degrees] C, 30 sec at 55 [degrees] C, and 30 sec at 72 [degrees] C. The primer sequences of early growth response protein 3 (EGR3) were derived from Terasaka et al. (2004). We designed the primers of internal gene [beta]-actin and trefoil factor 1 (TFFI; pS2) with Primer Premier 5 software (Premier Biosoft International, Palo Alto, CA, USA). The primer sequences were as follows: for [beta]-actin (NM_001101), 5'-CACTCT TCCAGCCTTCCTTCC-3' (forward) and 5'-AGGTCTTTGCGGATGTCCAC-3' (reverse); for EGR3 (NM_004430), 5 '-CCATGATTCCTGACTACAACCTC-3' (forward) and 5'-GTGGATCTGCT TGTCTTTGAATG-3' (reverse); and for TFFI (NM_003225), 5'-AGAAGCG TGTCTGAGGTGTC-3' (forward) and 5'-GCAAATAAGGGCTGCTGTT-3' (reverse). The quantification of target gene expression was based on a comparative cycle threshold (Ct) value. We normalized the expression level of each target gene to its reference gene [beta]-actin. The fold change of the target genes was analyzed by the [2-.sub.[DELTA] [DELTA] Ct] method (Livak and Schmittgen 2001). We used melting curve analysis and agarose gel electrophoresis to verify the correct PCR products.
Statistical analysis. All results are expressed as the mean [+ or -] SD. For statistical analysis, we used one-way analysis of variance (ANOVA) and Tukey's multiple range test to assess the significance of mean differences. Difference was considered significant at a p-value [less than or equal to] 0.05.
The concentration-response analyses were performed with four-parameter logistic curve regression analysis according to the following formula:
y= minimum+(maximum-minimum)/[l+[(x/[EC.sub.50]).sup.Hill slope]], 
where y is the response value, x is the log concentration of the test compound, and [EC.sub.50] is the concentration that induces half of the maximum proliferation effect or luciferase activity.
[EC.sub.50] values were calculated from this nonlinear regression model. [EC.sub.20] were calculated as
[EC.sub.X]=[[x/(100-x)].sup.(1/Hill slopc)]x[EC.sub.50], 
where x is 20% of the maximum effects, and the Hill slope and [EC.sub.50] were calculated from Equation 1.
All statistical analyses were performed using Sigma Plot (version 10.0; Systat Software Inc., San Jose, CA, USA).
Stimulation of MCF-7 cell proliferation. We used the E-screen assay to investigate the estrogenic activities of 12 PFIs in MCF-7 cells. FIAs are monoiodized fluorinated alkanes with even-numbered chains that have 4-12 carbons. PFBI [4 carbons in its alkyl chain (C-4)], PFDI (C-10), and PFDol (C-12) did not show proliferation effects within the concentration ranges, whereas PFHxI (C-6) and PFOI (C-8) produced full concentration-response curves compared with [E.sub.2] (Figure 1A); [EC.sub.50] values were 0.63 [beta] M and 1.15 [beta] M for PFHxI and PFOI, respectively (Table 2). The proliferation effects appeared to be dependent on the chain lengths of FIAs. Fluorinated diiodine alkanes (FDIAs) have even-numbered chains with 4 to 8 carbons. All FDIAs produced full concentration-response curves in the E-screen assay (Figure IB). The relative proliferation effects were in the following order: PFHxDI (C-6) > PFODI (C-8) > PFBDI (C-4). Likewise, proliferation potency also seems to be related to the specific carbon chain length of FDIAs. The [EC.sub.50] values of PFBDI (1.45 [beta] M), PFHxDI (7.5 nM), and PFODI (43.3 nM) were much lower than those of the corresponding FIAs with the same chain length. The order of their relative proliferation potencies was PFHxDI > PFODI > PFHxI > PFOI > PFBDI. These compounds are thus considered ro behave like xenoestrogens in che li-screen assay.
Table 2. Maximum induction and effective concentrations of tested chemicals based on the E-screen and MVLN assays. E-screen Maximum Relative Compound Induction (%) (a) [EC.sub.50] Potency (b) [E.sup.2] 100 3.12 pM 1 PFBI ND (d) PFHxI 99 0.63 4.9x [micro] M [10.sup.-6] PFOI 101 1.15 2.7x [micro] M [10.sup.-6] PFDI ND (d) PFDoI ND (d) 4:2 FTI ND (d) 6:2 FTI ND (d) 8:2 FTI ND (d) 10:2 FTI ND (d) PFBDI 97 1.45 2.2x [micro] M [10.sup.6] PFHxDI 100 7.5 4.2x nM [10.sup.4] PFODI 105 43.3 7.2x] nM [10.sup.5 PFOA ND (d) PFOC ND (d) PFOB ND (d) 1-lodohexane ND (d) MIVLN assay Maximum Compound Induction (%) (c) [EC.sub.50] [EC.sub.20] [E.sup.2] 100 16.4 pM 4.14 pM PFBI ND (e) PFHxI 47 26.7 14.1 [micro] M [micro] M PFOI 25 35.1 20.4 [micro] M [micro] M PFDI ND (e) PFDoI ND (e) 4:2 FTI ND (e) 6:2 FTI ND (e) 8:2 FTI ND (e) 10:2 FTI ND (e) PFBDI 21 29.6 13.8 [micro] M [micro] M PFHxDI 73 1.13 0.38 [micro] M [micro] M PFODI 38 2.87 1.07 [micro] M [micro] M PFOA ND (e) PFOC ND (e) PFOB ND (e) 1-lodohexane ND (e) Relative Compound Potency(b) [E.sup.2] 1 PFBI PFHxI 0.29x [10.sup.-6] PFOI 0.2x [10.sup.-6] PFDI PFDoI 4:2 FTI 6:2 FTI 8:2 FTI 10:2 FTI PFBDI 0.3x [10.sup.6] PFHxDI 1.1x [10.sup.5] PFODI 3.8x] [10.sup.6 PFOA -. PFOC . PFOB 1-lodohexane ND, not detected. (a) Percentage of the maximum proliferation effects of tested compounds to that of [E.sub.2]. (b) Ratio of [EC.sub.50] of [E.sub.2]. to that of test compounds. (c) Percentage of the maximum induction effects of tested compounds to that of [E.sub.2]. (d) The maximum relative proliferation effect was < 7%; the absorbance ratio of [E.sub.2] (100 pM) to control was 2.1 [+ or -] 0.2. (e) The maximum relative luciferase activity was < 5%; the relative luminescent unit ratio of [E.sub.2] (1 nM) to control was 13.5 [+ or -] 2.4.
Transactivation in MVLN cells. The MVLN assay has been widely used to study ER activity of rest compounds (Freyberger and Schmuck 2005). In the present study, we used the MVLN assay to further investigate ER activity and estrogenic potency of PFIs. Before the MVLN assay, we tested the cytotoxic effects of each compound using the WST-1 assay. Exposure of MVLN cells to FlAs, FTIs, or FDlAs did not produce significant cytotoxicity within the concentration ranges, and no cytotoxic effects were observed by microscopic examination (data not shown).
Because these compounds did not show maximum induction compared with [E.sub.2], relative potency based on the [EC.sub.20] would be more reliable than that derived from the [EC.cub.50] (Villeneuve et al. 2000). The estrogenic effects of PFIs revealed by the MVLN assay were in accordance with the results of the E-screen assay. As shown in Figure 2A, the induction of luciferase activity by PFBI, PFDI, and PFDol were at the basal level (< 5%), whereas PFHxI and PFOI induced luciferase activity in a dose-related manner. PFHxI ([EC.sub.20] =14.1 [micro] M) showed higher estrogenic activity than did PFOI ([EC.sub.20] = 20.4 [micro] M) in MVLM cells, with maximum induction values of 47% and 25%, respectively (Table 2). Luciferase activity induced by FDIAs seems to be related to the specific carbon chain length (Figure 2B). PFHxDI ([EC.sub.20]=0.38 [micro] M) showed stronger estrogenic potency than did PFODI ([EC.sub.20]=1.07 [micro] M) and PFBDI ([EC.sub.20]=13.8 [micro] M), with the maximum induction values of 73%, 38%, and 21%, respectively. Because the difference of [EC.sub.50] or [EC.sub.20] values among PFHxI, PFOI, and PFBDI were small, we compared the estrogenic potency with the maximum induction value in an MVLN assay. The order of estrogenic potency was PFHxDI > PFHxI > PFODI > PFOI > PFBDI, which is comparable to results from the E-screcn assay. Similarly, FDIAs possessed stronger estrogenic potency than did FIAs in the MVLN assay (PFBDI > PFBI; PFHxDI > PFHxI; PFODI > PFOI), which indicated that iodine substitution at the end of a fluorinatcd chain may enhance the estrogenic potency of FIAs. The optimum chain length for estrogenic activity was six carbons for FIAs and for FDIAs in both of these estrogen-screening assays.
Comparison of PFCs with similar structures. FTIs are partially fluorinated alkyl iodides, which arc produced by the cthylation ofFlAs in telomerizarion processes. Compared with FlAs and FDIAs, FTIs with various chain lengths did not show estrogenic effects in the E-screen or MVLN assays within the tested concentration ranges (0.01-200 [micro] M). We used a nonfluorinatcd hydrocarbon, 1-iodohcxanc (C-6), as the control to study the effects of fluoridation on estrogenic effects. Three eightcarbon PFCs-PFOA, PFOC, and PFOB-that contain no iodine substitution on the carbon chain were used as comparisons to study die effects of iodine substitution on estrogenic effects. As we suspected, 1-iodohexane, PFOA, PFOC, and PFOB showed negative results in the estrogen-screening assays (Table 2). These results further emphasize that a perfluo-rinated alky I chain and iodine substitution are important structural features for the estrogenic effects of PFIs.
Coexposure assay with OHT in MVLN assay. We used OHT, a strong estrogen antagonist in the mammary gland, to block the ER in the MVLN assay. OHT was coexposed with PFHxI, PFOI, PFBDI, PFHxDI, or PFODI. We used the highest induction concentrations obtained from MVLN assay in the coexposure experiments and the gene expression assay. As shown in Figure 3, coexposure of OHT with the tested chemicals resulted in marked reduction of luciferase activity, which further confirmed that these xenoestrogens can activate the ER.
Expression of estrogen-responsive genes, After MCF-7 cells were exposed to a series of PFCs for 48 hr, the expression levels of two estrogen-responsive genes (EGR3 and TFF1) were analyzed by real-time PCR. The TFF1 gene is involved in cell proliferation and also serves as a biomarker gene responding to estrogens (Brown et al. 1984; jorgensen et al. 2000). As one of the ER-mediated estrogen-inducing genes, EGR3 belongs to the early growth response family and plays an important role in the estrogen-dependent induction of the immune evasion system (Inoue et al. 2004). The expression levels of EGR3 and TFF1 are up-regulated by natural and synthetic estrogens in MCF-7 cells (Terasaka et al. 2004). PFHxI, PFOI, PFBDI, PFHxDI, and PFODI, which showed estrogenic effects in the E-screen and MVLN assays, significantly up-regulated the estrogen-responsive genes by 4.4-, 2.7-, 2.7-, 5.7-, 8.5-, and 7.7-fold for TFF1 and by 2.4-, 3.6-, 2.4-, 9.1-, and 11.2-fold for EGR3 (Figure 4A). PFOC, PFOB, 1-iodohexane, PFBI, PFDI, PFDol, and FTIs did not affect the expression of EGR3 or TFF1, but PFOA slightly up-regulated TFF1 by 1.57-fold. The levels of EGM3 and TFF1 mRNA were greatly elevated by 8.7- and 9.2-fold upon exposure to [E.sub.2] (Figure 4B). Therefore, PFHxI, PFOI, PFBDI, PFHxDI, and PFODI showed estrogenic activity in these assays. These xenoestrogens activated ER, which was followed by increased expression of the estrogen-responsive genes. PFBDI showed weaker estrogenic potency than did PFHxDI or PFODI in the E-screen and MVLN assays, whereas the expression of EGR3 and TFF1 induced by PFHxDI and PFODI was much higher than that induced by PFBDI. The up-regulation of EGR3 and TFFl was also greater for FDIAs compared with the mono-iodized FIAs. This adds further evidence that an increase in iodine substitution at the end of the fluorinated chain can enhance the estrogenic potencies of FIAs.
The endocrine-disrupting effects elicited by industrial chemicals have been of extensive concern (Colborn et al. 1993). Exposure to xenoestrogens may lower sperm count and male fertility and increase the incidence of breast and testicular cancer in humans (Toppari et al. 1996). Most of the adverse effects of these compounds are thought to be mediated through ER activation. Although the environmental behaviors of PFIs are not known, these volatile and high-production-volume chemicals could be released into the ambient environment during production, storage, and transport. The atmospheric oxidation of PFIs may contribute to the increased levels of other PFCs in the environment. Studies of the potential toxicities of PFIs are therefore needed for health risk evaluation. In this study, we investigated the estrogenic effects of PFIs by the E-screen and MVLN assays and the expression of estrogen-responsive genes. Our results showed that PFHxI, PFOI, PFBDI, PFHxDI, and PFODI exert estrogenic effects through activation of the ER. The relative estrogenic potencies obtained from the E-screen and MVLN assays are both related to the specific carbon chain length of FlAs and FDlAs. The optimum chain length for estrogenic effects is six carbons, and iodine substitution on the perfluorinated chain was crucial for the estrogenic effects. Those potent compounds were able to fully stimulate cell proliferation of MCF-7 cells, but this was not the case for the induction of reporter gene expression in MVLN cells. This discrepancy might be due to the difference of initial seeding density, exposure rime, and sensitivity between the two assays. The expression of the estrogen-responsive gene by these PFIs further confirmed the results. The estrogenic potencies of FDIAs were higher than that of the FIAs, indicating that the increasing number of iodine substitutions on FIAs renders the chemical more potent in inducing estrogenic activity. PFHxDI (C-6), with two iodine substitutions (one at each end) of the per-fluorinated chain, showed the highest potency among the PFIs.
Considerable evidence has indicated that chain length determines the biological effect of PFCs (Hu et at. 2002; Liao et al. 2009; Upham et al. 1998). Bioconcentration and bioaccumulation of PFCs are related to the length of the fluorinated chain in different species (Martin et al. 2003). Cytotoxic end points of PFCs such as in vitro cytotoxic effects, the alteration of cell membrane potential, and cytosolic pH arc directly related to perfluorinated chain length (Kleszczynski and Skladanowski 2009). The inhibition of perfluorinated fatty acids on gap junction intercellular communication also depends on chain length; shorter PFCs, including perfluorobutanesulfonate and perfluorohexanesulfonate, did not show effects, whereas PFOS significantly inhibits gap junction intercellular communication (Hu et al. 2002; Upham et al. 1998). The interference of PFCs on cultured rat hippocampal neurons was also related to the carbon chain length and functional groups (Liao et al. 2009). Our findings suggest that FDIAs and some of the FIAs exert estrogen effects through the activation of ER. Because the solubility of nonpolar FIAs in culture media decreased with increasing chain length, the lack of estrogenic effects for PFDI and PFDol might be attributed, in part, to decreased solubility and bioavailability of long-chain FIAs.
We used the nonfluorinated organic iodide 1-iodohexane to study the effect of fluorination on estrogenic effects compared with PFHxI. In the screening assays, 1-iodohexane did not exert estrogenic effects, indicating that fluorination is an important structural feature for estrogenic activity. The hydrophobic property of the fluorinated chain imparts the proteinophilic and lipophilic property of PFCs and results in the interaction of PFCs with multiple biological molecular targets in various species. PFOA did not show proliferation effects in MCF-7 cells, as previously reported by Maras et al. (2006). In the present study, we found that PFOA, PFOB, and PFOC also lack estrogenic effects. By comparing the structure-activity relationship between these PFCs, we propose that the iodine substitution is a key attribute for the estrogenic effect. The estrogenic effect was also lower for monoiodized fluorinated alkanes than for diiodized fluorinated alkanes, which further supports our assumption.
FTOHs exert estrogenic activity in MCF-7 cells and aquatic organisms (Ishibashi ct al. 2008; Maras et al. 2006). FTOHs behave as estrogens because of the similarity of their chemical structure and properties to other xenoestrogens, such as 4-nonyIphenol. In the telomerization processes, fluorotelomer iodides are oxidized to produce FTOHs. Compared with FTOHs, none of the FTIs induced cell proliferation, which indicated that the hydroxyl group is more important for the estrogenic effects than is iodine substitution in partially Huorinated chemicals. Some of the PFIs activated the ER and induced luciferase activity in MVLN cells. However, it is questionable whether these PFIs are able to directly bind to and activate the ER. Structural features such as a phenol ring and a hydrophobic group attached para to the hydroxyl group are essential for the estrogenic effects (Blair et al. 2000; Laws et al. 2006; Suzuki and Shapiro 2007). Furthermore, hydroxylated analogs of polybrominated diphenyl ethers and polychlorinated biphenyls have been shown to exert estrogenic effects (Bergeron et al. 1994; Fielden et al. 1997; Meerts et al. 2001). Therefore, it may be reasonable to expect that hydroxvlated forms of FIAs and FDIAs could also be estrogenic.
Compared with PFOI, both PFOB and PFOC showed no estrogenic activity. It is likely that bond strength also determines their reactivity. The strength of the bonds is C-F (467 kJ/mol) > C-H (453 kJ/mol) > C-Br (290 kJ/mol) > C-I (228 kJ/mol). Among the four halogens, fluorine is the most electronegative and iodine the least. The polarization of the C-l bond is lower than that of the C-H bond and the other carbon-halogen bonds. Because iodine is a good leaving atom and because of the chemical reactivity of the C-I bond, it would be easier for PFIs to be converted to their hydroxylated analogs during the exposure studies. Oxidation of FIAs can result in the formation of PFCAs (Lehrnler 2005). In this reaction, [C.sub.n] [F.sub.2n+1] OH is thought to have been formed by the cleavage of C-T bonds in FIAs and addition of OH (Yamamoto et al. 2007). We hypothesize that [C.sub.n] [F.sub.2n+1] is hydrolyzed to [C.sub.n] [F.sub.2n+1] OH in the culture media or inside the cells, and the degradation products or the metabolites of PFIs are the possible targets for ER, thereby exerting estrogenic activity. However, the underlying mechanisms for the estrogenic effects of PFIs have not been completely clarified, and further studies are also warranted to characterize possible catabolites of PFIs, which might also exhibit estrogenic activity.
The main functions of hormones are to maintain homeostasis and regulate reproduction and development. Exposure to endocrine-disrupting chemicals may cause adverse effects to the organs and glands that secrete hormones, further resulting in endocrine toxicity such as impaired reproduction and development. PFIs are volatile chemicals and have been detected around fluorochemical manufacturing areas (Ruan et al. 2010a). As important precursors for the synthesis of organic fluoride products, PFIs could be incorporated into fluorotelomer raw materials and fluorotelomer-based products as residues (Larsen et al. 2006). Occupational and indoor environments might be exposure risk zones, and inhalation could be a possible exposure route.
Some PFIs could act on ERs and potentially cause detrimental effects on reproductive and developmental systems. To our knowledge, this is the first study to find estrogenic activity of PFIs using three in vitro methods. Considering the current large and increasing production volume of telomerization-based PFCs, more extensive studies should be conducted on the environmental distribution and toxicological effects of PFIs.
Bergeron JM, Crews D, Mciachlan JA. 1994. PCBs as environmental estrogens-turtle sex determination as a biomarker of environmental contamination. Environ Health Perspect 102:780-781.
Blair RM, Fang H, Branham WS, Hass BS, Dial SL, Moland CL, et al. 2000. The estrogen receptor relative binding affinities of 188 natural and xenochemicals: structural diversity of ligands. Toxicol Sci 54(1):138-153.
Brace NO. 1999. Syntheses with perfluoroalkyl radicals from perfluoroalkyl iodides. A rapid survey of synthetic possibilities with emphasis on practical applications. Part one: alkenes, alkynes and allylic compounds. J Fluor Chem 93(1):1-25.
Brown AMC, Jeltsch JM, Roberts M, Chambon P. 1984. Activation of pS2 gene-transcription is a primary response to estrogen in the human-breast cancer cell-line MCF-7. Proc Natl Acad Sci USA 81(20):6344-6348.
Colborn T, Saal FSV, Soto AM. 1993. Developmental effects of endocrine-disrupting chemicals in wildlife and humans. Environ Health Perspect 101:378-384.
Dinglasan-Paniilio MJA, Mabury SA. 2006. Significant residual fluorinated alcohols present in various fluorinated materials. Environ Sci Technol 40(5):1447-1453.
Dupont 2005. DuPont Global PFOA Strategy. Presentation to the U.S. EPA, January 31, 2005. Public Docket AR226-1914. Washington, DC: U.S. Environmental Protection Agency, Office of Pollution Prevention and Toxics.
Ellis DA, Martin JW, De Silva AO, Mabury SA, Hurley MD, Andersen MPS, et al. 2004. Degradation of fluorotelomer alcohols: a likely atmospheric source of perfluorinated carboxylic acids. Environ SciTechnol 38(12):3316-3321.
Ellis DA, Martin JW, Mabury SA, Hurley MD, Andersen MPS, Wallington TJ. 2003. Atmospheric lifetime of fluorotelomer alcohols. Environ Sci Technol 37(17):3816-3820.
Fielden MR, Chen I, Chittim B, Safe SH, Zacharewski TR. 1997. Examination of the estrogenicity of 2,4,6,2',6'-pentachloro-biphenyl (PCB 104), its hydroxylated metabolite 2,4,6,2',6'-pentachloro-4-biphenylol (HO-PCB 104), and a further chlorinated derivative, 2,4,6,2',4',6'-hexachlorobiphenyl (PCB 155). Environ Health Perspect 105:1238-1248.
Freyberger A, Schmuck G. 2005. Screening for estrogenicity and anti-estrogenicity: a critical evaluation of an MVLN cell-based transactivation assay. Toxicol Lett 155(1):1-13.
Giesy JP, Kannan K. 2001. Global distribution of perfluorooctane sulfonate in wildlife. Environ Sci Technol 35(7):1339-1342.
Hu WY, Jones PD, Upham BL, Trosko JE, Lau C, Giesy JP. 2002. Inhibition of gap junctional intercellular communication by perfluorinated compounds in rat liver and dolphin kidney epithelial cell lines in vitro and Sprague-Dawley rats in vivo. Toxicol Sci 68(2):429-436.
Inoue A, Omoto Y, Yamaguchi Y, Kiyama R, Hayashi SI. 2004. Transcription factor EGR3 is involved in the estrogen-signaling pathway in breast cancer cells. J Mol Endocrinol 32(3):649-661.
Ishibashi H, Ishida H, Matsuoka M, Tominaga N, Arizono K. 2007. Estrogenic effects of fluorotelomer alcohols for human estrogen receptor isoforms alpha and beta in vitro. Biol Pharm Bull 30(7):1358-1359.
Ishibashi Hr Yamauchi R, Matsuoka M, Kim JW, Hirano M, Yamaguchi A, et al. 2008. Fluorotelomer alcohols induce hepatic vitellogenin through activation of the estrogen receptor in male medaka [Oryzias latipes). Chemosphere 71(10):1853-1859.
Jorgensen M, Vendelbo B, Skakkebaek NE, Letters H. 2000. Assaying estrogenicity by quantitating the expression levels of endogenous estrogen-regulated genes. Environ Health Perspect 108:403-412.
Kleszczynski K, Skladanowski AC. 2009. Mechanism of cytotoxic action of perfluorinated acids. I. Alteration in plasma membrane potential and intracellular pH level. Toxicol Appl Pharmacol 234(3):300-305.
Larsen BS, Stchur P. Szostek B, Bachmura SF, Rowand RC, Prickett KB, et al. 2006. Method development for the determination of residual fluorotelomer raw materials and perflurooctanoate in fluorotelomer-based products by gas chromatography and liquid chromatography mass spectrometry. J Chromatogr A 1110(1-2):117-124.
Lau C, Butenhoff JL, Rogers JM. 2004. The developmental toxicity of perfluoroalkyl acids and their derivatives. Toxicol Appl Pharmacol 198(2):231-241.
Laws SC, Yavanhxay S, Cooper RL, Eldridge JC. 2006. Nature of the binding interaction for 50 structurally diverse chemicals with rat estrogen receptors. Toxicol Sci 94(1):46-56.
Lehmler HJ. 2005. Synthesis of environmentally relevant fluori-nated surfactants -- a review. Chemosphere 58(11):1471-1496.
Liao CY, Wang T. Qui L, Zhou QF, Ou3n SM, Jiang GB. 2009. Changes in synaptic transmission, calcium current, and neurite growth by perfluorinated compounds are dependent on the chain length and functional group. Environ Sci Technol 43(6):2099-2104.
Liu C, Du Y, Zhou B. 2007. Evaluation of estrogenic activities and mechanism of action of perfluorinated chemicals determined by vitellogenin induction in primary cultured tilapia hepatocytes. Aquat Toxicol 85(4):267-277.
Livak KJ, Schmittgen TD. 2001. Analysis of relative gene expression data using real-time quantitative PCR and the [2.sup.-[DELTA][DELTA]Ct] method. Methods 25(4):402-408.
Maras M, Vanparys C, Muylle F, Robbens J, Berger U, Barber JL, et al. 2006. Estrogen-like properties of fluorotelomer alcohols as revealed by MCF-7 breast cancer cell proliferation. Environ Health Perspect 114:100-105.
Martin JW, Mabury SA, Solomon KR, Muir DCG. 2003. Bioconcentration and tissue distribution of perfluorinated acids in rainbow trout (Oncorhynchus mykiss). Environ Toxicol Chem 22(1):196-204.
Meerts IATM, Letcher RJ, Hoving S, Marsh G, Bergman A, Lemmen JG, et al. 2001. In vitro estrogenicity of poly-brominated diphenyl ethers, hydroxylated PBDEs, and polybrominated bisphenol A compounds. Environ Health Perspect 109:399-407.
Olsen GW, Burris JM, Ehresman DJ, Froehiich JW, Seacat AM, Butenhoff JL, et al. 2007. Half-life of serum elimination of perfluorooctanesulfonate, perfluorohexanesulfonate, and perfluorooctanoate in retired lluorochemical production workers. Environ Health Perspect 115:1298-1305.
Organisation for Economic Co-operation and Development. 2004. The 2004 OECD List of High Production Volume Chemicals. Paris: Organization for Economic Co-operation and Development. Available: http://www.oecd.orq/dataoec<i/55/38/33883530.pdf [accessed 3 November 2006].
Pons M, Gagne Dr Nicolas JC, Mehtali M. 1990. A new cellular-model of response to estrogens -- a bioluminescent test to characterize (antij estrogen molecules. Biotechniques 9(4):450-459.
Prevedouros K, Cousins IT, Buck RC, Korzeniowski SH. 2006. Sources, fate and transport of perfluorocarboxyiates. Environ Sci Technol 40(1):32-44.
Ruan T, Wang YW, Wang T, Zhang QH, Ding L, Liu JY, et al. 2010a. Presence and partitioning behavior of polyfluori-nated iodine alkanes in environmental matrices around a fluorochemical manufacturing plant: another possible source for perfluorinated carboxylic acids? Environ Sci Technol 44(15):5755-5761.
Ruan T, Wang YW, Zhang QH, Ding L, Wang P, Qu GB, et al. 2010b. Trace determination of airborne polyfluorinated iodine alkanes using multisorbent thermal desorption/ gas chromatography/high resolution mass spectrometry. J Chromatogr A 1217(261:4439-4447.
Soto AM, Sonnenschein C, Chung KL, Fernandez MF, Olea N, Serrano F0. 1995. The E-SCREEN assay as a tool to identify estrogens -- an update on estrogenic environmental-pollutants. Environ Health Perspect 103(suppl 7):113-122.
Suzuki T, Shapiro S. 2007. Predicting relative binding affinities for the ER-alpha estrogen receptor from molecular structure [Abstract]. J Pharm Pharmacol 59:A8.
Terasaka S, Aita Y, Inoue A, Hayashi S, Nishigaki M, Aoyagi K, et al. 2004. Using a customized DNA microarray for expression profiling of the estrogen-responsive genes to evaluate estrogen activity among natural estrogens and industrial chemicals. Environ Health Perspect 112:773-781.
Toppari J, Larsen JC, Christiansen P, Giwercman A, Grandjean P, Guillette LJ, et al. 1996. Male reproductive health and environmental xenoestrogens. Environ Health Perspect 104(suppl 4): 741-803.
Upham BL, Deocampo ND, Wurl B, Trosko JE. 1998. Inhibition of gap junctional intercellular communication fay perfluorinated fatty acids is dependent on the chain length of the fluorinated tail. Int J Cancer 78(4): 491-495.
Villeneuve Dl, Blankenship AL, Giesy J P. 2000. Derivation and application of relative potency estimates based on in vitro bioassay results. Environ Toxicol Chem 19(11): 2835-2843.
Yamamoto T, Noma Y, Sakai SI, Shibata Y. 2007. Photodegradation of perfluorooctane sulfonate by UV irradiation in water and alkaline 2-propanol. Environ Sci Technol 41(16):5660-5665. Young CJ, Hurley MD, Wallington TJ, Mabury SA. 2008. Atmospheric chemistry of 4:2 fluorotelomer iodide (n^FgC^Cfyl): kinetics and products of photolysis and reaction with OH radicals and CI atoms. J Phys Chem A 112(51):13542-13548.
Chang Wang, Thanh Wang, Wei Liu, Ting Ruan, Qunfang Zhou, Jiyan Liu, Aiqian Zhang, Bin Zhao, and Guibin Jiang
State Key Laboratory of Environmental Chemistry and Ecotoxicology, Research Center for Eco-Environmental Sciences, Chinese Academy of Sciences, Beijing, People's Republic of China
Address correspondence to G.Jiang, Research Center for Eco-Environmental Sciences, Chinese Academy of Sciences, P.O. Box 2871, Beijing 100085 China. Telephone: 86-10-62849129. Fax.: 86-10-62849339-E-mail: email@example.com
This study was supported by the Ministry of Science and Technology of the People's Republic of China (2007BAC27B02-la and 2009AA06Z407) and the National Natural Science Foundation of China (B20977100, 20921063 and 20897011).
The authors declare they have no actual or potential competing financial interests.
Received 6 April 2011; accepted 11 October 2011.
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|Author:||Wang, Chang; Wang, Thanh; Liu, Wei; Ruan, Ting; Zhou, Qunfang; Liu, Jiyan; Zhang, Aiqian; Zhao, Bin;|
|Publication:||Environmental Health Perspectives|
|Date:||Jan 1, 2012|
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