The Aryl hydrocarbon receptor mediates reproductive toxicity of polychlorinated biphenyl congener 126 in rats.

There was no difference in mean body weight between the groups at the beginning of the experimental period. After 28 days of exposure to PCB126, rats in the WT_PCB group weighed less than WT_O rats ( P 0.05; Figure 1A ). There was also no difference in body weight between the WT_O and AHR −/− _O groups ( P > 0.05; Figure 1A ). Relative ovarian weight (ovarian weight/body weight) was reduced in the WT_PCB group compared to WT_O ( P 0.05) or between WT_O and AHR −/− _O rats ( P > 0.05) ( Figure 1B ). Relative uterine weight did not differ between any groups ( P > 0.05; Figure 1C ). Exposure to PCB126 in WT rats increased ( P < 0.05) FSH and decreased ( P 0.05) between treatment groups in serum levels of testosterone ( Figure 2D ). Luteinizing hormone was higher in the AHR −/− _PCB than in AHR −/− _O ( P = 0.05) rats ( Figure 2B ). AHR deficiency reduced ( P 0.05) in the mean number of primordial or primary follicles between any groups ( Figure 3A , B ). In WT rats, exposure to PCB126 reduced ( P 0.05; Figure 3A – D ). There was also no difference in number of follicles of corpora lutea between WT_O and AHR −/− _O ovaries. Mean uterine area was reduced ( P 0.05) between the AHR −/− _O and AHR −/− _PCB rats ( Figure 4A ). There was also no difference ( P > 0.05) in uterine area between the WT_O and AHR −/− _O groups ( Figure 4A ). Mean uterine gland number was reduced ( P 0.05) between the AHR −/− _O and AHR −/− _PCB rats ( Figure 4B ). There was no difference ( P > 0.05) in uterine gland number between the WT_O and AHR −/− _O rats ( Figure 4B ). Neither PCB126 exposure nor AHR deficiency affected the ratio of glands/μm 2 area ( Figure 4C ). There was no difference ( P > 0.05) in abundance of the ERA ( Figure 5A ) or the ERB ( Figure 5B ) protein in any of the uterine compartments analyzed (stroma, luminal epithelium, and glandular epithelium) due to PCB126 exposure. Loss of AHR reduced ERA levels in the stroma ( P < 0.05; Figure 5A ) and the GE ( P < 0.05; Figure 5A ) but there was no impact of AHR loss on ERA abundance in the LE ( Figure 5A ), nor was there any impact of AHR deficiency on ERB straining in any compartment ( Figure 5B ). Exposure to PCB126 altered the abundance ( P < 0.05) of mRNA encoding 46 of the 84 chemical metabolism genes analyzed in WT rats (WT_O v WT_PCB; Table 1 ). Similarly, the abundance of mRNA encoding 31 genes were altered ( P < 0.05) due to loss of AHR (WT_O vs. AHR −/− _O; Table 2 ). However, there were no PCB126-induced alterations observed in the mRNA level of any genes in the AHR −/− rats (AHR_O v AHR_PCB). Ten genes differed ( P < 0.05) due to PCB126 exposure in the WT rats (WT_O v WT_PCB; Table 3 ), while only three were altered ( P < 0.05) in the AHR −/− rats due to PCB126 exposure (AHR −/− _O vs. AHR −/− _PCB; Table 4 ). Three genes ( P < 0.05) were reduced in abundance in AHR −/− _O relative to WT_O rats (WT_O vs. AHR −/− _O; Table 5 ). Exposure to PCB126 altered ( P 0.05) on abundance of mRNA encoding investigated genes in the AHR −/− rats exposed to PCB126 (AHR −/− _O vs. AHR −/− _PCB). One gene differed ( P < 0.05) in transcript abundance between the WT_O and the AHR −/−_ O ( Table 7 ).

The AHR −/− rat model was developed at the University of Kansas Medical Center after obtaining approval from the Institutional Animal Care and Use Committee with a Holzman-Sprague Dawley rat strain. The model was generated using CRISPR/Cas9-mediated disruption of the Ahr basic helix loop helix DNA binding domain. Ahr mutant rats identical to those used in this experiment are available at the Rat Resource & Research Center (RRRC# 831; strain name SD-Ahrem1Soar; University of Missouri, Columbia, MO; www.rrrc.us ). PCB126 (3,3’,4,4’,5-pentachlorobiphenyl) was synthesized, purified, and characterized as described in previous publications from our group [ 36 ]. A total of 25 female rats, 14 wild type (WT) and 11 AHR −/− , were included in the study. Rats were fed a standard rodent diet (Teklad 8604, Envigo), and singly housed in a wire cage with a controlled environment (14:10 h light:dark cycle). All animals had free access to food and water. Both WT and KO rats were injected with a single intraperitoneal (i.p.) dose of corn oil vehicle (5 mL/kg body weight) or PCB126 (1.63 mg/kg body weight), equivalent to 5 µmol/kg body weight) in corn oil at four weeks of age (experimental day one). This dose was chosen as it has been used in several earlier studies to investigate effects of PCB126 exposure while minimizing overt toxicity [ 37 , 38 ]. Since a major goal of the study was to identify a functional role for the AHR in modulating ovarian PCB126-induced effects, a PCB126 dose that is known to cause systemic toxicity was required. There was a total of four groups: WT_O (n = 7), WT_PCB (n = 7), AHR −/− _O (n = 5) and AHR −/− _PCB (n = 6). Two deaths occurred in the WT-PCB group following injection but prior to planned necropsy date. After 24 days of exposure, all rats received a one-time intraperitoneal injection of 40 µg gonadotropin releasing hormone (L4513, Sigma-Aldrich) dissolved in sterile phosphate buffered saline (PBS) to synchronize estrous cycles prior to euthanasia and all animals were confirmed to be at the estrus stage at euthanasia. Twenty-eight days following exposure to PCB126, rats were euthanized using carbon-dioxide asphyxiation followed by thoracotomy. After euthanasia, whole blood was collected through cardiac puncture into non-anticoagulant coated tubes. Blood was allowed to clot at room temperature and centrifuged at 1500 x g for 10 min. Serum was aliquoted from each animal and frozen at −80°C. Serum 17β-estradiol, progesterone, testosterone, follicle stimulating hormone (FSH), luteinizing hormone (LH) and anti-Müllerian hormone (AMH) were measured at the University of Virginia Center for Research in Reproduction Ligand Assay and Analysis Core ( https://med.virginia.edu/research-in-reproduction/contact-us/ligand-assay-analysis-core/ ) with appropriate controls for each assay included. Vaginal smears were collected and analyzed according to previously published protocols [ 39 , 40 ]. The ovaries and uteri were dissected, removed, and weighed. One ovary and one uterine horn per animal was fixed in 10% neutral buffered formalin and the other ovary and uterine horn were flash frozen in liquid nitrogen and stored at −80°C. Formalin fixed ovaries from five animals per treatment group (n = 20) were embedded in paraffin and serially sectioned at a thickness of 5 µm. Every 12 th section was mounted on a microscope slide and stained with hematoxylin and eosin. Two blinded assessors performed independent follicle counts. Inter-assessor reliability was determined using the intraclass correlation coefficient (ICC) and means of values from the assessors were used in the analysis. Statistical analysis was performed using one-way ANOVA (SPSS 25). Formalin fixed uterine horns from all animals (n = 23) were embedded in paraffin. 5 µm thick sections were selected from each quarter of the specimen (four sections per horn/animal) to obtain representative images of the entire horn. Sections were mounted and stained with hematoxylin and eosin. Images were captured of each of the four sections per animal with the same microscope configuration and magnification. Images were then analyzed in a blinded fashion and total uterine area (number of endometrial glands and glands per unit area) was calculated. Image J software (NIH, https://imagej.nih.gov/ij/index.html ) was used for the analysis with appropriate calibration. A total of ten 5 µm thick tissue sections from each of the 23 animals were used to assess the relative expression of estrogen receptor alpha and estrogen receptor beta proteins in the uterus using immunohistochemistry. Sections were deparaffinized in Citrisolv™ and rehydrated in graded ethanol. Antigen retrieval was performed by microwaving sections in sodium citrate buffer at full power for 10 minutes (10 mM sodium citrate, pH 6 with 0.5% Tween). Sections were cooled to room temperature and incubated in a solution containing 5% goat serum, 1% bovine serum albumin, 1% DMSO and Image IT-Fx ( I36933 , ThermoFisher) in PBS for one hour at room temperature to block nonspecific binding. The sections were incubated overnight at 4°C with either rabbit monoclonal antibody against estrogen receptor alpha (ERA) (1:100, ab32063, Abcam), rabbit polyclonal antibody against estrogen receptor beta (ERB) (1:100, ab3576, Abcam) or no primary antibody (negative control). After primary antibody binding, the sections were washed in PBS and incubated with Alexa-Fluor 488 conjugated goat anti-rabbit (1:200, 4412S, Cell Signaling) secondary antibody for 90 minutes at room temperature in a humidified slide incubation chamber. Sections were washed in PBS and mounted using SlowFade™ Gold mountant containing 4′,6-diamidino-2-phenylindole (DAPI) for counterstaining (S36938, ThermoFisher). All images were captured with a Leica DMI3000 B fluorescence microscope at the same intensity, exposure, and magnification. The quantification of estrogen receptor expression in the uterus was performed in three compartments: the stroma, luminal epithelium, and glandular epithelium. Of the ten tissue sections per animal, five were used to investigate the ERA and the other five were used to investigate the ERB. One of those five was used as a negative control for each antibody per animal. Acquired microscope images had adequate representation of all compartments of interest. Two images were taken of each primary antibody-stained section and one image was captured of the negative controls. ImageJ software was then used in a blinded fashion to calculate the total immunofluorescence in each compartment of interest in each image. Acquisition settings remained stable for each image. Ribonucleic acid (RNA) was isolated from ovaries and uteri to perform RT 2 profiler PCR arrays. Two different arrays, the rat metabolism array (PARN-002Z, Qiagen) and rat inflammation array (PARN-011Z, Qiagen), were employed on ovarian tissue. Ovarian RNA from three animals per exposure group was included in each array (n = 12). The same rat inflammation array was used on uterine tissue, also including RNA from three animals per exposure group (n = 12). RNA was isolated using RNeasy Mini kit (Qiagen) and concentrations determined using a ND-1000 Spectrophotometer (λ = 260/280 nm; NanoDrop Technologies). Total RNA (200 ng) was reverse transcribed to complementary DNA (cDNA) using an RT 2 first-strand kit (Qiagen) combined with an appropriate RT 2 SYBR Green master mix (Qiagen). The regular cycling program consisted of a 10 min hold at 95°C and 40 cycles of denaturing at 95°C for 15 sec along with a combined annealing and extension for 1 min at 60°C. Data were normalized with Actb , B2m , Hprt1 , Ldha , and Rplp1 housekeeping genes and analyzed using Qiagen software ( https://www.qiagen.com/us/shop/genes-and-pathways/data-analysis-center-overview-page/ ). All appropriate technical controls were employed, including no template and no primer controls. A fold change cut off of two was used. For all experiments, statistical analysis was performed using two-way ANOVA (SPSS 25) with post-hoc t-test with Welch’s correction. A biologically meaningful change was considered if the P -value was ≤ 0.05.

While production of PCBs has been banned worldwide, humans continue to be exposed to these compounds due to their persistent nature. Reproductive aged women in the United States currently have detectable levels of PCBs in their serum [ 3 , 4 ]. There is sufficient evidence to suggest that PCB exposure leads to adverse reproductive outcomes [ 41 – 43 ] and potentially even inter- [ 16 ] and trans-generational damage [ 17 ]. Endocrine disruption [ 18 ] and altered hypothalamic gene expression [ 19 ] across generations due to Aroclor 1221 exposure have been determined in rats. In the ovary, PCB126 exposure decreased follicle number, reduced 17ß-estradiol and progesterone, and altered estrous cyclicity in exposed rats [ 44 ]. PCB126 exposure also decreased progesterone synthesis [ 45 ], and decreased 17β-estradiol [ 46 ] in cultured porcine luteal cells. In cultured bovine luteal cells PCB126 reduced calcium mobilization in granulosa cells, potentially affecting ovarian steroidogenesis [ 47 ]. Further evidence for an ovarian impact of PCB126 exposure due to induction of mitochondrial apoptotic pathway has been demonstrated [ 48 ]. Despite these studies, modes of ovarian action of PCB126 remain unclear. The aims of this study were two-fold: the first was to determine ovarian and uterine effects of PCB126 and to determine if the ovary has the xenobiotic biotransformation capacity to respond to PCB126 exposure and the second was to use a rat model of AHR deficiency to investigate the requirement and involvement of AHR in PCB126-induced ovarian and uterine dysfunction. Transgenic rodent models have been used to investigate the role of the AHR in reproductive organ development and function. Mice deficient in AHR had reductions in ovarian reserve, reduced 17β-estradiol production, altered uterine 17β-estradiol response, and increased rates of miscarriage [ 28 , 49 ]. No studies on female reproductive function have been performed in AHR deficient rats, nor are there any studies in rats and mice assessing the AHR response to PCB126 exposure in the ovary or uterus. For this reason, the dose chosen for the study was one that is known to cause PCB126-induced toxicity but which does not cause overt systemic toxicity as evidenced by a recent study in which body weight gain was unaffected by PCB126 exposure for approximately 35 days after exposure [ 6 ]. In order to assess if AHR deficiency affected PCB126-induced female reproductive toxicity, a dose that caused effects in the WT rats was required. The half-life of PCB126 in humans is 3.32–5.58 years with the fat composition of the body influencing the elimination time [ 26 ]. In rats, PCB126 was determined not to have declined over a 22-day period, indicating a slow elimination [ 50 ]. Thus, in this study, a single dose of PCB126 at a dose known to cause toxicity was utilized to assess both basal reproductive toxicity as well as to determine a role for the AHR in mediating these effects. At the onset of dosing there was no difference in body weight across the experimental groups. It is noteworthy that two rats in the WT group who were exposed to PCB died, though no AHR −/− rats had this response. In addition, WT rats lost body weight post PCB126 exposure, but the AHR −/− rats displayed no effect of PCB126 exposure on their body weight. These findings imply a systemic impact of PCB126 exposure in the WT but not the AHR −/− rats. The PCB126-induced decline in body weight was unexpected and could have resulted in PCB-induced secondary effects that altered ovarian and uterine function. This is an area for future research on PCB126-induced reproductive toxicity. The ovary weight was lower in the WT but not AHR −/− rats, suggesting that ovotoxicity occurred due to PCB126 exposure. Follicle depletion can result from toxicant exposure [ 51 ] and there were decreased numbers of secondary and antral follicles in the WT rats exposed to PCB126. This follicle depleting impact of PCB126 exposure was limited to the large pre-antral and antral follicles, since there was no impact of PCB126 exposure on primordial or small follicle number. These findings were in agreement with a previous study on PCB126 exposed rats in which antral follicles were reduced in number, however that study classified ovarian follicles only as pre-antral or antral [ 44 ], thus the current study has determined that PCB126-induced follicle loss is evident at the secondary follicle stage onwards. The AHR −/− rats treated with either oil or PCB126 did not differ from the WT control rats in any follicle stage of development. Loss of more developed follicles induced by PCB126 in WT rats could be phenotypically manifested as anovulation or lowered 17β-estradiol levels in circulation. These findings support a specificity for PCB126 on reducing secondary and antral follicles but not more immature follicles stages and also provide evidence that the AHR is required for ovarian toxicity that occurs due to PCB126 exposure. The ovary is a steroidogenic organ and ovaries were collected at estrus, at which time 17β-estradiol is the predominant sex steroid hormone present. Exposure to PCB126 exposure reduced circulating 17β-estradiol and progesterone and increased follicle stimulating hormone. The reduction in 17β-estradiol and progesterone is in alignment with reduced levels of antral follicles and corpora lutea in the ovary due to PCB126 exposure. A recent study determined increased Cyp17a1 and Cyp19a1 transcript abundance and increased intra-ovarian 17β-estradiol content in Ahr −/− adult mice relative to their WT littermates [ 52 ]. In addition, increased follicle stimulating hormone as noted herein could result from decreased 17β-estradiol and is often a clinical indicator of ovarian senescence [ 53 ]. Exposure to PCB126 increased LH in the AHR −/− rats but not the WT rats, potentially indicating a direct pituitary effect of PCB126 exposure in the absence of AHR. No impact of AHR deficiency was noted on LH level, however, LH was lower in pre-pubertal Ahr −/− mice, relative to their WT counterparts, but this was not sustained into adulthood [ 52 ]. In addition, PCB126 exposure decreased the abundance of circulating anti-Müllerian hormone in WT rats, which is likely a secondary effect of the observed reduction in secondary and antral follicle number caused by PCB126 exposure since anti-Müllerian hormone is produced by those follicle stages. This PCB126-reduced anti-Müllerian hormone was not observed in the AHR −/− rats, indicating that PCB126 is an ovarian endocrine disruptor and that this is mediated through the AHR. In WT rats exposed to PCB126, there were increases in 44 and decreases in two ovarian mRNA transcript levels, indicating that the ovary responded to the PCB126 exposure in chemical metabolism gene induction. Many of these genes, including Cyp1a1 , Cyp1b1 and Gstp1 are known targets of the AHR [ 54 – 56 ], thus our findings recapitulated what is known about AHR function. These data do not discount a functional role for additional transcription factors in regulating transcription of the genes investigated. Interestingly in WT rats, Ahr mRNA was also induced, which indicates that Ahr is important for the ovarian response to PCB126 exposure recapitulating previous findings [ 57 ]. Both Gpx1 and Ggt1 were reduced by PCB126 exposure in the ovary. Interestingly, Gpx1 was also reduced in livers of PCB exposed male rats [ 38 ]. The ovarian involvement of Gpx1 as an antioxidant has been documented in response to other ovotoxicants [ 58 – 60 ] and to be altered with ovarian aging [ 61 ]. Less is known regarding the ovarian role of Ggt1 , though an association with GGT1 abundance and incidence of ovarian tumors [ 62 ] and Ggt1 polymorphism and polycystic ovarian syndrome is documented [ 63 ]. Exposure to PCB126 increased mRNA encoding paraoxonase 1 ( Pon1 ) which we previously observed to be also increased by PCB126 exposure in rat livers [ 64 ]. The PON1 enzyme activity in follicular fluid was associated with serum levels [ 65 ] and it was proposed that PON1 protein was transported into the follicle by HDL. Also, Pon1 polymorphism is associated with increased risk for polycystic ovarian syndrome [ 66 ]. Myeloperoxidase 1 ( Mpo1 ), an oxidant generating enzyme, was increased in the ovary of WT rats exposed to PCB126. While normally expressed only in myeloid cells, aberrant MPO expression has been observed in other tissues and associated with various diseases. Atypical MPO levels can lead to oxidative damage and elevated MPO was associated with ovarian cancer potentially through reduced apoptosis in epithelial ovarian cancers [ 67 ]. Additional genes that are known to have important functional roles in the ovary were increased in abundance in the WT PCB126-exposed rats include Cyp17a1 , Hsb17b3 and Cyp19a1 which are involved in the production of 17β-estradiol in the steroidogenic pre-ovulatory follicles. Despite reduced circulating 17β-estradiol, the ovary may be compensating to induce steroidogenic gene mRNA abundance. Thus, in the WT rats, exposure to PCB126 induced genes involved in chemical biotransformation and steroidogenesis. In the rats deficient in AHR, there was a complete absence of any changes in mRNA transcript abundance, supporting an important functional role for AHR in PCB126 ovarian biotransformation. It is recognized that PCB126 exposure has immunological effects [ 68 – 70 ], thus, the study determined if there were alterations in mRNAs of genes encoding inflammatory proteins in both the ovary and the uterus. In the ovary of WT rats, PCB126 exposure increased the abundance of 10 inflammatory mRNAs including the tumor necrosis factor family members, Tnfsrsf11b and Tnfsf10 . As the receptor for RANKL, increased Tnfsrsf11b could indicate altered granulosa cell communication [ 71 ]. Tnfsf10 (Trail ) induces ovarian apoptosis [ 72 ] and is increased in ovaries from females with metabolic disease [ 73 ] suggesting involvement in cell death responsible for the observed lower follicle number in the PCB126 exposed rats. In aging ovaries, IL6 has been determined to be reduced [ 74 ], potentially indicating a role for PCB126-induced Il6st in a pro-apoptotic function in this study. Corresponding also to the PCB126-reduced follicle numbers were increased Bmp2 as potentially a compensatory response since BMP2 has roles in folliculogenesis [ 75 ] and viability of secondary follicles [ 76 ]. The chemokine receptor, Ccr1 , was increased by PCB126 exposure, and has an ovarian role [ 77 ] and is observed to be involved in ovarian inflammation as a receptor for CCL5 [ 78 ]. Other biomarkers for polycystic ovary syndrome, Csf1 [ 79 ] and Pf4 [ 80 ] were increased by PCB126 exposure. The receptor for IL1 was increased by PCB126 exposure and Il1 deficiency is associated with a prolonged ovarian lifespan [ 81 ]. The Cxc3cr1 gene encodes the receptor for fractalkine which has a role in regulation of ovarian steroidogenesis in LH-responsive granulosa cells [ 82 ] and in modulating PI3K signaling [ 83 ], a known folliculogenesis regulator [ 84 ]. In the rats deficient in the AHR, there were decreased abundance of three mRNAs, Ccl11 , Ccl22 and Il11 due to PCB126 exposure. Increased ovarian stromal expression of Ccl11 is associated with ovarian aging [ 85 ], Il11 is increased in ovulatory follicles in the rat ovary [ 86 ] while less regarding a role for ovarian Ccl22 is known. Thus, these mRNAs could be direct targets of PCB126 independent of the AHR. Taken together, exposure to PCB126 in WT rats induced mRNAs related to apoptosis, steroidogenesis regulation and with roles in ovarian pathologies, supporting an ovarian dysfunction-induction by PCB126 exposure. Uterine gland number and uterine area were both reduced in response to PCB126 exposure, but this effect was absent in the AHR deficient rats. A negative impact of PCB126 on uterine weight was previously reported [ 87 ], however our study was at a lower PCB126 exposure and this was not noted herein. The impact of PCB126 exposure on uterine inflammatory mRNAs as well as the localization and abundance of the estrogen receptors were investigated. Thirteen uterine mRNAs were altered by PCB126 exposure in WT rats with only one of these being reduced in abundance. Three mRNAs with roles in uterine endometrial function, Ccl24 [ 88 , 89 ], Ccl19 [ 90 ], Ccl5 [ 91 , 92 ], were increased by PCB126 exposure. Increased Il33 observed due to PCB126 exposure is associated with inflammation during endometriosis [ 93 ] as is abnormal expression of Il1r1 [ 94 ] and Ccr1 [ 95 ]. Uterine BMP2 is a marker of decidualization [ 96 ] and was increased by PCB126 exposure. Increased Pf4 is associated with endometrial cancer [ 97 ] and endometritis [ 98 ]. Less is known about the uterine function of Tnfrsf11b though lack of the ligand, RANKL, in mice is associated with higher pre-term fetal loss [ 99 ]. Uterine roles for Cx3cr1 , Cxcl12 and Cxcr5 are documented related to maternal-conceptus interface [ 100 , 101 ], endometriosis [ 102 ] and endometrial remodeling [ 103 ]. Another gene with a role in endometriosis, Ldha [ 104 ], had reduced abundance due to PCB126 exposure. In the AHR deficient rats, increased Il2rb was noted, potentially an AHR-independent target of PCB126. A role for Il2rb in endometrial hyperplasia is supported in mice [ 105 ]. Despite reduced 17β-estradiol in PCB126 exposure WT rats, no impact of PCB126 exposure was observed on the level of ERA and ERB in stroma, luminal or glandular epithelium in either the WT or AHR deficient rats, discounting this as a PCB126 mode of action. Interestingly, lack of AHR reduced levels of ERA but not ERB in the stroma and glandular epithelium in the absence of a PCB126 exposure. Collectively, these findings support that there are PCB126-induced alterations to genes with roles in uterine pathology including endometriosis in agreement with recent human studies associating PCB exposure with increased risk for this disease [ 106 ]. This study supports activation of the AHR by PCB126, and that the ovary responds to PCB126 exposure in the form of increased xenobiotic metabolism and inflammatory mRNAs. Further, as summarized in Figure 6 , in WT rats, PCB126 exposure reduces body weight, ovary weight, secondary and antral follicles, corpora lutea, progesterone, 17β-estradiol, AMH, uterine gland number and area, increased FSH, and alters ovarian chemical biotransformation and inflammatory mRNA levels. These responses were almost completely absent in rats deficient in AHR, demonstrating the requirement for AHR action for ovarian and uterine impacts of PCB126. Although ovarian steroid hormones were not affected by PCB126 exposure in AHR −/− rats, LH was increased. Thus, PCB126 acts as an endocrine disruptor with strong evidence of a role for the AHR in this outcome. The impact of PCB126 on several hormones could be a secondary effect of the reduction in large pre-ovulatory follicles, altered systemic metabolism or changes to hormone half-life. Several of the mRNAs identified to be altered in the ovary and uterus by PCB126 exposure are associated with polycystic ovary syndrome and endometriosis, respectively, two common reproductive pathologies that affect a large number of women.

Polychlorinated biphenyls (PCBs) are persistent organic pollutants that were extensively employed in the electrical, electronics, plastics, paint, and pesticide industries until production, but not use, was banned in the United States in 1977 due to harmful health effects [ 1 ]. Exposure to PCBs is ongoing, via ingestion of contaminated food, inhalation of contaminated air, and sometimes dermal/occupational exposure [ 2 ]. As a consequence, PCBs have been detected in the serum of 71% of reproductive aged women, as well as in human follicular fluid, ovarian tissue, placenta, uterine muscle, amniotic fluid, breast milk, semen, and fetal cord blood [ 3 – 5 ]. Polychlorinated biphenyls are endocrine disrupting chemicals broadly classified as dioxin-like and non-dioxin-like congeners based on their similarities in toxicity to 2,3,7,8-tetrachlorodibenzo-p-dioxin (TCDD) with PCB126 being the most potent dioxin-like toxin among PCBs [ 6 ]. Reproductive toxicity has been demonstrated in both animal and human studies following exposure to PCBs. In human women, PCB exposure has been associated with altered menstrual function, earlier onset of menopause, increased miscarriage risk, and increased time to pregnancy [ 5 , 7 – 12 ]. In men, PCB exposure has been associated with decreased sperm parameters [ 5 , 13 ] and endocrine disruption [ 14 ]. Furthermore, PCBs cross the placenta [ 15 ] and have transgenerational effects [ 16 – 19 ], including evidence of epigenetic alterations in sperm and brain [ 20 ]. Individuals exposed to PCBs in utero have decreased fecundity, reduced antral follicles, lower birth weight, and lower IQ [ 2 , 21 – 24 ]. The mechanisms through which PCBs impart reproductive harm remain to be fully elucidated in both the male and the female, since both could contribute to reproductive and transgenerational impacts of PCBs. Although PCB126 was a minor component of commercial PCB mixtures, it contributes a majority of dioxin equivalents in many environmental samples [ 25 ]. The half-life of PCB126 in humans is years in duration [ 26 ]. Many biologic effects of PCBs are receptor mediated and dioxin-like PCBs, including PCB126, bind to the aryl hydrocarbon receptor (AHR), a cytosolic, ligand–activated, nuclear transcription factor [ 27 ]. The most well studied AHR target genes include those of the cytochrome P450 family, such as Cyp1a1 , Cyp1a2 and Cyp1b1 , which encode xenobiotic metabolizing enzymes [ 28 ]. Exposure to PCB126 increases transcript abundance of the Cyp1 genes in rat liver, lung, spleen, kidney, stomach and thymus [ 29 ]. Biotransformation of endogenous and xenobiotic compounds can result in the formation of toxic metabolites as well as metabolic byproducts including reactive oxygen species. It is proposed that activation of the AHR and its downstream effects contribute to PCB-induced adverse health outcomes [ 30 ]. Furthermore, the AHR pathway interacts with the estrogen receptor pathway and multiple immunologic pathways, thus, AHR activation could be responsible for altered immunologic and endocrine phenotypes [ 31 – 34 ]. The AHR is highly conserved among mammalian species and is found throughout the reproductive tract, including in the uterus and ovaries of both animals and humans [ 28 , 35 ]. Although AHR function after toxicant exposure has been investigated widely for the past 40 years, its physiological role has only recently been evaluated [ 32 ]. Understanding the role of AHR in reproductive biology is insufficient, though it is known that the absence of Ahr in mice leads to impaired reproductive function [ 28 ]. This study used a rat model of AHR deficiency to investigate whether adverse reproductive effects following PCB126 exposure are mediated by the AHR and to investigate ovarian PCB126 biotransformation and inflammation mRNA induction in the ovary and uterus.