TCDD-induced multi- and transgenerational changes in the methylome of male zebrafish gonads.

As our understanding of the effects of environmental contaminants expands, we now know that certain chemicals cause adverse health effects for both the directly exposed generation and subsequent generations that were either indirectly exposed through the germline or not exposed at all. Transgenerational effects that are passed from exposed to unexposed generations are thought to be propagated epigenetically by mechanisms such as DNA methylation, histone modifications, and/or small non-coding RNA ( 1 ). The list of contaminants known to produce transgenerational effects will continue to grow but currently includes chemicals such as phthalates ( 2–4 ), lead ( 5 , 6 ), polychlorinated biphenyls ( 7 , 8 ), and dioxins, specifically 2,3,7,8-tetrachlorodibenzo- p -dioxin (TCDD) ( 9–11 ). TCDD is a persistent environmental toxicant formed as a byproduct of industrial processes including incineration, metal production, and paper and pulp bleaching ( 12 ). TCDD bioaccumulates ( 13 ), thus the main method of modern-day human exposure is ingesting animal products such as meat, fish, and dairy ( 12 ). Toxic effects of TCDD are generally propagated through binding and activation of the aryl hydrocarbon receptor (AhR) leading to acute health effects including headaches, nausea, and skin irritation ( 14 ). Additional long-term health impacts can include reproductive effects with decreased fertility, defects in spermatogenesis, and endometriosis ( 10 , 15 ); liver effects including fibrosis, disrupted transcriptomics, and tumorigenesis ( 16–18 ); and several types of cancer including breast, stomach, colon, ovary, and testis ( 19 ). As the most potent AhR agonist, the effects of TCDD are well characterized; therefore, it can be used as a model chemical to better understand the mechanisms of other AhR agonists and/or endocrine disrupting chemicals. Trans- or multigenerational effects following TCDD exposure have been reported in rodents ( 2 , 9 ), fish ( 10 , 11 ), and humans ( 20–22 ) at concentrations as low as 50 ppt. Exposure levels of TCDD in humans are generally very small, estimated at an average 0.5 pg/kg (parts per quadrillion) body weight per day in the USA ( 23 ), so it is essential to determine the effects of such low level exposures, especially on sensitive populations such as developing organisms. Transgenerational mechanisms are thought to be propagated through epigenetic effects, and several studies have examined various epigenetic effects of TCDD ( 24 ); however, no study has yet evaluated the specific mechanisms through which epigenetic effects translate to transgenerational outcomes. Understanding the mechanism(s) underlying these transgenerational outcomes is necessary to identify prevention and treatment options for both exposed and unexposed generations. Zebrafish ( Danio rerio ) are an ideal model organism to study transgenerational effects of chemical exposure. Since their eggs are externally fertilized, fewer generations are needed to study transgenerational effects in zebrafish than in rodent models ( 25 ). Females release hundreds of eggs per spawning event, thus many fish can be exposed simultaneously during early development allowing for medium- to high-throughput screening of environmental toxicants. Importantly, zebrafish are an NIH-approved human model organism with a fully sequenced genome allowing for translational genomic, transcriptomic, and epigenetic analysis. Previous work in our lab revealed significant differential methylation of specific genes in the testes of zebrafish exposed to TCDD during sexual differentiation and maturation ( 26 ). Testes were the target organ of this previous study because of earlier work in which we discovered transgenerational reproductive effects, primarily male-mediated, in TCDD-exposed fish ( 11 , 25 ). Adult zebrafish in the F0 generation and two subsequent unexposed generations (F1 and F2) displayed TCDD-induced fertility defects, as defined by fewer eggs released and a decreased percentage of eggs fertilized, as well as defects in spermatogenesis. In addition, transcriptomic analysis revealed that differentially expressed genes were involved in similar fertility-related pathways across all three generations, though the specific genes involved in these pathways varied. In this study, we aim to integrate findings from these previous experiments by investigating DNA methylation as a mechanism of transgenerational inheritance of reproductive effects following TCDD exposure. We chose to investigate DNA methylation because it is the most well-studied, thus relatively well understood, epigenetic mechanism. In addition, other studies have demonstrated the presence of DNA methylation in response to TCDD exposure ( 9 , 27–29 ), but no one has yet examined the transgenerational whole genome DNA methylation response to TCDD exposure. Here, we examine DNA methylation status of the testes of F1 and F2 offspring of the TCDD-exposed F0 generation. Using whole genome bisulfite sequencing, we found changes in the DNA methylation profile of all three generations in the form of differentially methylated sites (DMSs), regions (DMRs), and genes (DMGs), each of which reveal different types of information. DMSs represent a change in methylation at a single base while DMRs represent a change in the methylation status of a region of DNA, defined in this study as 1 kb. DMRs are often associated with diseases including inflammatory bowel syndrome, post-traumatic stress disorder, and colon cancer, and are generally more replicable in multiple individuals with the same disease status than DMSs ( 30–33 ). Nevertheless, DMSs provide useful information as well and should not be overlooked. Several of the DNA methylation changes found in this study overlap with differentially expressed genes and among generations.

Zebrafish (AB strain) were kept at 28°C in buffered reverse osmosis water (60 mg/l Instant Ocean Salts; Aquarium Systems, Mentor, OH, USA) with a standard light/dark cycle of 14/10 h and fed Aquatox Fish Diet flakes (Zeigler, PA, USA) twice per day, supplemented with brine shrimp. Fish were raised in beakers with daily water changes of 40–60% at a density of five fish per 400 ml beaker between 3- and 6-week post-fertilization (wpf), and five fish per 800 ml beaker between 6- and 9-wpf. Adult fish were raised on a recirculating system at a maximum density of five fish per liter until euthanization at 1-year post-fertilization. Fish were euthanized with tricaine methanesulfonate (1.67 mg/ml). Animal use protocols were approved by the Institutional Animal Care and Use Committees at Wayne State University and the University of Wisconsin–Madison, according to the National Institutes of Health Guide to the Care and Use of Laboratory Animals (Protocol No. M00489). Exposures were performed as previously described ( 34 ). TCDD (>99% purity; Chemsyn) was used as a 0.4 ng/μl stock solution in dimethyl sulfoxide (DMSO). Zebrafish were exposed at 3-wpf and again at 7-wpf to waterborne TCDD (50 pg/ml) or vehicle (0.1% DMSO) for 1 h in glass beakers with gentle rocking. The number of fish per volume of dosing solution was 1 fish/ml at 3-wpf and 1 fish/2 ml at 7-wpf. All results are derived from three independent TCDD exposure experiments performed in successive blocks. These exposed fish are referred to as F0 fish. At maturity, F0 males and females were spawned to yield the F1 generation, which were kept as separate blocks, each derived from F0 fish from a single experiment. These were in turn crossed at adulthood to produce the F2 generation fish, again descended from discrete exposure experiments. The fish tissues used for methylation analysis originated from the same blocks as those used in the previously published microarray and histology studies ( 34 , 35 ). Testes were extracted from F1 and F2 generation zebrafish descended from TCDD- and DMSO- (vehicle) treated zebrafish and flash frozen in liquid nitrogen. Samples were kept at −80°C until DNA isolation. DNA isolation was performed on 4 DMSO control and 4 TCDD-exposed samples using the BioRobot EZ1 workstation following the provided protocol from Qiagen (Hilden, Germany). Concentration and quality of DNA was measured using Qubit (Invitrogen, Carlsbad, CA, USA) and DropSense 96 (Trinean, Gentbrugge, Belgium), respectively ( Supplementary Table S1 ). DNA was collected from different testicular tissue than used for RNA collection and microarray analysis. Microarray data were previously analyzed ( 11 , 35 ). Microarray data for the F0 generation ( GSE77335 ), and the F1 and F2 generations ( GSE111446 ) are available on the NCBI GEO database. Microarray data were analyzed with one-way between subject ANOVA using the Transcriptome Analysis Console (TAC, Affymetrix). Genes uploaded into Ingenuity Pathway Analysis (IPA; Qiagen Bioinformatics; Redwood City, CA, USA) for pathway analysis were defined as significantly altered with a P -value ≤0.05 and absolute fold change ≥1.5. Gene expression was validated by qPCR of nine genes of interest. The validation and IPA analysis data was previously reported ( 11 ). Although all microarray data were previously uploaded, fold changes for a subset of genes not reported in the previous paper are discussed here for the first time. Bisulfite conversion of methylated cytosines of DNA from F1 and F2 zebrafish testes was performed using the EZ DNA Methylation Kit (Zymo, Irvine, CA, USA). The resulting bisulfite-converted ssDNA was converted to Illumina libraries with the TruSeq DNA Methylation Kit (Illumina, San Diego, CA, USA). DNA libraries were sequenced with 100-bp paired-end reads on an Illumina HiSeq 2500 run in high output mode. Reads from six F1 and six F2 fish testes (three controls and two descendants of TCDD-treated fish for the F1 generation, and two controls and four descendants of TCDD-treated fish for the F2 generation after removing samples that did not pass our quality control cutoffs post-amplification) were aligned (bismark 0.18.1; bowtie2 2.2.3) to the zebrafish genome (dR10) and DMSs were determined (methylKit 1.6.3) between conditions ( 36–38 ). Methylated sites (percent methylation change >5%; P -value ≤0.05) were annotated to the nearest gene. Five percent methylation change was used as a cutoff based on previous ( 39–41 ). These cutoff values for significant methylation change are consistent with our previous publication examining changes in DNA methylation in the F0 generation ( 26 ) and other DNA methylation studies ( 40 , 42 ). Raw data and processed files were uploaded to the NCBI GEO database (record GSE149919 ). Differentially expressed genes from the microarray data were overlapped with annotations for DMSs. Individual replicates from each condition were kept separate and not pooled. Genes associated with differential methylation (methylation change >5%, P -value ≤0.05) were converted to homologous human genes and uploaded into IPA software and analyzed using RefSeq ID as the identifier.  T Pathway analysis was performed on the available F1 (1094 molecules for DMSs and 3057 molecules for DMRs) , and F2 (21 molecules for DMSs and 17 molecules for DMRs) for enriched disease and biologic functions.

A total of 5706 sites (2955 hypermethylated, 2751 hypomethylated; P -value <0.05) were significantly differentially methylated in the testicular tissue from the F1 generation ( Fig. 1A ). For the F2 generation, 230 DMSs were identified with 79 hypermethylated and 151 hypomethylated ( Fig. 1B ). We previously reported 397 DMSs in the F0 generation with 113 sites hypermethylated and 284 hypomethylated ( 26 ). No changes in global methylation levels were discovered in either generation, similar to the F0 generation findings ( 26 ). In the F1 generation, most DMSs are within the gene body, relatively equally divided between introns and exons ( Fig. 2A ). This was not the case for both the F0 and F2 generations in which the majority of DMSs are in the intergenic region ( Fig. 2B ) ( 26 ). Volcano plot of significantly DMSs between F1 generation ( A ) and F2 generation ( B ) descendants of TCDD-treated and -untreated zebrafish testes depicting percent methylation change and P -value of methylated sites (circles). Significantly changed CpG sites (percent methylation change 5%; P -value ≤0.05) are in yellow Distribution of significant (percent methylation change ≥5%; P -value ≤0.05) F1 generation ( A ) and F2 generation ( B ) DMSs relative to nearest gene. x-Axis represents location of DMS relative to nearest gene and y-axis represents number of sites at each location The F1 generation had 11 583 DMRs and the F2 generation had 130; 6730 of the DMRs in the F1 generation were hypomethylated and 4854 were hypermethylated. Like the F1 DMSs, an even distribution of intragenic DMRs was observed between exons and introns; however, there were overall more intergenic than intragenic F1 DMRs. In the F2 generation, 94 of the DMRs were hypomethylated and the remaining 36 were hypermethylated. Most of the DMRs in the F2 generation were located outside of the gene body. In total, there were 132 DMGs in the F0, 5353 genes in the F1, and 53 in the F2 generation ( Fig. 3 ). Fewer DMGs were found in the F0 and F2 generations compared to the F1. A large proportion of these genes (93% for F0 and 96% for F2), however, were also differentially methylated in at least one other generation, and 34 genes were differentially methylated in all three generations ( Supplementary Table S3 ). Only 2.5% of DMGs in the F1 generation overlapped with a DMG in another generation. Of the 5353 DMGs in the F1 generation, 383 were associated with only DMSs, 3382 were associated with only DMRs, and the remaining 1242 were associated with both DMSs and DMRs. In the F2 generation, 16 were associated with just DMSs, 13 with just DMRs, and 21 with both DMSs and DMRs. Many of the DMGs in both the F1 and F2 generations are involved in pathways such as reproduction, endocrine system, xenobiotic metabolism, and epigenetics, as shown in Tables 1–3 . Though there were many more DMGs in the F1 generation, more IPA pathways were related to male reproduction in the F2 generation than the F1 ( Tables 4 and 5 ). Venn diagram of significantly differential methylated genes and overlap in F0, F1, and F2 generations ( P -value <0.05) Differentially methylated F1 genes involved in reproduction Numbers of DMSs and regions are shown with direction of methylation change. Gene is associated with a DMR. Gene is associated with a DMS. Differentially methylated F1 genes involved in the endocrine system, drug metabolism, histone modifications, or DNA methylation Numbers of DMSs and regions are shown with direction of methylation change. Gene is associated with a DMS. Gene is associated with a DMR. Differentially methylated F2 genes involved in reproduction, the endocrine system, and epigenetic processes Numbers of DMSs and regions are shown with direction of methylation change. Gene is associated with a DMS. Gene is associated with a DMR. F1 IPA pathways related to male reproduction F2 IPA pathways related to male reproduction In the F1 generation, 159 genes were both differentially methylated and expressed ( Table 6 and Supplementary Table S2 ) while in the F2 generation, there were five ( pbx3b , si: dkey-266f7.5 , snai3 , tmem132e , and capn7 ; Table 7 ), four of which (all except tmem132e ) were differentially methylated in all three generations ( Supplementary Table S3 ). We previously found that the F0 generation had seven DMGs that were also differentially expressed ( 26 ), one of which ( rab11bb ) was differentially methylated in the F1 and F2 generations as well ( Supplementary Table S3 ). Of the 159 genes in the F1 generation, 29 have DMSs or regions located in the exon, 21 in the intron, 90 in a location outside of the gene body, and 19 had methylated sites or regions in multiple locations. In addition, 34% of the F1 genes have the same direction of gene expression and DNA methylation change (e.g. up-regulated and hypermethylated or down-regulated and hypomethylated), 30% have opposite directions of gene expression and DNA methylation change, and the remaining 27% have multiple sites of differential methylation that are both hyper- and hypomethylated. Genes both differentially methylated and differentially expressed in the F1 generation with roles in reproduction Nucleotide excision repair protein; decreased expression associated with defects in spermatogenesis Nakane et al ( 53 ) and Singh et al . ( 54 ) Cofactor in the beta-adrenergic receptor kinase-mediated desensitization of beta-adrenergic receptors; involved in FSH signaling pathway All DMSs and/or DMRs are listed. Gene is associated with a DMR. Gene is associated with a DMS. All genes both differentially methylated and differentially expressed in the F2 generation All DMSs and/or DMRs are listed. Gene is associated with a DMS. Gene is associated with a DMR. Several of the F1 genes that are both differentially methylated and differentially expressed have reproductive effects ( Table 6 ), and one gene in the F2 generation ( snai3 ) is involved in spermatogenesis ( 43 ). Transcriptomic analysis identified 25 differentially expressed genes in the F1 generation and 19 genes in the F2 generation with roles in epigenetic regulation ( Tables 8 and 9 ). Of these genes, 56% were down-regulated in the F1 generation and 74% down-regulated in the F2 generation. The majority of these epigenetic genes were involved in either methyl or acetyl group histone modifications. Differentially expressed F1 and F2 genes involved in epigenetic processes Fold changes and P -values of differentially expressed F1 and F2 genes involved in epigenetic processes

We discovered that TCDD exposure during sexual differentiation and maturation causes multi- and transgenerational DNA methylation changes in testicular tissue from zebrafish with decreased reproductive capacity. While all three generations had site-specific changes in DNA methylation, the F1 generation had substantially more DMSs, DMRs, and DMGs than either the F0 or F2 generations. In addition, of the DMSs in the F1 generation, most were located within the gene body, almost equally distributed between introns and exons, while in the F0 and F2 generations most DMSs were found in intergenic regions that consist of non-coding DNA. This could explain the small percentage of overlapping DMGs between the F1 and F0/F2 generations compared to the higher percentage of overlapping DMGs between the F0 and F2 generations and also suggests that TCDD has the largest effect on DNA methylation multigenerationally (i.e. indirectly on the F1 generation), as opposed to directly (F0) or transgenerationally (F2). In fact, the F1 generation had the greatest number of genes that were both differentially methylated and expressed. Although these findings do not correlate with phenotypes, as the most severe decreases in reproductive capacity were observed in the F0 generation ( 10 , 35 ), or transcriptomic outcomes, which were most altered in the F2 generation ( 11 ), it is not unusual for patterns of epigenetic inheritance to be generationally distinct ( 9 , 44 , 45 ). These outcomes are likely due to the shifting balance between direct and heritable effects of exposure in each generation and align with a dynamic view of epigenetic inheritance, in which multiple epigenetic mechanisms interact with the transcriptome in a nonlinear fashion across generations ( 46 ). Another potential explanation of the differences in methylation between generations could be different proportions of testicular cell types. We previously found a reduction in mature sperm cells (spermatozoa) and an increase in immature sperm cells (spermatogonia) in the F0 and F1 generations of TCDD-exposed zebrafish compared to control, but no change from control in the F2 generation ( 11 , 35 ). DNA methylation status changes by cell type ( 47 ), so it is possible that these histological findings have some impact on the differential methylation status we find between experimental and control fish and between generations. However, this does not fully account for the increase in DMSs and DMRs in the F1 over the F0 generation ( Fig. 3 ), because the histological outcomes between the F0 and F1 generations were similar ( 11 , 35 ). Several genes that were differentially methylated in all three generations are involved in reproductive processes, including mitochondrial regulator stoml2 ( 48 ), fmr1 , implicated in the progression of spermatogenesis and RNA regulation ( 49 , 50 ), and snai3 , also involved in spermatogenesis as well as embryonic mesodermal formation ( 43 ). A subset of DMGs involved in reproduction also had differential gene expression, including: otud6 and sall1a , which are both associated with cryptorchidism ( 51 , 52 ); xpa and arrb1 , which are both nucleotide excision repair genes likely involved in spermatogenesis ( 53 , 54 ); and acox1 , involved in fatty acid beta oxidation and required for fertility in mice ( 55 ) in the F1 generation, as well as snai3 in the F2 generation ( Tables 6 and 7 ). Interestingly, acox1 is differentially expressed in both the F1 and F2 generations, although only differentially methylated in the F1. Unexpectedly, we found minimal overlap between differential methylation and expression in each generation, despite the association of many DMGs with pathways related to TCDD exposure endpoints including reproduction, endocrine system function, xenobiotic metabolism, and epigenetics ( Tables 1–3 ). One possible explanation for the mismatch between transcriptomic and methylomic outcomes is that methylation patterns, in general, are established during early development and remain consistent throughout the majority of adulthood, whereas the transcriptome is dynamic across the lifespan. It is possible that altered methylation patterns established early in life are dysregulating development-specific transcriptomic networks, which are no longer evident in adulthood when the methylome and transcriptome were evaluated. Several DMGs in both the F1 and F2 generations with roles in reproduction (discussed in detail below) have shown distinct patterns of expression specifically during gonadal development ( 43 , 56 , 57 ). Future work will evaluate acute gene expression changes in zebrafish gonads during reproductive development in response to TCDD exposure. The influence of other epigenetic mechanisms on gene expression may offer another potential explanation for the discrepancy between differentially methylated and expressed genes. In addition to DNA methylation, other mechanisms including histone modifications and non-coding RNAs, are often involved in regulation of gene expression ( 58–60 ). For instance, histone modifying proteins can interact with DNA methyltransferases ( 61 ) and conversely, the status of DNA methylation can affect the status of chromatin structure and histone modifications ( 62 ). In this study, the F1 generation had at least 28 DMGs involved in epigenetic pathways ( Table 2 ), including the histone acetyltransferase mrgbp ( 63 ), which was differentially methylated in all three generations and was the only epigenetic-related DMG found in the F2 generation. These epigenetic-related DMGs have a known role in histone modifications with the exception of 3 DMGs in the F1 generation, specifically dnmt3aa , dnmt3ab , and dnmt3ba , which are de novo DNA methyltransferases ( 64 ). Similarly, we uncovered a large subset of differentially expressed genes involved in histone modification in both the F1 and F2 generations, including: histone demethylase, kdm6bb ; histone methyltransferases, prdm6 and kmt2d ; histone deacetylases, sall1a and hdac10 ( 65–69 ). Our data suggest that DNA methylation is likely one of multiple epigenetic mechanisms regulating transgenerational reproductive transgenerational changes in responses to TCDD exposure in zebrafish. Several findings were not surprising based on previous TCDD exposure studies. For instance, transgenerational reproductive effects of TCDD exposure are mainly male-mediated ( 10 , 11 ). Similarly, exposure to endocrine-disrupting compounds in rodents led to male germline-associated transgenerational outcomes, including reproductive effects and DNA methylation changes ( 70–74 ). We observed a large percentage of DMGs overlapping among all three generations, suggesting these sites were inherited transgenerationally and supporting a mechanism of paternal inheritance for DNA methylation. In fact, Potok et al . ( 75 ) showed that DNA methylation of the early embryo is nearly identical to that of the parental sperm. Furthermore, many of the DMGs in the F1 and F2 generations are involved in reproductive processes, including spermatogenesis, Sertoli cell junctions, and gonadal development ( Tables 1 and 3 ). Collectively, our findings support the hypothesis that defects in spermatogenesis are a mechanism for decreased male fertility due to altered sperm development in the F0–F2 generation following TCDD exposure in the F0 generation ( 11 ). Our previous research also showed F0–F2 zebrafish with female secondary sex characteristics and appearance, but testicular tissue upon dissection ( 10 ). In the F1 generation, genes related to sexual differentiation were also differentially methylated ( Table 1 ). One of these genes, nr0b1 , plays an important role in sexual differentiation in multiple organisms including humans ( 76 , 77 ), rodents ( 78 ), and fish ( 79 ). Chen et al . ( 79 ) found that homozygous nr0b1 knockout zebrafish underwent a female to male sex reversal. Two isoforms of Sox9, a regulator of sexual differentiation and maturation in many species ( 80 , 81 ), were also differentially methylated in the F1 generation. Zebrafish have two isoforms of sox9: sox9a , which is expressed in testes, and sox9b , which is expressed in ovaries. All juvenile zebrafish develop a premature ovary early in development that either matures to become a functional ovary or undergoes apoptosis and develops into testes. This process is thought to be mediated by the sox9 axis, specifically an increase in sox9a is found in gonads transitioning from ovaries to testes ( 57 ). Our findings suggest that dysregulation of many genes, not a single pathway, contributes to TCDD’s sexual differentiation effects and support the hypothesis that sox9a and/or sox9b cause dysregulation of gonad development followed by uncoupling from other sexual-development functions ( 11 ). Finally, TCDD is a strong agonist for AhR, and most of the effects of TCDD exposure are mediated through this receptor ( 82 ). Therefore, it was unsurprising that three AhR genes, ahr1a , ahr1b , and ahr2 , were differentially methylated in the F1 generation ( Table 2 ). Of the three, Ahr2 had the most DMSs and regions. Though humans have only one AhR gene, in zebrafish, TCDD binds both ahr1b and ahr2 (not ahr1a ), but only ahr2 is necessary for a toxic response to TCDD exposure, including skeletal and fin abnormalities and yolk sac and cardiac edema ( 83 ). In the F0 and F2 generation, none of the three AhR genes were differentially methylated; however, ahr2 expression was up-regulated in both the F0 and F2 generations, but not in the F1. The F0 up-regulation could be explained by a positive feedback mechanism in which AhR activation leads to increased AhR gene expression, which has been found in innate lymphoid cells ( 84 ). In addition, it is conceivable that differential methylation of the AhR genes in the F1 prevented up-regulation, and could be protective mechanism following indirect exposure. In conclusion, developmental TCDD exposure led to changes in DNA methylation of zebrafish testes in the F0, F1, and F2 generations. Significantly more F1 genes were differentially methylated with a much smaller number of changes in the F0 and F2 generations. Few of these DMGs correlated with differential gene expression, which could potentially be explained by the variation of gene expression changes throughout the lifetime of an organism and/or the interplay of several epigenetic processes controlling gene expression (i.e. not just DNA methylation). In support of this, a number of histone modification genes were both differentially methylated and expressed in all generations, but particularly in the F1. Many DMGs overlapped between multiple generations, providing further evidence of male-mediated inheritance of DNA methylation patterns. In addition, several DMGs in all generations were involved in reproductive pathways, like those found in response to TCDD exposure (decreased fertility, defects in spermatogenesis, and skewed sex ratios). Collectively, our results suggest that DNA methylation is one mechanism of male-mediated transgenerational reproductive effects of TCDD exposure in zebrafish, but these effects are likely inherited through integration of multiple epigenetic pathways.

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