Introduction

As time passes and human needs evolve, there is a demand for the modernization of industries. This causes high production rates of various chemicals. Some of these chemicals may have harmful effects on the body of both humans and animals. One such class of chemicals is known as endocrine-disrupting chemicals (EDCs). They are a heterogeneous group of molecules that are of both synthetic and natural origin and possess the ability to mimic or antagonize natural hormones and can interact with hormone receptors (Yilmaz et al. 2020).

Among various types of EDCs, the most abundantly available chemical is bisphenol A (BPA). It is a white, crystalline solid compound of synthetic nature, which serves as a precursor to polycarbonates, polyesters, polysulfones, polyether ketones, and a major class of epoxy resins (vinyl ester resins). Due to its properties, it has been classified as a plasticizer. Hence, it has an extensive range of applications and is commonly found in baby bottles, metal-based food, beverage can linings, ophthalmic lenses, medical and dental supplies, electronics and electric appliances, water pipes, and carbonless receipt (Yilmaz et al. 2020). Since BPA is small in structure and is lipophilic in nature, it gives it the ability to cross cellular barriers and bio-accumulate in adipose tissues of most animals and humans, thereby accommodating its participation in various reactions that take place in the body (Rutkowska and Rachoń 2014).

BPA has been identified as a xenoestrogen, because of its ability to disturb the functioning of the endocrine system by mimicking the behavior of the natural estrogen, 17-β estradiol (Iso et al. 2006). Its activity was defined towards classical nuclear ERα and ERβ receptors, their expression, interactions, and effect on steroidogenesis. Due to such disruptions, the subsequent effects observed are in the growth of ovarian follicles, enlarged prostate, increased bodyweight, alterations in testosterone excretion, and sperm quality (Melzer et al. 2011; Richter et al. 2007).

BPA is observed to show moderately acute toxicity in animals, especially mammals. It has been reported to show effects on the functioning of other hormones like androgens, insulin, prolactin, and thyroid hormone (Wetherill et al. 2007; Renaud et al. 2019). The most common pathological effects observed in laboratory studies with and peer-reviewed human studies are obesity, cardiovascular diseases, hyperinsulinemia, thyroid, hypertension, ovarian and testicular developmental issues, polycystic ovarian syndrome (PCOS), and cancer (Michałowicz 2014). BPA tends to affect various pathways like the insulin pathway, glucose pathway, lipid metabolism, protein metabolism, and ovarian steroidogenesis, thereby having the potential to cause metabolic-endocrine disorders like PCOS in premenopausal women. PCOS is an extremely prevalent metabolic endocrine disorder in premenopausal women, displaying a broad spectrum of clinical manifestations and subsequent associative morbidities (Belenkaia et al. 2019). It is a heterogeneous disorder that is characterized by a combination of symptoms and manifestations of excess androgen in the form of hyperandrogenism and/or hirsutism, ovarian dysfunction both morphological and endocrinal, and menstrual irregularities observed as the number of cycles per year or the length of each cycle.

The worldwide prevalence of PCOS is estimated to range from 4 to 12% (Meier 2018) making it one of the most common endocrine-metabolic disorders in women during their reproductive age. Despite this, PCOS continues to be one of the poorly understood medical disorders among, patients, practitioners, pharmaceuticals, and even the research community (Escobar-Morreale 2018). Over the decades, research on PCOS has suggested that it is multifaceted in nature and there are various factors like genetic (gene interactions and effect of environment on gene expression), epigenetic (modifications and alterations), endocrine, metabolic, environmental factors, and lifestyle that influence the onset of PCOS in women (Prabhu et al. 2021).

Human interaction with BPA

Exposure in humans can be classified into two broad categories, environmental exposure and intake from food. The possible routes of exposure are ingestion, inhalation, and dermal uptake in humans. Environmental exposure is due to various factors such as BPA leaching into the atmosphere or water bodies by industrial activities, dumping of waste in landfills, and many more. Whereas the exposure due to intake of food is related to the interaction of plants and animals with BPA, the consequent bioaccumulation, and the contact of food with packaging materials (Kang et al. 2006). Unlike most EDCs, BPA has a short half-life of 6 h and has the ability to get eliminated as BPA-glucuronide due to enzyme activity under normal conditions. Yet, it is considered to be persistent because of its widespread application and continuous exposure of the population to it (Encarnação et al. 2019). Therefore, to set a safety level of exposure to humans, the US Environmental Protection Agency (EPA) and the National Toxicology Program (NTP) convened a committee to study the various biological effects that occur due to typical human exposure. After various experimental studies, the levels reported are as follows, the no-observed-adverse-effects level (NOAEL) is 5.0 mg/kg body-weight/day and the low-observed-adverse-effects level (LOAEL) is observed to be at 50 mg/kg body-weight/day. Therefore, consequently, the tolerable daily intake (TDI) of BPA was reported to be 4 µg/kg body-weight/day (Hong and Yang 2017).

Metabolism and toxicity of BPA

The primary organ responsible for the metabolism of BPA in humans is the liver. In the liver, phase II conjugation of BPA results in the transformation to mainly BPA-glucuronide (BPA-G) and small amounts of BPA-sulfate (BPA-S) conjugates (Fan et al. 2017). Uridine-5-diphospho-glucuronosyltransferases (UGTs) are the important class of enzymes involved in the catalysis of BPA glucuronidation that results in the transformation of BPA to BPA-G, and the main enzymes involved in the process are believed to be hepatic UGT2B15 and UGT1A9 (Hanioka et al. 2008). Furthermore, BPA is reported to be majorly excreted in the urine as glucuronide (94.6%) (Provencher et al. 2014). The abnormalities in the functioning of UGTs enzyme cause the increase in levels of unconjugated BPA concentration in the system (Khan et al. 2021). Alongside, its ability to mimic the behavior of 17-β estradiol (Iso et al. 2006) results in the disruption of various pathways, causing moderately acute toxicity in humans. The most common pathological effects observed in laboratory studies with, and peer-reviewed human studies are obesity, cardiovascular diseases, hyperinsulinemia, thyroid, hypertension, ovarian and testicular developmental issues, PCOS, and cancer (Michałowicz 2014) (Fig. 1).

Fig. 1
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Human exposure to BPA and its consequent metabolism

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This review attempts to correlate the alteration in expression of various genes targeted by BPA and endocrine function in the pathophysiology of PCOS. It focuses on gene expression and endocrinal regulation in animal models and in vitro cultures of human cell lines, because of the limitations like uncontrolled exposure, the impact of various other lifestyle factors, and the ethical constraint observed in human studies.

Search strategies

The search was conducted using PubMed as an electronic database. Studies were identified using the combination of the following search terms: “bisphenol A” AND “gene expression” OR “mRNA expression” OR “altered expression” OR “polycystic ovarian syndrome” OR “female reproductive system” OR “Insulin resistance” OR “Hyperandrogenism” OR “Ovulatory dysfunction” OR “estrous cyclicity” OR “Chronic inflammation” OR “steroidogenic hormones” OR “gonadotropins” OR “female sex hormones.” All the data from both animal and in vitro studies on the relationship among BPA and the different aspects of the female reproductive and endocrine system, along with the clinical manifestation of PCOS were considered for inclusion. Furthermore, the information regarding mRNA expression, alteration of steroid hormone levels, BPA exposure, and PCOS were discussed in the review.

Gene expression studies

BPA has been observed to target and alter the gene expression of several important genes associated with PCOS, and their corresponding protein level dysregulation supports the observation (Table 1). Many observational studies have researched the alteration in gene expression by evaluating the levels of their transcribed mRNA, in various aspects like the disruption of the hypothalamic-pituitary-ovary (HPO) axis, disruption of steroidogenic and metabolic pathways and their results can be associated with the pathophysiology and manifestations of PCOS (Table 2).

Table 1 List of genes targeted by BPA in the female reproductive system
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Table 2 Alteration in gene expression on BPA exposure
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Gonadotropin dysregulation

In female animals, the estrous cycle and in female humans the menstrual cycle is regulated by the interaction between hormones released by the hypothalamus, pituitary, and ovaries, thereby forming the HPO-axis. The pulsatile release of gonadotrophin-releasing hormone (GnRH) from the hypothalamus, prompts the release of luteinizing hormone (LH) and follicle-stimulating hormone (FSH) from the anterior segment of the pituitary. These gonadotrophs in the ovarian level, act on ovarian follicles to release progesterone (P) and estrogen (E). Estradiol (E2) is one of three estrogens produced, that regulates the release of LH and GnRH by a negative feedback action (Adachi et al. 2007) on binding with estrogen receptor α (ER α) exhibited by kisspeptin neurons in the arcuate nucleus (ARC) and anteroventral periventricular nucleus (AVPV) (Kinoshita et al. 2005). E2 decreases the expression of KISS1 mRNA in ARC and increases KISS1 mRNA in AVPA, resulting in negative and positive feedback respectively (Dungan et al. 2006). As BPA possesses the ability to mimic the action of E2, it can bind to ER α (Fang et al. 2000), and thereby disrupt the functioning of the hypothalamus and pituitary gland. Also, the expression of genes like KISS1, GNRH, LHB, and FSHB has been subjected to alteration, as observed in various animal and in vitro studies when exposed to BPA.

The effects of BPA highly depend on the time of exposure, its duration, and dosage, hence having varying impacts on the result as observed in various studies. The dose-dependent exposure of mouse embryonic hypothalamic cells to BPA for 3 h, displayed significantly reduced expression of Gnrh1 at 200μM when compared with control and other lower doses. The results suggested that Gnrh1 expression in the cells was unresponsive to treatment below 200μM and its downregulation at high dose exposure results in disruption of maturation of the HPO-axis (Warita et al. 2013). The downregulation of the gene allows the hypothesis that high dose exposure to BPA incapacitates female rats from producing normal LH surges as seen in Wistar rats (Monje et al. 2010), since the gene codes for GnRH which stimulates the secretion of gonadotropins like LH and FSH from the pituitary gland.

On the other hand, neonatal exposure to BPA in female Sprague Dawley rats is seen to cause an upregulation of KISS1 and GNRH1 genes. Kisspeptin regulates the surge in gonadotropin levels during the initiation of female puberty and its activation by the neonatal BPA exposure shows that it can affect pubertal development (Qiu et al. 2020). This observation is also seen in a study conducted by Xi et al. (2011) on CD-1 mice, perinatal exposure to BPA causes upregulation of KISS1 mRNA and GNRH mRNA in adults, which in turn causes alteration in the gene expression of gonadotropins (FSHB, LHB) and their receptors (FSHR, LHCGR). As the feedback system is disturbed, these changes in the hypothalamus and pituitary can be both the cause and the consequence of the altered HPO-axis functioning.

The upregulation of ESR1 (Wang et al. 2014) and ESR2 (Xi et al. 2011; Wang et al. 2014) mRNA in the pituitary exhibit a molecular basis of the selective action of BPA on the AVPV-kisspeptin neuron, which causes further upregulation of GNRH as observed in a study on ICR mice when exposed to 20 μg/kg body weight per day of BPA (Wang et al. 2014). The dose-dependent alteration in expression of GnRH is not only observed in mammals but also in teleost (Qin et al. 2012).

Disrupted ovarian steroidogenesis and hyperandrogenism

Ovarian steroidogenesis is a culmination of the interaction between LH, FSH, and enzymes like p450scc, p450c17, and aromatase. Androgen formation in ovarian theca cells is stimulated by LH and in granulosa cells, and biosynthesis of E2 from androgens is stimulated by FSH. StAR protein regulates the transfer of cholesterol into granulosa cells so that p450scc can convert it to pregnanolone, which is then converted to progesterone by HSD-3 β and simultaneously to androstenedione by the 17,20-lyase activity of p450c17; furthermore, progesterone also gets converted to androstenedione in the theca cells. This androstenedione gets converted to estrone by aromatase and further to E2 by the activity of HSD-17 β in granulosa cells (Hannon and Flaws 2015). The dysregulation of gene expression caused by BPA exposure, at the hypothalamus and pituitary level impacts the functioning of the ovary. The upregulation of FSHB, LHB (Xi et al. 2011) FSHR, and LHCGR (Xi et al. 2011; Faheem et al. 2017) genes on high-dose BPA exposure and its consequent increase in stimulation of the ovarian follicles positively correlate it with the altered expression of genes coding for enzymes that participate in the conversion of androgens to E2 (Xi et al. 2011).

A study conducted by Zhou et al. (2008) on Sprague Dawley rats treated with varying doses of BPA exhibited upregulation of StAR, CYP11A1, and CYP17A1 in ovarian T-1 cells. At a 10–4 M dose of BPA, the increased expression of StAR and CYP11A1 may promote the production of more progesterone which paired with the upregulation of CYP17A1 at 10–5 M results in increased production of androgens. The sudden downregulation of CYP17A1 at 10−4 M is assumed to be the result of cytotoxicity of granulosa cells from continuous testing (Zhou et al. 2008). The downregulation of CYP19A1 suggests that there is a decrease in the conversion of androgen to E2, on exposure to BPA (Xi et al. 2011; Chu et al. 2018; Watanabe et al. 2012). On exposure to BPA, the upregulation of HSD3B1 (Wang et al. 2014; Samardzija et al. 2018) and downregulation of HSD17B gene (Shi et al. 2021) further consolidate the chances of increased androgen levels, as there is a possible increase in conversion of progesterone to androgens and androstenedione to E2, respectively.

Furthermore, BPA exposure has also been observed to upregulate the genes encoding orphan nuclear receptors like estrogen-related receptor-γ (ESRR-γ) (Arase et al. 2011), thereby suggesting that BPA can participate in an orphan nuclear receptor-mediated alteration of the expression of steroidogenic enzymes in the ovary (Xi et al. 2011). The contradicting and differing results of alteration in gene expression could be credited to the difference in cell types and organisms under study, their dosage, and time of dosage. The disruption caused by BPA in the expression of genes participating in ovarian steroidogenesis could cause hyperandrogenism and ovulatory dysfunction (Rutkowska and Rachoń 2014).

Ovarian folliculogenesis disruption

The dysregulation of gonadotropin secretion and its consequent disruption of the HPO-axis contribute to ovarian follicular arrest and major changes in the morphology and functioning of the ovary. The upregulation of LHB (Xi et al. 2011) may contribute to the hypertrophy of ovarian follicles thereby leading to their premature luteinization (Azziz et al. 2016). It is observed that on pre-pubertal exposure to high doses of BPA, the expression of AMH increases in ovarian granulosa cells. The upregulation of AMH can be contributed to the effect of BPA in increased numbers of small antral follicles in comparison to the overall numbers of follicles present in the ovary (Li et al. 2014). This could lead to a decrease in FSH sensitivity, which could further impair follicular growth (Gruijters et al. 2003).

Whereas exposure to low doses of BPA shows downregulation of the AMH gene, this result is hypothesized to be caused by the effect of BPA on the reduction of granulosa cell activity and its subsequent accelerated apoptosis (Cao et al. 2018). Another possible factor could be the downregulation of IGF1, IGF2, and IGF1R genes on perinatal BPA exposure, which tends to result in the lack of development of ovarian cells and suppresses growth in general (Aluru et al. 2010).

Adipose tissue dysfunction, insulin resistance, and chronic inflammation

Adipose tissue acts not only as a fat storage reservoir that participates in homeostasis but also as an endocrine organ that secretes regulatory adipokines, cytokines, and chemokines. BPA is known to disrupt various metabolic pathways such as lipid metabolism, carbohydrate metabolism, insulin signaling pathway, and cause adipose tissue inflammation. A study conducted by Ariemma et al. (2016) observed the various effects of prolonged low dose exposure of BPA on adipocyte differentiation. BPA exposure tends to increase pre-adipocyte growth by upregulation of PPARG, AdipoQ, and LEP genes that regulate adipogenesis and paired with the proinflammatory action of BPA; this exacerbates insulin sensitivity in adipocytes and hampers the insulin signaling pathway (Ariemma et al. 2016). It is observed that the regulation of glucose level on BPA exposure compensates for the upregulation of the INS1 gene (Haq et al. 2020). On exposure to BPA, the upregulation of LEP (Ariemma et al. 2016; Cimmino et al. 2019) in cultures of adipocytes displays a possibility of an increase in fat storage, thereby drawing a correlation between BPA exposure and obesity.

Furthermore, the dose-dependent downregulation of AdipoQ mRNA in in vitro cultures of adipocytes (Cimmino et al. 2019; Menale et al. 2017; Ahmed et al. 2020) suggests the dysregulation in the breakdown of fatty acids and desensitization of cells to insulin. This combined with the upregulation of RETN (Menale et al. 2017) inhibits insulin action and presents a possible link between BPA exposure causing obesity and insulin resistance. As adipose tissue insulin resistance is intricately linked to increased inflammation, the alteration in expression of inflammatory cytokines such as IL6 (Ariemma et al. 2016; Cimmino et al. 2019; Ahmed et al. 2020), IFNG (Ariemma et al. 2016; Miao et al. 2008), TNFA (Miao et al. 2008) that are adipose-derived confirms the effect of BPA exposure leading to chronic inflammation in adipocytes may cause insulin resistance.

Hormonal changes caused by BPA

The alteration in the expression of hormone-coding genes and enzymes brings about biochemical changes in hormone and enzyme levels. Since BPA can have post-translational effects on the expression of proteins, it is important to corroborate the results of gene expression with protein expression (Table 3).

Table 3 Hormone level alterations observed in animal models
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The study conducted by Zhou et al. (2008) on female Sprague Dawley rats showed elevated levels of testosterone and progesterone, along with reduced levels of estradiol. The levels are a result of the altered gene expression of steroidogenic enzymes—StAR, p450scc, p450c17, and aromatase in the ovary on BPA exposure (Zhou et al. 2008). This supports the hypothesis that BPA exposure can cause hyperandrogenism. As the increased androgen levels activate a pro-inflammatory condition, there is a development of a pro-oxidant state in the ovaries; this, in turn, accelerates cellular apoptosis. And the hampered cellular activity due to repeated exposure of granulosa cells to low doses of BPA causes a decrease in Anti-Mullerian hormone (AMH) and estradiol levels in ovarian follicles. This could in turn lead to a decrease in ovarian reserve as it hampers the number of raised follicles and the quality of mature oocytes (Cao et al. 2018). However, the effect of BPA on the expression of AMH has been observed to vary with the stage of development. In the pre-pubertal period, increased levels of AMH and decreased number of corpus luteum result in a significant decrease in serum levels of P4, displaying a disruption in follicular development (Li et al. 2014).

The dysregulated functioning of the HPO-axis plays a major role in the underlying mechanism of altered hormone levels and ovarian morphology. The increased GnRH pulsatility and reduced GnRH-induced LH levels (Fernández et al. 2009) on high-dose BPA exposure further result in the alteration of sex hormone levels where serum Testosterone (T) and E2 levels are increased, and P levels are decreased (Fernández et al. 2010). This correlates the effects of BPA exposure to the altered hypothalamic-pituitary functioning as observed in PCOS.

A study conducted by Gámez et al. (2015) observes increased LH and E2 levels; this contradicts the previous results, and this can be attributed to the difference in BPA dosage and the time of exposure. Other than hyperandrogenism, BPA too has been observed to have the potential to induce oxidative stress that may affect the alteration in hormone levels (increase in T; decrease in E2, P, LH, and FSH) because of the impaired HPO-axis functioning and altered histopathology of the ovary (Ijaz et al. 2020).

Ovarian morphological changes caused by BPA

As discussed in the previous sections, BPA has a mild estrogenic activity similar to E2 and possesses the ability to disrupt the HPO-axis. This disruption causes clinical manifestations in the form of hormonal imbalance and subsequent alteration in ovarian morphology. Various studies that focus on this aspect are summarized in Table 4.

Table 4 Ovarian morphological changes observed in animal models
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A dose-dependent decrease in oocytes is observed with an increase in the dose of BPA exposure because of oocyte apoptosis (Fernández et al. 2010). This in turn shows lowered development of primordial follicles on exposure to high doses of BPA (Zhu et al. 2018). On BPA exposure the alteration in expression of ESR1 and ESR2 in ovarian follicles causes an increase in follicular recruitment (Rodríguez et al. 2010), thereby resulting in the observation of increased numbers of preovulatory follicles (Fernández et al. 2010; Ijaz et al. 2020), primary follicles (Gámez et al. 2015), and secondary follicles (Gámez et al. 2015). It has been observed that BPA alters follicular growth and induces atresia, thereby leading to observations of increased atretic follicles (Fernández et al. 2010; Gámez et al. 2015; Ijaz et al. 2020) on exposure to high doses. This in turn leads to decreased number of antral follicles (Fernández et al. 2010; Gámez et al. 2015; Ijaz et al. 2020; Zhu et al. 2018), hence increasing rates of follicular arrest that leads to anovulation (Rutkowska and Rachoń 2014). As the BPA-exposed animals exhibit reduced LH secretion because of the irregular GnRH pulsatility (Fernández et al. 2009), its ability to cause cell enlargement and production of P may decrease (Azziz et al. 2016), and this paired with low numbers of antral follicles that may mature leads to a significant decrease in the number of corpus luteum observed (Fernández et al. 2010; Ijaz et al. 2020; Zhu et al. 2018; Adewale et al. 2009).

A study conducted by Qiu et al. (2020) observes normal ovarian morphology and follicular development, in adult rats that were neonatally exposed to BPA. Since the time of exposure plays a huge role in the development of effects, this could contribute to the difference in results (Qiu et al. 2020).

Effect of BPA on PCOS

The effect of BPA on pathways like insulin signaling, lipid metabolism, ovarian steroidogenesis, and the functioning of the HPO-axis is well observed in animal models and in vitro human cell line studies. The results obtained can be correlated with the findings in various human epidemiology studies. These studies focus on the relationship between BPA and the factors crucial in the clinical manifestation and pathogenesis of PCOS, by establishing a correlation between the presence of BPA and the altered levels of hormone levels in PCOS patients.

BPA has been observed to cause disruptions in several metabolic pathways and functioning of the endocrine system, thereby giving rise to PCOS in premenopausal women. Since BPA mimics the activity of 17-β estradiol, it has been reported to possess the ability to disrupt steroid feedbacks at the hypothalamus-pituitary level and steroid action at the ovarian level, thereby suppressing HPO-axis functions (Wang et al. 2017). This includes hypersecretion of circulating LH and increased levels of FSH, causing alteration of LH:FSH ratios (Vahedi et al. 2016).

In addition, BPA contributes to the disarrayed metabolic profile in PCOS due to the involvement of BPA in insulin resistance (Kandaraki et al. 2011) and its promotion of inflammatory conditions through the development of obesity and infiltration of macrophages into the adipose tissue (Tarantino et al. 2013). Chronic inflammation aids the development of insulin resistance, and the subsequent compensatory hyperinsulinemia indirectly leads to increased amplitude and frequency of GnRH and LH pulse secretion observed in PCOS. This increase also induces relative resistance of follicles to FSH and subsequent increase in production of AMH, promoting a decrease in antral follicle count thereby plausibly impairing the ovarian reserve (Zhou et al. 2017). Furthermore, BPA exposure causes attenuation of aromatase expression in the follicular fluid causing dysregulation in estrogen production (Wang et al. 2017). This paired with the potential of BPA to increase androgen levels due to its inhibitory effect on the action of testosterone-hydroxylase (Takeuchi et al. 2006) has the ability to cause hyperandrogenism (Jurewicz et al. 2021).

Moreover, a prospective observational study conducted by Déchaud et al. (1999) suggests that an increase in free testosterone levels in the serum is because of the ability of BPA to displace sex steroid hormones from SHBG. In association with these findings, it appears that in PCOS the metabolism and excretion of BPA are impaired due to the effect of hyperandrogenism in blocking the expression of uridine diphosphate-glucuronosyl transferase (UGTs) that completely metabolizes BPA (Vermeulen 1993). The resulting effects are well studied by Takeuchi et al. (2004) in a case-controlled study that indicates increased BPA levels in women diagnosed with PCOS. Despite BPA having a short half-life, it has an inhibitory effect on the activity of UGT, which causes BPA to remain incompletely metabolized thereby increasing its levels in the body. This causes an alteration in gene expression that disturbs various endocrinal processes like gonadotropin secretion and receptivity, ovarian steroidogenesis, insulin activity, and regulation of adipokines, which in turn causes demonstration of clinical manifestations like ovulatory dysfunction, disrupted folliculogenesis, polycystic ovarian morphology, hyperandrogenism, hyperinsulinemia, obesity that are associated with PCOS (Fig. 2).

Fig. 2
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The effect of BPA on the expression of certain genes involved in the PCOS pathogenesis

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All these results compiled suggest that the presence of BPA in women with PCOS could be both a cause and consequence of disrupted hormonal patterns and metabolic activity that result in clinical manifestations like hyperandrogenism, ovulatory dysfunction observed as the length of the menstrual cycle and duration of bleeding (Rashidi et al. 2017) and altered ovarian morphology.

Conclusion

Since the studies on gene expression in BPA-induced PCOS models are relatively limited, this review encapsulates the effect of BPA on the expression of 28 genes that take part in various metabolic and endocrinal pathways, whose disruption may play a major role in the pathogenesis of PCOS.