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Review

Bisphenols as Environmental Triggers of Thyroid Dysfunction: Clues and Evidence

Institute of Clinical Physiology, National Research Council, 56124 Pisa, Italy
*
Author to whom correspondence should be addressed.
These authors equally contributed to the manuscript.
Int. J. Environ. Res. Public Health 2020, 17(8), 2654; https://doi.org/10.3390/ijerph17082654
Received: 23 March 2020 / Revised: 9 April 2020 / Accepted: 10 April 2020 / Published: 13 April 2020
(This article belongs to the Special Issue Environmental Pollution and Thyroid)

Abstract

Bisphenols (BPs), and especially bisphenol A (BPA), are known endocrine disruptors (EDCs), capable of interfering with estrogen and androgen activities, as well as being suspected of other health outcomes. Given the crucial role of thyroid hormones and the increasing incidence of thyroid carcinoma in the last few decades, this review analyzes the effects of BPS on the thyroid, considering original research in vitro, in vivo, and in humans published from January 2000 to October 2019. Both in vitro and in vivo studies reported the ability of BPs to disrupt thyroid function through multiple mechanisms. The antagonism with thyroid receptors (TRs), which affects TR-mediated transcriptional activity, the direct action of BPs on gene expression at the thyroid and the pituitary level, the competitive binding with thyroid transport proteins, and the induction of toxicity in several cell lines are likely the main mechanisms leading to thyroid dysfunction. In humans, results are more contradictory, though some evidence suggests the potential of BPs in increasing the risk of thyroid nodules. A standardized methodology in toxicological studies and prospective epidemiological studies with individual exposure assessments are warranted to evaluate the pathophysiology resulting in the damage and to establish the temporal relationship between markers of exposure and long-term effects.
Keywords: Bisphenol A; bisphenols; endocrine disruptors; thyroid hormones; thyroid cancer Bisphenol A; bisphenols; endocrine disruptors; thyroid hormones; thyroid cancer

1. Introduction

Thyroid hormones (THs) play a critical role in the regulation of physical development, somatic growth, metabolism, and energy provision and are essential for normal brain development in humans [1]. Thus, any interference with THs status and signaling during development may have an impact on physical health, and can be associated with neurological deficits and even irreversible mental retardation in the case of severe maternal TH deficiency [2]. Meanwhile, thyroid cancer (TC) incidence rates have been rising in many western countries, including the United States where the incidence increased 3.6% per year during 1974 to 2013 [3]. TC is the most common endocrine malignancy, and by 2030, it is estimated to become the fourth leading cancer diagnosis in the United States [4]. Papillary thyroid cancer (PTC), in particular, is the most frequent histotype with a typically excellent prognosis, accounting for 70% to 90% of well-differentiated thyroid malignancies, and though over diagnosis of small tumors is thought to contribute significantly to the increase in incidence, PTC incidence has significantly increased for every stage and tumor size category [3]. The etiology of TC is multifactorial and the proposed risk factors in the literature include sex, family history of TC, radiation exposure, excess weight, iodine intake, and dietary habits [5]. Although the thyroid is characterized by a low proliferation index, it is particularly susceptible to environmental chemicals that may contribute to the increasing incidence of TC [6].
According to a recent statement by the Endocrine Society, endocrine disrupting chemicals (EDCs) are defined as single exogenous agents or mixture of compounds capable of interfering with any aspect of hormone action, from the synthesis to the transport, catabolism, and elimination of the hormones produced [1,7]. One of the characteristics of many EDCs is a nonmonotonic dose response that replicates hormone characteristics; thus, a proportionally greater effect is observed at low doses than at high doses because of hormone receptor saturation and overstimulation that decrease the response [7,8]. Increasing evidence has shown the ability of several EDCs (e.g., polybrominated diphenyl ethers, polychlorinated biphenyls, pesticides, and phthalates) to exhibit thyroid disrupting activities in animals and, with some inconsistencies, in humans [1,9]. Interference of environmental chemicals with thyroid function can occur at multiple levels including, among others, toxicity at the thyroid gland, disturbance of THs synthesis, secretion and metabolism, competitive binding with the TH binding proteins, and interaction with thyroid hormone receptors (TRs) [1,10].
Bisphenol A (BPA; 2,2-bis(4-hydroxyphenyl)propane) is described as an EDC able to interact with human estrogen receptors (ERs) [11]. In rodent models, a variety of effects was observed in estrogen-target organs (e.g., brain, mammary gland, ovary, and uterus) following exposure to BPA at or below the lowest observed adverse effect level (LOAEL) during prenatal and neonatal periods [12]. Changes in one of the target organs can lead to secondary alterations in bone, adipose tissue, cardiovascular tissue, and the immune system [13]. In humans, increased levels of BPA were associated with adverse health outcomes including cancer [14,15], reproductive disorders [16], altered neurobehavior [17], cardiovascular disease [18], type 2 diabetes [19], and obesity [20]. In addition, BPA acts as an antiandrogen, affecting steps of the activation and function of the androgen receptor [21] and spermatogenesis in both animals [22] and humans [23].
Though not systematic, the present effort is a thorough review (173 references included in the full text), comprising in vitro, in vivo, and epidemiological studies that have assessed the effects of bisphenols (BPs), namely bisphenol A (BPA), its analogues, and its halogenated derivatives on the thyroid, considering their actions at different levels in cells or organs, in different animal models and in humans and their potential to exert a risk in causing a direct impact on the gland. Original studies published in English in peer-reviewed journals from 1 January 2000 to 31 October 2019 were searched in Pubmed through the search strategy: ((bisphenol* OR BPA OR tetrabromobisphenol* OR TBBP* OR tetrachlorobisphenol OR TCBPA) [ALL FIELDS]) AND (thyroid OR thyroid disorders OR thyroid function OR thyroid cancer OR thyroid nodule [ALL FIELDS]). From the initial search of 303 records, a total of 82 studies were selected by two authors on the basis of adherence to the purposes mentioned above.

2. Bisphenols in the Environment and Humans

BPA is a monomer in the manufacture of polycarbonate plastics and epoxy resins widely used in diverse consumer products such as food and liquid containers, protective coatings inside metallic food and beverage cans and medical devices, as well as in flame retardants and thermal papers [24]. It is one of the 2000 endocrine disruptors known as “highest volume” chemicals, with an annual production of at least 8 million tons throughout the world [25].
BPA can be released from both effluent discharge of manufacturing plants and from transport, processing, and disposal of waste of BPA-containing products in landfills and incinerators [26]. Less than 1% of environmental BPA has been estimated to occur in the atmosphere, where it undergoes photo-oxidation and breakdown [27]. Nonetheless, the presence of BPA in the environment, though at low levels and despite the short half-life, is ubiquitous [28].
Due to its lipophilicity, detectable levels of the unconjugated form of BPA were measured in adipose tissue, brain, liver, and breast milk in humans (Table 1a). Moreover, BPA can pass through the placenta and amniotic fluid thereby exposing the fetus, as well as the developing infant, to exposure and accumulation [29] (Table 1a).
The first safety standard for humans set by the US-Environmental Protection Agency in 1988, adopted by the Food and Drug Administration as the reference dose and based on the LOAEL for BPA, was 50 micrograms per kilogram of body weight per day [30]. In 2013, the re-evaluation of BPA exposure and toxicity led the European Food Safety Authority to considerably reduce the safe level of BPA from 50 to 4 µg/kg/day (31). Human exposure to BPA is continuous and widespread, and diet is likely the major source of exposure in all population groups because of the ability of BPA to migrate from polycarbonate containers and metallic cans to food and beverages [31]. In 2011, the European Union banned the manufacture of baby bottles containing BPA [32], followed in 2012 by the Food and Drug Administration [33]. Infants and toddlers exhibit the highest estimated external average exposure because of their elevated consumption of food and beverages per kg of body weight [31] (Table 1a). Other routes of exposure are represented by inhalation of outdoor and indoor air, ingestion of domestic dust, dermal contact with thermal paper and cosmetics, and, for children, mouthing of toys [31]. The estimates for exposure to dietary and non-dietary sources are at least one order lower than the tolerable daily intake set by the European Food Safety Authority, except daily intake of infants fed with canned liquid formula in polycarbonate bottles (Table 1a).
BPA has a half-life in humans of about 6 h [34]. Following the oral exposure, in humans BPA is absorbed from the gastrointestinal tract and then metabolized in the liver, where is primarily conjugated with glucuronic acid to the non-active BPA-glucuronide, which is the main metabolite in urine and blood [34]. Urinary total BPA (conjugated + free), considered the most appropriate biomarker to assess human exposure [35], was detected among the different age classes in 88% to 98% of volunteers who participated in the National Health and Nutrition Examination Survey [35]. Significantly higher concentrations have been detected in children than in adolescents and adults whereas BPA levels measured in the blood of adults are approximately one order of magnitude lower than those found in the corresponding urine [36] (Table 1a).
Several structural analogues were introduced in the market to replace BPA [37]. Bisphenol F (BPF; 4,4′-dihydroxydiphenylmethane), bisphenol S (BPS; 4,4′-sulfonyldiphenol), and bisphenol Z (BPZ; 1,1-bis(4-hydroxyphenyl)-cyclohexane) are used in epoxy resin products [38], in cleaning products and thermal paper [39], and in highly heat resistant plastic materials and electrical insulation [40], respectively. BPAF (1,1,1,3,3,3-hexafluoro-2,2-bis(4-hydroxyphenyl)propane) is a fluorinated derivative widely used in the manufacturing of polycarbonate copolymers with 10,000 to 500,000 pounds annually produced in the United States [41]. BPA substitutes have been detected in various environmental matrices, and, with a few exceptions, their concentration values in urine are lower than those of BPA [42] (Table 1b).
Tetrabromobisphenol A (TBBPA), a persistent compound synthesized by bromination of BPA initially replaced polybrominated diphenylthers, at present is the most widely employed brominated flame retardant, with a reported 2011 volume of 120 million pounds in the United States [43]. In the last years, tetrabromobisphenol S (TBBPS) and tetrachlorobisphenol A (TCBPA) have been extensively used as alternatives to TBBPA [44]. TBBPA is measured in the environment and in human body [45], and TBBPA exposure represents a significant health risk especially for children residing in an e-waste processing region [46] (Table 1c).

3. Thyroid Disrupting Properties of BPs: in Vitro Studies

Biological function of thyroid hormone triiodothyronine (T3) is generally mediated by the nuclear receptors TRα1, TRβ1, and TRβ2 that are conserved in all vertebrates. T3 binds to the TRs with similar affinities mediating TH-regulated transcription with different levels in different tissues [60]. TRα1 is the predominant subtype in cardiac muscle and bone, TRβ1 is the predominant subtype in kidney and liver, while TRβ2 is more abundantly expressed in the hypothalamus and in the pituitary gland, and has a critical role in the regulation of the hypothalamic–pituitary–thyroid (HPT) axis [61]. TRs bind at DNA as homodimers or forms heterodimers with the retinoid X receptor to T3 response elements and they can regulate transcription both in the absence and in the presence of ligands [62]. On positively regulated genes, the unliganded TRs bind to corepressor proteins such as the silencing mediator of retinoid and thyroid hormone receptor (SMRT) or the nuclear receptor corepressor (N-CoR), resulting in the suppression of transcription [63]. The binding of T3 to TRs leads to a dissociation of the corepressors, and the subsequent recruitment of coactivator proteins, such as those of the p160/SRC (steroid receptor coactivator) family, including SRC1, SRC2, and SRC3, thus promoting activation of transcription [63].
In vitro models have tested and verified the ability of BPs to disturb thyroid function through multiple mechanisms that may produce different consequences depending on the heterogeneity of experimental conditions among studies such as the chemical tested, the concentrations used, and the presence/absence of T3 or T3 antagonists. BPs were reported to exert numerous effects on the thyroid, and each affected pathway may lead to perturbations of thyroid hormone levels, leading to a dysregulation of thyroid function. The pathways are not necessarily inter-connected, but there is some evidence that BPs may lead to an impact on the gland and its function at multiple levels, as reported in the following paragraphs.

3.1. Interference with T3 Transcriptional Activity

Numerous studies have evaluated the ability of BPs to suppress hormonal transcriptional activities mediated by TRα1 and TRβ1 in competitive binding and transient expression assays (Table 2).
BPs mainly acts as TR antagonists, inhibiting crucial processes related to development [64,65,66,67]. The TH signaling interference can occur by a direct binding of BPs to the receptor due to the high degree of structural similarity with THs (Figure 1) and preventing the binding of T3 [10,68,69,70,71]. Inhibitory effects of BPs on T3 hormonal activity were reported in different cell lines at doses of 106–10−4 M [2,10,64,65,69,72,73,74], with brominated bisphenols showing a much stronger anti-TH activity than BPA and BPS [68].
Whereas BPA alone did not induce visible effects on T3-induced transcription [2,73,75,76], in the presence of physiological concentrations of T3, low-dose BPA enhanced the interaction of TR with N-CoR by directly binding to TR [2].
BPA may exert disrupting effects on TH-mediated transcription interfering with a different non-genomic mechanism mediated by integrin αvβ3, a heterodimeric transmembrane glycoprotein [77]. In normal conditions, T3 and thyroxine (T4) induce serine phosphorylation of TR-β1 by binding to αvβ3 and activating mitogen-activated protein kinases (MAPK) and/or c-Src/PI3K pathways [78], which determines the dissociation of N-CoR or SMRT from TR-β1 and consequent activation of transcription. The competitive binding of BPA to αvβ3 antagonizes the serine phosphorylation of TR-β1 leading to the recruitment of N-CoR/SMRT to TR-β1 and suppression of transcription [79].
A few studies observed that, in the absence of T3, BPs behave as TR agonists [65,69,70,72,80] and this thyromimetic effect can occur at very low concentrations (10−8–10−7 M) [69,70] and disappear at high doses (10−4 M) [65,69], showing a biphasic concentration-response relationship.

3.2. Cell Proliferation

The rat tumor pituitary cell line GH3 has been frequently employed as a standard pituitary cell model for assessing TH effects [81]. Indeed, cell proliferation and growth hormone (GH) secretion primarily depend on THs [81] and involve TR-mediated mechanisms, specifically the induction of gene expression [82].
A series of investigations assessed the agonistic and antagonistic properties of BPs in GH3 cell growth both in absence and in presence of T3 (Table 2). BPA, and in particular BPA derivatives, generally promoted GH3 cell proliferation and GH release in the concentration range of 10−6–10−4 M [70,81,83]. In some studies, the agonistic activity was detected exclusively in the presence of T3 [82,84], whereas in others BPA and its substitutes inhibited cell growth with T3, and TH-antagonistic effects appeared to depend on the tested dose and the time of exposure [80,85].
Effects of BPs on cell growth were antagonized by amiodarone, a known TR antagonist [80]. Nonetheless, amiodarone was also reported to act as a slight agonist at low concentrations and antagonist at increasing doses, and BPA and its halogenated derivatives exhibited comparable dose–response curves [76]. In PTC cells, BPA had similar proliferative effects as E2 [86], and consistent with this finding, co-exposure to E2 potentiated the increased GH3 cell proliferation (from 190% to 252% after 96 h) by BPA and BPAF [85]. In contrast, TBBPA could not counteract the inhibitory effect of fulvestrant, a strong antiestrogen, on cell growth [81].
Cell growth was further antagonized by U0126, an inhibitor of MEK, the kinase responsible for the activation of ERK in the Raf–MEK–ERK pathway in mammalian cells [87]. Similarly, TBBPA at concentrations in the lower micromolar range caused arrest of cells growth in the G1 or G2 phase, depending on the duration and intensity of the treatment and on cell specific and dose dependent modulations of the Raf–MEK–ERK pathway [87].

3.3. Cytotoxicity

MAPKs have an important role in cellular signaling pathways, and the kinases JNKs/SAPKs and p38 MAPKs are often activated by cellular stresses and thus primarily linked to cytokine biosynthesis and induction of apoptosis [88]. Thus, any interference of exogenous chemicals with kinases and phosphatases involved in cellular signaling processes can result in possible cytotoxic effects, including cell death [87].
Similar to cell proliferation, cell viability has been evaluated in cell lines exposed to BPs (Table 2).
Cytotoxicity was observed after exposure to BPA and its halogenated derivatives at a concentration range of 10−5–10−4 M; alone and/or with T3 [10,73,76,82,87]. TBBPA was found to produce cytotoxicity 100 times higher than BPA [75] although in other cell models comparable doses of BPA, TBBPA, and TCBPA did not cause changes in cell viability [65,70,89].

3.4. Competitive Binding with Thyroid Hormone Binding Proteins

One of the possible mechanisms of BPs for disrupting TH homeostasis is the competitive binding with serum transport proteins due to the structural similarity to T4 and T3. THs mainly bind to three transport proteins in human serum, namely thyroxine-binding globulin (TBG), which is responsible for 75% of the specific T4 binding activity, transthyretin (TTR), and human serum albumin [90]. A few studies tested the capability of these chemicals to compete with THs for binding to TTR, which in non-mammalian vertebrates exhibit a higher affinity for T3 than T4, whereas in human plasma is responsible for only 10% to 15% of the TH transport [91] (Table 2).
Meertz et al. [92] found no TTR binding for 17 polybrominated diphenyl ethers at maximum concentrations confirming that hydroxylation at the para position with at least one adjacent halogen substituent could represent a prerequisite for TTR binding. Indeed, TBBPA was the most potent competitor among the phenolic compounds tested, binding to TTR in a range from 1.6 [84] to 10.6-fold [92] stronger than the natural ligand T4. Moreover, the affinity of TBBPA for TTR was three times greater than that of BPA [70], and this is in line with the higher binding affinity of halogenated derivatives for TRs compared with BPA [10,71]. Actually, the hydroxylated derivatives of BPA also exhibited a strong affinity for TBG, as elucidated in a transport protein-based biosensor assay [93]. Using a fluorescent probe, Cao et al. observed that BPA affinity for TTR and TBG was weaker than T4 by 300 to 2666 fold; hence the current levels of BPA in humans are unable to interfere with T4 serum transport [90].

3.5. Perturbation of Thyroid Hormone Uptake

Thyroid hormone uptake into target cells is controlled by membrane bound transporters, such as monocarboxylate transporter (MCT) 8, MCT10, and multiple members of the Na-independent organic anion transport protein (OATP) family [94]. OATP1C1, in particular, shows a high degree of tissue selectivity, being expressed predominantly in brain and testis, and high preference for T4 and reverse T3 as the ligand [95], and it facilitates the transport of T4 across the blood–brain barrier [96]. In different species, MCT expression has been detected in numerous tissues including the brain wherein MCT8 is responsible for the neuronal uptake of T3 [95]. Mutations in the MCT8 gene cause a severe X-linked psychomotor retardation associated with highly elevated serum T3 levels and decreased T4 concentrations whereas the thyroid-stimulating hormone (TSH) values remain in the normal or slightly elevated range levels [97].
In a recent study performed in cells overexpressing the human MCT8 gene, among the several common environmental contaminants classified as flame retardants, pesticides, plasticizers, and others that are suspected to disrupt TH signaling, only BPA was observed to reduce T3 uptakes to around 60% and 40% of the control at concentrations (125 μM) below those that reduced cell viability <80% [94]. This finding is consistent with an earlier study that detected a slight inhibition of T3 transport capabilities of MCT8 by BPA, though at concentrations likely higher than those occurring in vivo [98].

3.6. Dysregulation of Gene Expression

In addition to the ability to interfere with TR signaling throughout a direct binding to the receptor, a number of studies observed that BPs may directly affect thyroid gene expression (Table 2).
At doses as low as 10−6 M, BPA and its analogues induced expression of transcripts of genes implicated in thyroid cell activity and proliferation (e.g., the Thyroid stimulating hormone-receptor (Tsh-r)), TH biosynthesis (e.g., Tg, Sodium iodide symporter (Slc5a5 encoding NIS), Thyroid-peroxidase (Tpo) and their transcription regulators (e.g., Paired box 8 (Pax8), NK2 homeobox 1 (Nkx2-1), and Forkhead box E1 (Foxe1)) by over 1.5 fold [89,99,100]. Conversely, BPA did not markedly affect transcriptional expression of Slc5a5, Nkx2-1, and Tpo but inhibited NIS-mediated iodide uptake [100]. BPA increased the expression of Tg gene in the presence of increasing TSH amounts, suggesting a potency similar to that of TSH in enhancing Tg-promoter activity [94]. The authors also reported that two anti-estrogens, which alone induced the activity of the Tg promoter, were not able to enhance BPA activity on the Tg promoter, indicating that the effects triggered by BPA do not necessarily involve ER signaling [89]. BPA at the nanomolar range significantly impaired the transcriptome of thyroid cells in a time dependent manner [101]. In fact, whereas short-term exposure to BPA did not cause any relevant transcriptomic changes, long-term exposure, though unable to exert visible damage on cells, determined a slight deregulation of many genes involved in cell proliferation/death, cancer, and DNA repair [101].
BPA and its analogues BPZ, BPF, and bisphenol M (BPM; 4,4′-(1,3-phenylenediisopropylidene)bisphenol) suppressed the transcription of several genes involved in the regulation of the HPT axis (e.g., TSH-specific β subunit (Tshβ), Thyroid hormone receptors (Trα and Trβ), and Deiodinases (Dio1 and Dio2)) in a concentration range of 10−7–10−6 M, with BPA substitutes being able to disrupt thyroid regulation at lower doses than BPA [75,85,99]. Furthermore, co-exposure with E2 potentiated decreased expression of Trα, Trβ and Dio2 [85].
BPA inhibited the activities of DIO1 and DIO2 [102], and both BPA and TBBPA markedly dysregulated transcription of Dio3, which is responsible for protection of tissues from TH excess and is the predominant deiodinase expressed in human placenta [103], and hepatic phase II metabolizing genes (Sulfotransferases (Sult1) and UDP-glucuronosyltransferases (Ugt)) [75]. TBBPA, but not BPA, increased expression of the Ttr gene [75], an action at mRNA level that corroborates the competing binding capabilities of TBBPA with TTR [70,84].

4. Thyroid Disrupting Properties of BPs: in Vivo Studies

In vivo effects of BP exposure on thyroid function/action are contradictory and difficult to compare, as a consequence of the scarce number of studies performed especially in mammals, the different models, and diversity of the experimental conditions, i.e., the chemical used, the time and dose of treatments, the outcomes assessed. In regards the risk of thyroid cancer associated to BPs exposure, the subject remains almost entirely unexplored.

4.1. Rodents

In rodents, most of the studies have been performed in pregnant females, and have evaluated the variations of TH levels in mothers and pups following prenatal and/or lactational exposures (Table 3).
In accordance with numerous in vitro studies, BPA can act as a selective TH antagonist on TRβ, inhibiting TH-negative feedback. Indeed, Zoeller et al. [104] and Zhang et al. [105] observed a significant increase of serum T4 levels in pups of both sexes and in female adults, respectively, without any apparent interference on TSH release. In male adult rats, treatment with BPA led to an increase of T4 levels and a reduction of the T3/T4 ratio, suggesting that in exposed animals BPA may impair the peripheral conversion of T4 to T3 [102].
In other experiments, BPA exposure did not produce significant variations in plasma T4 levels [106,107,108,109] or, alternatively, the effects may not endure after BPA removal and metabolism [110,111,112]. It is still unclear whether exposure to BPA and its derivatives can cause hypothyroidism due to limited evidence. A decrease in T4 levels was found in male and female adult rodents [110,113,114] and in rat pups of both sexes [114] or with a sex-specific effect [112,115]. The competition of BPs with TTR, as observed in vitro [70,84,92], resulting in a portion of serum T4 displaced from TTR, could determine an increased rate of T4 metabolism and elimination and the consequent reduction of T4 circulating levels [110].
Perinatal or neonatal exposure to BPA was associated with a significant increase of TSH levels in juvenile males [116] and in females in estrus [117,118], accompanied by a significant increase of GH levels and an impaired sensitivity of the thyroid gland to TSH stimulation, respectively, both of which indicate an alteration of the HPT axis [117]. On the other hand, the reduction of serum T3 or T4 after TBBPA treatment induced feedback stimulation, as suggested by the increased pituitary weight [114], whereas in other studies this was insufficient to affect serum TSH or TH levels, thyroid histopathology, and thyroid weight [107,110].
Adult males treated with BPA showed a decrease activity of hepatic DIO1, coherently with what has been reported in vitro [102]. Moreover, in female adult rats BPA lowered thyroid iodide uptake and thyroid peroxidase (TPO) activity, which are two essential steps in TH biosynthesis, probably due to an elevation of reactive oxygen species (ROS) production. Both NIS and TPO have been found to be sensitive to ROS [119,120], and in particular the decrease in TPO activity could be attributable to the oxidation of this enzyme [106]. Increased expression of pituitary Tshβ was reported in female rat neonates exposed to BPA [117], whereas Silva et al. did not find any significant reduction of Tshβ mRNA levels in treated female rats [106].
To date, it remains unclear whether BPA plays a role in the pathogenesis of thyroid carcinoma. Zhang et al. recently demonstrated that BPA could enhance the susceptibility to TC [105]. Rats pre-treated with N-bis (2-hydroxypropyl) nitrosamine, a drug stimulating thyroid proliferation and promoting a cancerous phenotype [121] and then exposed to BPA and excess iodine for 64 weeks, exhibited a significant increase in incidence of TC and thyroid hyperplasia lesions as well as the up-regulation of ERα in the hyperplasia lesions. The authors speculated that BPA could increase ERα expression in the thyroid, which possibly participated in the proliferation process [105].

4.2. Sheep

Sheep are considered a more relevant model to humans than rodents to evaluate fetal exposure to thyroid disruptors and their effects on the mother/newborn thyroid functions because of a similarity in the timing of the ontogenesis of thyroid [122]. In both species thyroxine binding globulin is the main blood transport protein for THs [123], and thyroid system maturation is qualitatively similar in the sheep and human fetuses, although the total maturation time is different (165 days vs. 300 days) [122,124].
Two studies have investigated the relationship of BPA exposure with thyroid function (Table 3). Viguié et al. [122] reported that BPA exposure of pregnant ewes was associated with a transitory hypothyroxinemia of both mothers and their newborn lambs, with a significant reduction of both circulating total T4 (TT4) and free T4 (FT4), findings in agreement with rodent studies [111,112]. In a following study, the authors confirmed alterations of gestational thyroid function, observing a significant reduction of FT4 and total T3 (TT3), but not TT4, in pregnant ewes treated with environmentally-relevant BPA concentrations via subcutaneous and dietary routes of administration [123]. After subcutaneous administration, the maximum serum concentration of BPA obtained was significantly higher (0.4 nmol/mL vs. 0.1 nmol/mL) and more prolonged than after dietary administration [123].

4.3. Zebrafish

Numerous studies have been published on the use of zebrafish (Danio rerio) to explore the effects of EDCs on the thyroid, due to several advantages: a short life cycle, high rates of production, real-time observations during the entire embryonic development, and high conservation of the molecular mechanisms regulating thyroid development with those of mammals [125,126]. The early life of fish, in particular, is acknowledged as highly sensitive to the effects of EDCs [127].
Coherently with results observed in vitro and in rodents, BPs may disturb TH homeostasis and gene expression in zebrafish embryos/larvae (Table 3).
Positive [37,38,128] and negative [37,38,128,129,130,131] associations between exposure to BPs and T3 and/or T4 levels have been reported, depending on the chemical used, the dose tested, and the time of exposure. Reductions in T4 concentrations, when accompanied with higher TSH contents, may compensate hypothyroidism in zebrafish larvae and stimulate TH synthesis [38,129]. Some experiments observed an interaction between TH levels and sex [129,131]. Tang et al. showed a reduction in whole-body TT4 and TT3 levels but not a significant variation of ratio TT3/TT4, which indicates the relative normal TH homeostasis [130].
Similarly, BPs disrupting effects on thyroid gene expression vary according to the different experimental conditions, especially the duration of exposure [126]. Hence, transcription levels of genes implicated in thyroid cell function and proliferation (Tsh-r), TH activity (Trα, Trβ), and transport (Ttr) can be up- [37,68,126,130,132,133] or down-regulated [38,68,126,128,130,133]. The transcription of Hematopoietically expressed homeobox (Hhex) was up-regulated in larval fish following exposure to BPA or BPF, although it is important to note that the Hhex gene is expressed in early life, contributing to differentiation and development of the thyroid gland, as well as of other organs, such as the pancreas and liver [37].
Increased [89,128,129] or decreased [130,132,134,135] expression of Slc5a5, Tpo, Pax8, and Tg transcripts was dependent on the dose and window of exposure. Additionally, BPA and BPS appeared to interact with PAX8 and thyroid transcription factor 1 (TTF1) in silico [135]. Genes such as Tpo, Tg, and Slc5a5 have binding sites for PAX8 or TTF1 on their enhancer or promoting regions. Differences of interactions between BPs and the transcription factors could be attributable to stimulation or inhibition with varying BPs doses, and produced as final effect altered expression of the genes controlled by PAX and TTF1 [135].
BPs stimulated thyroid signaling increases expression of Corticotrophin-releasing hormone (Crh) mRNA in the hypothalamus [37,38,129] and of Tsh and Tshβ in the pituitary gland [89,128,130,132,133,134], except for TBBPA, which down-regulated Tshβ mRNA in embryos [133].
Exposure to BPA and BPA analogues further induced transcription of genes involved in TH metabolism, i.e., Dio1 and/or Dio2 [37,129,132,134], which are implicated in activation/inactivation of T4 and in conversion of T4 to T3 in peripheral tissues, respectively [136,137], and Ugt1ab [37,38,129].
Notably, co-treatment with T3 appeared to reverse or eliminate thyroid disrupting effects of TBBPA on THs levels and gene transcription in zebrafish larvae [128], whereas a combined exposure of BPAF and sulfamethoxazole, an antibiotic used especially in aquaculture, produced more pronounced changes in transcription levels [134].

5. Thyroid Disrupting Properties of BPs: Human Studies

Perturbations in THs parameters consequent to exposure to BPA have been documented in humans, i.e., the general population, pregnant women, or occupational settings, although the study design, predominantly cross-sectional, does not allow establishment of any causal relationship. Research has highlighted positive, negative, or null associations with T4 levels, whereas a few prospective birth cohort studies suggest that prenatal BPA exposure may modify THs normal serum concentration in a sex-specific manner. Several investigations have demonstrated BPA-induced disruption of thyroid function by altering serum TSH levels. This effect could occur from a direct action of BPA on the pituitary gland via the estrogen signaling pathway or, alternatively, from a transient increase of T3 or T4 production that could lead to a feedback mechanism and the subsequent release inhibition of TSH. Overall, discrepant results among studies may be attributable to BPA levels, time of exposure, iodine intake, differences in age, ethnicity, diet, socioeconomic status, and the determination methods of THs, while at present the potential role of BPs in thyroid carcinogenesis in humans remains to be deeply explored (Table 4). It is noteworthy that the absence of adjustment for other confounding factors such as co-exposure to other EDCs makes the overall evaluation of thyroid dysfunction related to BPs exposure complex. Furthermore, a comparison between effects observed in animal models with those reported in epidemiological studies is complex given different serum T4 half-lives (12–24 h in rats vs. 5–9 days in humans), metabolic pathways of BPs, and doses of exposure, which in humans is more likely to be chronic and low level [138].

5.1. Effects on Serum TH Levels

Studies carried out in the general population and in mother/child cohorts showed positive [139,140,141], negative [142,143,144,145], and no associations between BPA exposure and serum T4 levels [143,146,147,148,149,150,151], whereas the relationship with serum T3 levels was estimated in few studies, with different findings [139,141,142,149,150].
In agreement with results from studies in animals [104,105,108], exposure to BPA led to TSH release/suppression independent of alterations in circulating THs levels [143,145,147,148,150,152] or, less frequently, was associated with variations of serum T4 levels [139,149].
There was no association of BPA with hypothyroidism in Japanese women with a history of recurrent miscarriages [151], nor any significant relationship between serum TBBPA in Korean infants with congenital hypothyroidism and THs levels [140]. Conversely, middle-aged and elderly Chinese with overt or subclinical hyperthyroidism had higher urinary BPA than euthyroid subjects [151], and an increased content of urinary BPA was also observed in obese adults undergoing a diet program or bariatric surgery compared to lean controls, probably due to differences in food intake [152].
Sex-related differences in the relationship between BPA and THs were reported both in the general population [142] and in newborns [143,148], coherently with studies performed in rats [112,115], and possibly attributable to a less efficient ability to metabolize BPA, i.e., a reduced expression of uridinediphosphate-glucuronosyltransferase 2B1 in male compared to female livers [153], or to a different androgen-related metabolism of BPA [154].
The interactions between BPA and THs during pregnancy and fetal development have been recently studied. The association between BPA and TSH levels in newborns was stronger when the time elapsed between the two measurements was shorter [143,148], suggesting that specific windows of exposure may influence susceptibility to BPA or, alternatively, that a transient effect on the HPT axis may occur, as shown in rodents [111,112]. However, the inverse association of BPA–TSH in pregnant women detected through repeated measures as well as stratified analyses by visit could indicate the absence of a specific window of vulnerability [139].

5.2. Association with Thyroid Diseases

The influence of BPA on thyroid autoimmunity is controversial (Table 4). Whereas urinary BPA concentration was associated with variations of TH levels both in children and adults of both sexes, independent of serum thyroglobulin antibodies (TgAb) and thyroid peroxidase antibodies (TPOAb) [149,155], another study found a positive relationship between serum BPA and TPOAb in men and women [156]. Moreover, a significant negative correlation of serum BPA with FT4 in male subjects was found only after exclusion of subjects with positive thyroid antibodies, suggesting that TgAb might be a mediator of the relationship between BPA and FT4 [144].
Kim and Oh reported a slight positive correlation between serum TBBPA and thyroid-stimulating hormone receptor antibodies, indicative of metabolic diseases, in mothers of infants with congenital hypothyroidism, suggesting that brominated derivatives of BPA might affect thyroid function status [140].
Recent investigations have explored the role of BPs as risk factors of occurrence of thyroid nodules (TNs), palpably and/or ultrasonographically discrete lesions, distinct from the surrounding parenchyma of the thyroid gland, which are either benign or malignant [157]. A study reported no association between BPs and higher risk of TNs in adult females [147], whereas Wang et al. observed an inverse correlation of urinary BPA and the risk of multiple TNs but not of solitary TNs in schoolchildren [158]. On the other hand, a significant near linear association between BPA and higher risk of TNs was observed exclusively among participants positive for TgAb and TPOAb [159]. Both urinary BPA and creatinine-adjusted BPA levels were higher in Chinese women with TNs than those without TNs [159], which is consistent with the increased urinary BPA contents in patients with nodular goiter and PTC (160), while median urinary BPA levels were lower in the cases compared to controls among women from Cyprus and Romania [147]. In the study by Zhou et al. [160], which was aimed to investigate the relationship between BPA and iodine exposure with nodular goiter and PTC, sex-specific associations were shown, with higher concentrations of BPA in women than in men affected by PTC and nodular goiter, and a lower urinary BPA content in the female PTC group than the female nodular goiter group, probably due to differences in BPA elimination rates. Marotta et al. recently found a significant dose-independent correlation between BPAF and the risk of differentiated TC in subjects with TNs. Of note, this association was not related to an increase of TSH levels, indicating a potential direct mutagenic action of BPAF on thyroid cells [161].

6. Discussion

The thyroid is highly susceptible to environmental pollutants, which may act as either genotoxic or non-genotoxic carcinogens [147]. BPA is a widespread chemical detected in urine specimens of the majority of adult populations. BPA analogues and derivatives are ubiquitous contaminants, measured in environmental and biological matrices, exhibiting a thyroid disrupting potential comparable and even stronger than BPA. The mechanisms of BPs action on THs are complex and need to be still elucidated.
Overall, the in vitro studies demonstrate that BPs may bind to TRs, acting mainly as TR antagonists, but also as agonists or without exerting any effect on TH signaling. Similarly, different patterns of Trβ expression following BPs exposure were observed in in vivo models. THs and their receptors regulate many important processes such as proliferation, differentiation, and apoptosis, and since TRβ is the major isoform in the thyroid, it can be hypothesized that disruption of its expression, leading to abnormalities in T3-induced transcriptional activity, could be involved in tumorigenesis [72,162].
In vivo experiments, supported by in vitro evidence, highlighted the ability of BPA and its substituting chemicals to affect thyroid follicular cell gene expression, particularly transcriptional levels of those genes encoding for factors involved in THs synthesis (TPO, NIS, Tg, PAX8). Up-regulation of Tg and Slc5a5 transcript levels may promote thyroid development to compensate for the depressed T4 concentration, as also reported for polybrominated diphenyl ethers [163]. Transcriptional levels of deiodinases were more elevated in exposed zebrafish, in accordance with a study reporting that hypothyroidism caused by EDCs is associated with higher activity and expression of Dio2 [164]. On the other hand, a recent study reported a reduction of liver DIO1 activity in BPA-treated adult rats [102], which is a finding worth of note as decreased expression of DIO1 was observed in nearly all PTCs and is likely an early event in malignant TC [165].
In rodents and in two different types of cell lines, BPA up-regulated Pax8 transcripts, suggesting a role of BPA in increasing Pax8 expression independent from the cellular context [89]. PAX8 is a cell-lineage-specific transcription factor that has been mainly characterized in the thyroid gland for its role in thyrocyte differentiation, and it has been revealed as a potential diagnostic marker for several cancer sites including TC [166].
TSH should represent an effective index of activation of the HPT axis to evaluate central effects of xenobiotics on thyroid function through measurement of TSH secretion or expression as a compensatory mechanism for maintaining TH homeostasis. Moreover, TSH levels are an independent predictor of thyroid nodule malignancy regardless of age, sex or family history [6]. Increased expression of TSH and TSHβ observed in vivo was also reported after exposure to pesticides and halogenated chemicals in fish [163,167] suggesting that elevated production of TSH could represent one of the mechanisms of action of BPs, as already hypothesized for other EDCs (9). In pituitary cells, BPA and E2 could further induce release of TSH desensitizing the response to thyrotropin releasing hormone from hypothalamus [118]. In contrast, humans and pregnant ewes exhibited hypothyroxinemia after BPA exposure without significant modifications of TSH, whilst other epidemiological studies reported a decreased TSH production, probably consequent of a direct action of BPA on pituitary gland through estrogen receptor signaling or of a feedback mechanism triggered by BPA-mediated perturbations on circulating T3 and T4 [139].
The frequency of chronic autoimmune Hashimoto’s thyroiditis, the most common cause of primary hypothyroidism in western countries, has increased in the last two decades, and a variety of factors such as tobacco smoking, iodine and selenium intake, and exposure to EDCs, may contribute to the elevated incidence by interacting with susceptibility genes (6). Autoimmune thyroiditis may coexist with TC [168], and a recent meta-analysis demonstrated that this condition predisposes patients to the development of the papillary histotype [169]. Thyroid autoantibodies were reported to be positively associated with the level of urinary BPA, therefore subjects with thyroid autoantibodies positivity, as characterized by immune dysfunction and a lower ability to eliminate damaged cells, are probably more vulnerable to the effects of BPs on TNs [159].
It cannot be excluded that exposure of thyrocytes to BPA involves hydrogen peroxide generation due to an elevated activity of a calcium-dependent NAPDH oxidase (DUOX) [106]. TPO is a key enzyme in the synthesis of THs, catalyzing, through the cofactor H2O2, the iodination of tyrosyl residues in Tg [106]. Thus, the increased oxidative stress in the thyroid gland, which is related to a reduction of TPO activity, corroborates the negative correlation between TPO and DUOX2 in thyroid nodular lesions [170]. Furthermore, oxidant/antioxidant balance was recently reported to be impaired in children affected by autoimmune thyroiditis, though it is unclear whether oxidative stress is the real cause of the disease or the likely consequence of exposure to EDCs, including BPA [155].
Finally, BPA is potentially linked to excess iodine in the pathogenesis of the nodular goiter and TC in animals [105] and humans [160]. High urinary iodine is a risk factor for the development of benign TNs and PTC [171], being associated with reduced expression of NIS, an early abnormality in the pathway of thyroid cell transformation, and increased occurrence of BRAF mutations [172], which are both hallmarks of differentiated TC [173].

7. Conclusions

This review aims at evaluating the extensive body of experimental and human studies that in the last two decades have attempted to explore the effects of BPA, its substitutes, and its halogenated derivatives on the thyroid at different levels. Despite the variety of approaches applied and the heterogeneous and sometimes even conflicting results from the examined studies, a series of interesting indications supports the hypothesis of a role of BPs in interfering with the normal thyroid function. Although the toxicity pathways of BPs on the thyroid need to be further elucidated, BPA analogues and halogenated derivatives do not emerge as safer alternatives to BPA in term of TH disruption. There is evidence that BPs alters THs circulating levels, inhibiting TH-negative feedback, act as selective TR antagonists, and interfere with expression of genes involved in thyroid stimulation, TH synthesis, TH activity, and TH transport and metabolism. Several reported findings, mainly from experimental studies, are, however, rather inconsistent, while the association of BPs exposure with thyroid cancer is so far almost unexplored. The lack of uniformity in experimental methodology, as well as substantial differences in populations investigated in epidemiological studies, do not allow definitive conclusions to be drawn. Standardized in vivo, in vitro, and in silico studies are recommended to evaluate the physiopathology of the damage associated with exposure to environmentally relevant levels of BPs, identify other potential molecular targets, and clarify the structure−activity relationship of BPs. At the same time, large population-based human studies with prospective designs and repeated measures of urine BPs concentrations and thyroid volume over time, as well as an accurate control of confounders, should be performed for the assessment of the temporal relationship between markers of exposure and long-term effects.

Author Contributions

Conceptualization, F.G. and F.B.; methodology, F.G., E.B., and A.C.; data curation, F.G.; writing—original draft preparation, F.G.; writing—review and editing, F.G., E.B., A.C., G.I., F.B.; visualization, F.G., E.B., A.C., G.I., and F.B.; supervision, A.C., G.I., and F.B.; project administration, F.B.; funding acquisition, F.B. All authors have read and agree to the published version of the manuscript.

Funding

This research was funded by the Italian Ministry of Education, University and Research, MIUR–Deliberation CIPE n. 105/2015, 23 December 2015, grant number B62F15001070005.

Conflicts of Interest

The authors declare no conflict of interest.

Abbreviations

3,3′-Cl2BPA3,3′-dichlorobisphenol A
3,5-Cl2BPA3,5-dichlorobisphenol A
95% CI95% confidence interval
96 h-LC5096 h median lethal concentration
AMAmiodarone
BMIBody mass index
BPABisphenol A; 2,2-bis(4-hydroxyphenyl)propane)
BPAFBisphenol AF; 1,1,1,3,3,3-hexafluoro-2,2-bis(4-hydroxyphenyl)propane
BPAPBisphenol AP (4,4′-(1-phenylethylidene)bisphenol
BPBBisphenol B (2,2-bis(4-hydroxyphenyl)butane)
BPFBisphenol F; 4,4′-dihydroxydiphenylmethane
BPMBisphenol M; 4,4′-(1,3-phenylenediisopropylidene)bisphenol)
BPPBisphenol P (2,2-bis(4-hydroxyphenyl)butane)
BPSBisphenol S; 4,4′-sulfonyldiphenol
BPZBisphenol Z; 1,1-bis(4-hydroxyphenyl)-cyclohexane
BPsBisphenols
BrdU5′-bromo-2′-deoxyuridine
BSABody surface area
BWBody weight
CHAMACOSCenter for the Health Assessment of Mothers and Children of Salinas
ClBPA3-chlorobisphenol A
ClxBPASum of ClBPA, 3,5-Cl2BPA, and 3,3′-Cl2BPA
crCreatinine
CrhCorticotrophin-releasing hormone
c-Src/PI3KProto-oncogene tyrosine-protein/phosphatidylinositol 3-kinase
D1Type 1 iodothyronine deiodinase
D2Type 2 iodothyronine deiodinase
DHPNN-bis (2-hydroxypropyl) nitrosamine
Dio1Deiodinase 1
Dio2Deiodinase 2
Dio3Deiodinase 3
dpfDays post-fertilization
DTCDifferentiated thyroid cancer
EC50Median effective concentration
EDC(s)Endocrine disrupting chemical(s)
EGFPExcitation and emission of green fluorescent proteins
ELISAEnzyme linked immunosorbent assay
ERsEstrogen receptors
ERαEstrogen receptor α
E217-β estradiol
ERKExtracellular-signal-regulated kinase
Foxe1Forkhead box E1
FT3Free triidothyronine
FT4Free thyroxine
GDGestation day
GFPGreen fluorescent protein
GHGrowth hormone
GMGeometric mean
GPR30G protein-coupled receptor 30
HhexHematopoietically expressed homeobox
HOMEHealth Outcomes and Measures of the Environment
hpfhours post fertilization
HPTHypothalamic–pituitary–thyroid
HTHashimoto’s thyroiditis
IC10Concentration at which 10% of the inhibition was observed
IC50Concentration at which 50% of the inhibition was observed
ICIFulvestrant
IQRInterquartile range
JNKc-Jun NH2-terminal kinase
KIPotassium iodine
LC50Median lethal concentration
LOAELLow observed adverse effect level
LODLimit of detection
LOECLowest observed effect concentration
LOWLimit of quantification
MAPKMitogen-activated protein kinase
MCTMonocarboxylate transporter
MEKMitogen-activated protein kinase/ERK kinase
MTT3-(4,5-dimethylthiazol-2-yl)-2,5-diphenyltetrazolium bromide
NaISodium iodide
N-CoRNuclear receptor co-repressor
n.d.Not detected
NGNodular goiter
NHANESNational Health and Nutrition Examination Survey
NHES IVThai National Health Examination Survey
Nkx2-1NK2 homeobox 1
OATPOrganic anion transport protein
Pax8Paired box 8
PNDPostnatal day
PTCPapillary thyroid cancer
qRT-PCRQuantitative real time polymerase chain reaction
ROSReactive oxygen species
SAPKStress-activated proteins kinases
Slc5a5Gene encoded for sodium iodide symporter
SMRTSilencing mediator for retinoid and thyroid
SRCSteroid receptor coactivator
Sult-st1/2/3/5Sulfotransferase 1/2/3/5
T3Triiodothyronine
T4Thyroxine
TAMTamoxifen
TBBPATetrabromobisphenol A
TBBPSTetrabromobisphenol S
TBGThyroxine binding globulin
TCThyroid cancer
TCBPATetrachlorobisphenol A
TgThyroglobulin
TgAbThyroglobulin antibody
TH(s)Thyroid hormone(s)
TN(s)Thyroid nodule(s)
TpoThyroid peroxidase
TPOAbThyroid peroxidase antibody
TR(s)Thyroid receptor(s)
TRAbThyroid receptor antibody
TrαThyroid receptor α
TrβThyroid receptor β
TRHThyrotropin-releasing hormone
Trh-RThyrotropin-releasing hormone receptor
TSHThyroid stimulating hormone
TshβTSH-specific β subunit
Tsh-rThyroid stimulating hormone-receptor
TTRTransthyretin
TT3Total triiodothyronine
TT4Total thyroxine
UgtUridine diphosphate -glucuronosyltransferase

References

  1. Calsolaro, V.; Pasqualetti, G.; Niccolai, F.; Caraccio, N.; Monzani, F. Thyroid Disrupting Chemicals. Int. J. Mol. Sci. 2017, 18, 2583. [Google Scholar] [CrossRef] [PubMed][Green Version]
  2. Moriyama, K.; Tagami, T.; Akamizu, T.; Usui, T.; Saijo, M.; Kanamoto, N.; Hataya, Y.; Shimatsu, A.; Kuzuya, H.; Nakao, K. Thyroid hormone action is disrupted by bisphenol A as an antagonist. J. Clin. Endocrinol. Metab. 2002, 87, 5185–5190. [Google Scholar] [CrossRef] [PubMed]
  3. Lim, H.; Devesa, S.S.; Sosa, J.A.; Check, D.; Kitahara, C.M. Trends in Thyroid Cancer Incidence and Mortality in the United States, 1974-2013. JAMA 2017, 317, 1338. [Google Scholar] [CrossRef] [PubMed]
  4. Nettore, I.C.; Colao, A.; Macchia, P.E. Nutritional and Environmental Factors in Thyroid Carcinogenesis. Int. J. Environ. Res. Public Health 2018, 15, 1735. [Google Scholar] [CrossRef] [PubMed][Green Version]
  5. Liu, F.C.; Lin, H.T.; Lin, S.F.; Kuo, C.F.; Chung, T.T.; Yu, H.P. Nationwide cohort study on the epidemiology and survival outcomes of thyroid cancer. Oncotarget 2017, 8, 78429–78451. [Google Scholar] [CrossRef][Green Version]
  6. Pellegriti, G.; Frasca, F.; Regalbuto, C.; Squatrito, S.; Vigneri, R. Worldwide increasing incidence of thyroid cancer: Update on epidemiology and risk factors. J. Cancer Epidemiol. 2013, 2013, 965212. [Google Scholar] [CrossRef][Green Version]
  7. Zoeller, R.T.; Brown, T.R.; Doan, L.L.; Gore, A.C.; Skakkebaek, N.E.; Soto, A.M.; Woodruff, T.J.; Vom Saal, F.S. Endocrine-disrupting chemicals and public health protection: A statement of principles from The Endocrine Society. Endocrinology 2012, 153, 4097–4110. [Google Scholar] [CrossRef]
  8. Vandenberg, L.N.; Colborn, T.; Hayes, T.B.; Heindel, J.J.; Jacobs, D.R.; Lee, D.H.; Shioda, T.; Soto, A.M.; vom Saal, F.S.; Welshons, W.V.; et al. Hormones and endocrine-disrupting chemicals: Low-dose effects and nonmonotonic dose responses. Endocr. Rev. 2012, 33, 378–455. [Google Scholar] [CrossRef]
  9. Gorini, F.; Iervasi, G.; Coi, A.; Pitto, L.; Bianchi, F. The Role of Polybrominated Diphenyl Ethers in Thyroid Carcinogenesis: Is It a Weak Hypothesis or a Hidden Reality? From Facts to New Perspectives. Int. J. Environ. Res. Public Health 2018, 15, 1834. [Google Scholar] [CrossRef][Green Version]
  10. Kitamura, S.; Kato, T.; Iida, M.; Jinno, N.; Suzuki, T.; Ohta, S.; Fujimoto, N.; Hanada, H.; Kashiwagi, K.; Kashiwagi, A. Anti-thyroid hormonal activity of tetrabromobisphenol A, a flame retardant, and related compounds: Affinity to the mammalian thyroid hormone receptor, and effect on tadpole metamorphosis. Life Sci. 2015, 76, 1589–1601. [Google Scholar] [CrossRef]
  11. Welshons, W.V.; Nagel, S.C.; vom Saal, F.S. Large effects from small exposures. III. Endocrine mechanisms mediating effects of bisphenol A at levels of human exposure. Endocrinology 2006, 147, S56–S69. [Google Scholar] [CrossRef] [PubMed]
  12. Rubin, B.S. Bisphenol A: An endocrine disruptor with widespread exposure and multiple effects. J. Steroid Biochem. Mol. Biol. 2011, 127, 27–34. [Google Scholar] [CrossRef]
  13. Vandenberg, L.N.; Maffini, M.V.; Sonnenschein, C.; Rubin, B.S.; Soto, A.M. Bisphenol A and the great divide: A review of controversies in the field of endocrine disruption. Endocr. Rev. 2009, 30, 75–95. [Google Scholar] [CrossRef]
  14. Kim, Y.S.; Hwang, K.A.; Hyun, S.H.; Nam, K.H.; Lee, C.K.; Choi, K.C. Bisphenol A and nonylphenol have the potential to stimulate the migration of ovarian cancer cells by inducing epithelial–mesenchymal transition via an estrogen receptor dependent pathway. Chem. Res. Toxicol. 2015, 28, 662–671. [Google Scholar] [CrossRef] [PubMed]
  15. Yang, M.; Ryu, J.H.; Jeon, R.; Kang, D.; Yoo, K.Y. Effects of bisphenol A on breast cancer and its risk factors. Arch. Toxicol. 2009, 83, 281–285. [Google Scholar] [CrossRef] [PubMed]
  16. Mínguez-Alarcón, L.; Hauser, R.; Gaskins, A.J. Effects of bisphenol A on male and couple reproductive health: A review. Fertil. Steril. 2016, 106, 864–870. [Google Scholar] [CrossRef] [PubMed][Green Version]
  17. Mustieles, V.; Pérez-Lobato, R.; Olea, N.; Fernández, M.F. Bisphenol A: Human exposure and neurobehavior. Neurotoxicology 2015, 49, 174–184. [Google Scholar] [CrossRef]
  18. Han, C.; Hong, Y.C. Bisphenol A, Hypertension, and Cardiovascular Diseases: Epidemiological, Laboratory, and Clinical Trial Evidence. Curr. Hypertens. Rep. 2016, 18, 11. [Google Scholar] [CrossRef]
  19. Bertoli, S.; Leone, A.; Battezzati, A. Human Bisphenol A Exposure and the “Diabesity Phenotype”. Dose Response 2015, 13, 155932581559917. [Google Scholar] [CrossRef][Green Version]
  20. Carwile, J.L.; Michels, K.B. Urinary bisphenol A and obesity: NHANES 2003–2006. Environ. Res. 2011, 111, 825–830. [Google Scholar] [CrossRef][Green Version]
  21. Xu, L.C.; Sun, H.; Chen, J.F.; Bian, Q.; Qian, J.; Song, L.; Wang, X.R. Evaluation of androgen receptor transcriptional activities of bisphenol A, octylphenol and nonylphenol in vitro. Toxicology 2005, 216, 197–203. [Google Scholar] [CrossRef] [PubMed]
  22. Richter, C.A.; Birnbaum, L.S.; Farabollini, F.; Newbold, R.R.; Rubin, B.S.; Talsness, C.E.; Vandenbergh, J.G.; Walser-Kuntz, D.R.; Vom Saal, F.S. In vivo effects of bisphenol A in laboratory rodent studies. Reprod. Toxicol. 2007, 24, 199–224. [Google Scholar] [CrossRef] [PubMed][Green Version]
  23. Li, D.K.; Zhou, Z.; Miao, M.; He, Y.; Wang, J.; Ferber, J.; Herrinton, L.J.; Gao, E.; Yuan, W. Urine bisphenol-A (BPA) level in relation to semen quality. Fertil. Steril. 2011, 95, 625–630. [Google Scholar] [CrossRef]
  24. Calafat, A.M.; Ye, X.; Wong, L.Y.; Reidy, J.A.; Needham, L.L. Exposure of the U.S. Population to Bisphenol A and 4- tertiary -Octylphenol: 2003–2004. Environ. Health Perspect. 2008, 116, 39–44. [Google Scholar] [CrossRef] [PubMed][Green Version]
  25. Michałowicz, J. Bisphenol A – sources, toxicity and biotransformation. Environ. Toxicol. Pharmacol. 2014, 37, 738–758. [Google Scholar] [CrossRef] [PubMed]
  26. Flint, S.; Markle, T.; Thompson, S.; Wallace, E. Bisphenol A exposure, effects, and policy: A wildlife perspective. J. Environ. Manag. 2012, 104, 19–34. [Google Scholar] [CrossRef] [PubMed]
  27. Colin, A.; Bach, C.; Rosin, C.; Munoz, J.F.; Dauchy, X. Is drinking water a major route of human exposure to alkylphenol and bisphenol contaminants in France? Arch. Environ. Contam. Toxicol. 2014, 66, 86–99. [Google Scholar] [CrossRef]
  28. Canesi, L.; Fabbri, E. Environmental Effects of BPA: Focus on Aquatic Species. Dose Response 2015, 13, 1559325815598304. [Google Scholar] [CrossRef][Green Version]
  29. Corrales, J.; Kristofco, L.A.; Steele, W.B.; Yates, B.S.; Breed, C.S.; Williams, E.S.; Brooks, B.W. Global Assessment of Bisphenol A in the Environment: Review and Analysis of Its Occurrence and Bioaccumulation. Dose Response 2015, 13, 155932581559830. [Google Scholar] [CrossRef][Green Version]
  30. Vogel, S.A. The politics of plastics: The making and unmaking of bisphenol a “safety”. Am. J. Public Health 2009, 99, S559–S566. [Google Scholar] [CrossRef]
  31. EFSA, European Food Safety Authority. Scientific Opinion on the risks to public health related to the presence of bisphenol A (BPA) in foodstuffs. EFSA Panel on Food Contact Materials E Flavourings and Processing Aids (CEF). EFSA J. 2015, 13, 3978. [Google Scholar] [CrossRef]
  32. Commission Directive 2011/8/EU of 28 January 2011 amending Directive 2002/72/EC as regards the restriction of use of Bisphenol A in plastic infant feeding bottles (Text with EEA relevance 4). Available online: https://eur-lex.europa.eu/LexUriServ/LexUriServ.do?uri=OJ:L:2011:026:0011:0014:EN:PDF (accessed on 14 February 2020).
  33. Food and Drug Administration (FDA). Food Additive Regulations Amended to No Longer Provide for the Use of BPA-Based Materials in Baby Bottles, Sippy Cups, and Infant Formula Packaging. In 2012, 77 Fed. Reg. 41,899. Available online: https://www.federalregister.gov/documents/2012/07/17/2012-17366/indirect-food-additives-polymers (accessed on 14 February 2020).
  34. Vandenberg, L.N.; Hauser, R.; Marcus, M.; Olea, N.; Welshons, W.V. Human exposure to bisphenol A (BPA). Reprod. Toxicol. 2007, 24, 139–177. [Google Scholar] [CrossRef] [PubMed]
  35. CDC (Centers for Disease Control and Prevention). Fourth National Report on Human Exposure to Environmental Chemicals; CDC: Atlanta, GA, USA, 2013; pp. 1–770. [Google Scholar]
  36. Zhang, T.; Sun, H.; Kannan, K. Blood and urinary bisphenol A concentrations in children, adults, and pregnant women from china: Partitioning between blood and urine and maternal and fetal cord blood. Environ. Sci. Technol. 2013, 47, 4686–4694. [Google Scholar] [CrossRef] [PubMed]
  37. Lee, S.; Kim, C.; Shin, H.; Kho, Y.; Choi, K. 2019 Comparison of thyroid hormone disruption potentials by bisphenols A, S, F, and Z in embryo-larval zebrafish. Chemosphere 2013, 221, 115–123. [Google Scholar] [CrossRef] [PubMed]
  38. Huang, G.; Tian, X.; Fang, X.; Ji, F. Waterborne exposure to bisphenol F causes thyroid endocrine disruption in zebrafish larvae. Chemosphere 2016, 147, 188–194. [Google Scholar] [CrossRef] [PubMed]
  39. Rochester, J.R.; Bolden, A.L. Bisphenol S and F: A Systematic Review and Comparison of the Hormonal Activity of Bisphenol A Substitutes. Environ. Health Perspect. 2015, 123, 643–650. [Google Scholar] [CrossRef]
  40. Cacho, J.I.; Campillo, N.; Viñas, P.; Hernández-Córdoba, M. Stir bar sorptive extraction coupled to gas chromatography–mass spectrometry for the determination of bisphenols in canned beverages and filling liquids of canned vegetables. J. Chromatogr. A 2012, 1247, 146–153. [Google Scholar] [CrossRef]
  41. Liao, C.; Liu, F.; Moon, H.B.; Yamashita, N.; Yun, S.; Kannan, K. Bisphenol analogues in sediments from industrialized areas in the United States, Japan, and Korea: Spatial and temporal distributions. Environ. Sci. Technol. 2012, 46, 11558–11565. [Google Scholar] [CrossRef]
  42. Zhou, X.; Kramer, J.; Calafat, A.M.; Ye, X. Automated on-line column-switching high performance liquid chromatography isotope dilution tandem mass spectrometry method for the quantification of bisphenol A, bisphenol F, bisphenol S, and 11 other phenols in urine. J. Chromatogr. B Analyt. Technol. Biomed. Life Sci. 2014, 944, 152–156. [Google Scholar] [CrossRef]
  43. Office of Chemical Safety & Pollution Prevention, EPA. Doc. No.740-R1-4004, TSCA Work Plan Chemical Problem Formulation and Initial Assessment: Tetrabromobisphenol A and Related Chemicals Cluster Flame Retardants 10, 2015. Available online: https://www.epa.gov/sites/production/files/2015-09/documents/tbbpa_problem_formulation_august_2015.pdf (accessed on 14 February 2020).
  44. Yin, N.; Liang, S.; Liang, S.; Yang, R.; Hu, B.; Qin, Z.; Liu, A.; Faiola, F. TBBPA and Its Alternatives Disturb the Early Stages of Neural Development by Interfering with the NOTCH and WNT Pathways. Environ. Sci. Technol. 2018, 52, 5459–5468. [Google Scholar] [CrossRef]
  45. Malkoske, T.; Tang, Y.; Xu, W.; Yu, S.; Wang, H. A review of the environmental distribution, fate, and control of tetrabromobisphenol A released from sources. Sci. Total Environ. 2016, 569–570, 1608–1617. [Google Scholar] [CrossRef] [PubMed]
  46. Wu, Y.; Li, Y.; Kang, D.; Wang, J.; Zhang, Y.; Du, D.; Pan, B.; Lin, Z.; Huang, C.; Dong, Q. Tetrabromobisphenol A and heavy metal exposure via dust ingestion in an e-waste recycling region in Southeast China. Sci. Total Environ. 2016, 541, 356–364. [Google Scholar] [CrossRef] [PubMed]
  47. Yamazaki, E.; Yamashita, N.; Taniyasu, S.; Lam, J.; Lam, P.K.S.; Moon, H.B.; Jeong, Y.; Kannan, P.; Achyuthan, H.; Munuswamy, N.; et al. Bisphenol A and other bisphenol analogues including BPS and BPF in surface water samples from Japan, China, Korea and India. Ecotoxicol. Environ. Saf. 2015, 122, 565–572. [Google Scholar] [CrossRef] [PubMed]
  48. Liao, C.; Liu, F.; Guo, Y.; Moon, H.B.; Nakata, H.; Wu, Q.; Kannan, K. Occurrence of eight bisphenol analogues in indoor dust from the United States and several Asian countries: Implications for human exposure. Environ. Sci. Technol. 2012, 46, 9138–9145. [Google Scholar] [CrossRef] [PubMed]
  49. Fu, P.; Kawamura, K. Ubiquity of bisphenol A in the atmosphere. Environ. Pollut. 2010, 158, 3138–3143. [Google Scholar] [CrossRef][Green Version]
  50. Yamamoto, T.; Yasuhara, A.; Shiraishi, H.; Nakasugi, O. Bisphenol A in hazardous waste landfill leachates. Chemosphere 2001, 42, 415–418. [Google Scholar] [CrossRef]
  51. Geens, T.; Neels, H.; Covaci, A. Distribution of bisphenol-A, triclosan and n-nonylphenol in human adipose tissue, liver and brain. Chemosphere 2012, 87, 796–802. [Google Scholar] [CrossRef]
  52. Sun, Y.; Irie, M.; Kishikawa, N.; Wada, M.; Kuroda, N.; Nakashima, K. Determination of bisphenol A in human breast milk by HPLC with column-switching and fluorescence detection. Biomed. Chromatogr. 2004, 18, 501–507. [Google Scholar] [CrossRef]
  53. World Health Organization & Food and Agriculture Organization of the United Nations (2011). In Proceedings of the Joint FAO/WHO Expert Meeting to Review Toxicological and Health Aspects of Bisphenol A: Final Report, Including Report of Stakeholder Meeting on Bisphenol A, Ottawa, ON, Canada, 1–5 November 2010. Available online: https://apps.who.int/iris/bitstream/handle/10665/44624/97892141564274_eng.pdf?sequence=1&isAllowed=y (accessed on 14 February 2020).
  54. Liao, C.; Liu, F.; Alomirah, H.; Loi, V.D.; Mohd, M.A.; Moon, H.B.; Nakata, H.; Kannan, K. Bisphenol S in urine from the United States and seven Asian countries: Occurrence and human exposures. Environ. Sci. Technol. 2012, 46, 6860–6866. [Google Scholar] [CrossRef]
  55. Liu, K.; Li, J.; Yan, S.; Zhang, W.; Li, Y.; Han, D. A review of status of tetrabromobisphenol A (TBBPA) in China. Chemosphere 2016, 148, 8–20. [Google Scholar] [CrossRef]
  56. Yang, S.; Wang, S.; Liu, H.; Yan, Z. Tetrabromobisphenol A: Tissue distribution in fish, and seasonal variation in water and sediment of Lake Chaohu, China. Environ. Sci. Pollut. Res. Int. 2012, 19, 4090–4096. [Google Scholar] [CrossRef] [PubMed]
  57. Zhu, Z.C.; Chen, S.J.; Zheng, J.; Tian, M.; Feng, A.H.; Luo, X.J.; Mai, B.X. Occurrence of brominated flame retardants (BFRs), organochlorine pesticides (OCPs), and polychlorinated biphenyls (PCBs) in agricultural soils in a BFR-manufacturing region of North China. Sci. Total Environ. 2014, 481, 47–54. [Google Scholar] [CrossRef] [PubMed]
  58. Cariou, R.; Antignac, J.P.; Zalko, D.; Berrebi, A.; Cravedi, J.P.; Maume, D.; Marchand, P.; Monteau, F.; Riu, A.; Andre, F.; et al. Exposure assessment of French women and their newborns to tetrabromobisphenol-A: Occurrence measurements in maternal adipose tissue, serum, breast milk and cord serum. Chemosphere 2008, 73, 1036–1041. [Google Scholar] [CrossRef] [PubMed]
  59. EFSA Panel on Contaminants in the Food Chain (CONTAM). Scientific Opinion on Tetrabromobisphenol A (TBBPA) and its derivatives in food: TBBPA and its derivatives in food. EFSA J. 2011, 9, 2477. Available online: https://efsa.onlinelibrary.wiley.com/doi/pdf/10.2903/j.efsa.2011.2477 (accessed on 14 February 2020). [CrossRef]
  60. Harvey, C.B.; Bassett, J.H.D.; Maruvada, P.; Yen, P.M.; Williams, G.R. The rat thyroid hormone receptor (TR) Δβ3 displays cell-, TR isoform-, and thyroid hormone response element-specific actions. Endocrinology 2007, 148, 1764–1773. [Google Scholar] [CrossRef][Green Version]
  61. Kublaoui, B.; Levine, M.A. Receptor transduction pathways mediating hormone action. In Pediatric Endocrinology, 4th ed.; Elsevier Inc.: Amsterdam, The Netherlands, 2014; pp. 34–89. [Google Scholar]
  62. Fattori, J.; Campos, J.L.; Doratioto, T.R.; Assis, L.M.; Vitorino, M.T.; Polikarpov, I.; Xavier-Neto, J.; Figueira, A.C. RXR agonist modulates TR: Corepressor dissociation upon 9-cis retinoic acid treatment. Mol. Endocrinol. 2015, 29, 258–273. [Google Scholar] [CrossRef]
  63. Aagaard, M.M.; Siersbæk, R.; Mandrup, S. Molecular basis for gene-specific transactivation by nuclear receptors. Biochim. Biophys. Acta 2011, 1812, 824–835. [Google Scholar] [CrossRef][Green Version]
  64. Guyot, R.; Chatonnet, F.; Gillet, B.; Hughes, S.; Flamant, F. Toxicogenomic analysis of the ability of brominated flame retardants TBBPA and BDE-209 to disrupt thyroid hormone signaling in neural cells. Toxicology 2014, 325, 125–132. [Google Scholar] [CrossRef]
  65. Jugan, M.L.; Lévy-Bimbot, M.; Pomérance, M.; Tamisier-Karolak, S.; Blondeau, J.P.; Lévi, Y. A new bioluminescent cellular assay to measure the transcriptional effects of chemicals that modulate the alpha-1 thyroid hormone receptor. Toxicol. In Vitro 2007, 21, 1197–1205. [Google Scholar] [CrossRef]
  66. Iwamuro, S.; Yamada, M.; Kato, M.; Kikuyama, S. Effects of bisphenol A on thyroid hormone-dependent up-regulation of thyroid hormone receptor α and β and down-regulation of retinoid X receptor γ in Xenopus tail culture. Life Sci. 2006, 79, 2165–2171. [Google Scholar] [CrossRef]
  67. Seiwa, C.; Nakahara, J.; Komiyama, T.; Katsu, Y.; Iguchi, T.; Asou, H. Bisphenol A exerts thyroid-hormone-like effects on mouse oligodendrocyte precursor cells. Neuroendocrinology 2004, 80, 21–30. [Google Scholar] [CrossRef] [PubMed]
  68. Lu, L.; Zhan, T.; Ma, M.; Xu, C.; Wang, J.; Zhang, C.; Liu, W.; Zhuang, S. Thyroid Disruption by Bisphenol S Analogues via Thyroid Hormone Receptor β: In Vitro, in Vivo, and Molecular Dynamics Simulation Study. Environ. Sci. Technol. 2018, 52, 6617–6625. [Google Scholar] [CrossRef] [PubMed]
  69. Terasaki, M.; Kosaka, K.; Kunikane, S.; Makino, M.; Shiraishi, F. Assessment of thyroid hormone activity of halogentaed bisphenol A using a yeast two-hybrid assay. Chemosphere 2011, 84, 1527–1530. [Google Scholar] [CrossRef] [PubMed]
  70. Kudo, Y.; Yamauchi, K.; Fukazawa, H.; Terao, Y. In vitro and in vivo analysis of the thyroid system–disrupting activities of brominated phenolic and phenol compounds in Xenopus laevis. Toxicol. Sci. 2006, 92, 87–95. [Google Scholar] [CrossRef][Green Version]
  71. Kitamura, S.; Jinno, N.; Ohta, S.; Kuroki, H.; Fujimoto, N. Thyroid hormonal activity of the flame retardants tetrabromobisphenol A and tetrachlorobisphenol A. Biochem. Biophys. Res. Commun. 2002, 293, 554–559. [Google Scholar] [CrossRef]
  72. Hofmann, P.J.; Schomburg, L.; Köhrle, J. Interference of Endocrine Disrupters with Thyroid Hormone Receptor–Dependent Transactivation. Toxicol. Sci. 2009, 110, 125–137. [Google Scholar] [CrossRef][Green Version]
  73. Sun, H.; Shen, O.X.; Wang, X.R.; Zhou, L.; Zhen, S.; Chen, X. Anti-thyroid hormone activity of bisphenol A, tetrabromobisphenol A and tetrachlorobisphenol A in an improved reporter gene assay. Toxicol. In Vitro 2009, 23, 950–954. [Google Scholar] [CrossRef]
  74. Otsuka, S.; Ishihara, A.; Yamauchi, K. Ioxynil and tetrabromobisphenol a suppress thyroid-hormone-induced activation of transcriptional elongation mediated by histone modifications and RNA polymerase II phosphorylation. Toxicol. Sci. 2014, 138, 290–299. [Google Scholar] [CrossRef][Green Version]
  75. Yang, J.; Chan, K.M. Evaluation of the toxic effects of brominated compounds (BDE-47, 99, 209, TBBPA) and bisphenol A (BPA) using a zebrafish liver cell line, ZFL. Aquat. Toxicol. 2015, 159, 138–147. [Google Scholar] [CrossRef]
  76. Freitas, J.; Cano, P.; Craig-Veit, C.; Goodson, M.L.; David Furlow, J.; Murk, A.J. Detection of thyroid hormone receptor disruptors by a novel stable in vitro reporter gene assay. Toxicol. In Vitro 2011, 250, 257–266. [Google Scholar] [CrossRef]
  77. Sheng, Z.G.; Tang, Y.; Liu, Y.X.; Yuan, Y.; Zhao, B.Q.; Chao, X.J.; Zhu, B.Z. Low concentrations of bisphenol a suppress thyroid hormone receptor transcription through a nongenomic mechanism. Toxicol. Appl. Pharmacol. 2012, 259, 133–142. [Google Scholar] [CrossRef] [PubMed]
  78. Bhargava, M.; Lei, J.; Ingbar, D.H. Nongenomic actions of L-thyroxine and 3,5,3′-triiodo-L-thyronine. Focus on “L-Thyroxine vs. 3,5,3′-triiodo-L-thyronine and cell proliferation: Activation of mitogen-activated protein kinase and phosphatidylinositol 3-kinase”. Am. J. Physiol. Cell Physiol. 2009, 296, C977–C979. [Google Scholar] [CrossRef] [PubMed][Green Version]
  79. Sheng, Z.; Wang, C.; Ren, F.; Liu, Y.; Zhu, B. Molecular mechanism of endocrine-disruptive effects induced by Bisphenol A: The role of transmembrane G-protein estrogen receptor 1 and integrin αvβ3. J. Environ. Sci. (China) 2019, 75, 1–13. [Google Scholar] [CrossRef] [PubMed]
  80. Zhang, Y.F.; Ren, X.M.; Li, Y.Y.; Yao, X.F.; Li, C.H.; Qin, Z.F.; Guo, L.H. Bisphenol A alternatives bisphenol S and bisphenol F interfere with thyroid hormone signaling pathway in vitro and in vivo. Environ. Pollut. 2018, 237, 1072–1079. [Google Scholar] [CrossRef] [PubMed]
  81. Ghisari, M.; Bonefeld-Jorgensen, E.C. Impact of environmental chemicals on the thyroid hormone function in pituitary rat GH3 cells. Mol. Cell. Endocrinol. 2005, 244, 31–41. [Google Scholar] [CrossRef] [PubMed]
  82. Schriks, M.; Vrabie, C.M.; Gutleb, A.C.; Faassen, E.J.; Rietjens, I.M.C.M.; Murk, A.J. T-screen to quantify functional potentiating, antagonistic and thyroid hormone-like activities of poly halogenated aromatic hydrocarbons (PHAHs). Toxicol. In Vitro 2006, 20, 490–498. [Google Scholar] [CrossRef]
  83. Kitamura, S. Comparative study of the endocrine-disrupting activity of bisphenol a and 19 related compounds. Toxicol. Sci. 2005, 84, 249–259. [Google Scholar] [CrossRef]
  84. Hamers, T.; Kamstra, J.H.; Sonneveld, E.; Murk, A.J.; Kester, M.H.A.; Andersson, P.L.; Legler, J.; Brouwer, A. In vitro profiling of the endocrine-disrupting potency of brominated flame retardants. Toxicol. Sci. 2006, 92, 157–173. [Google Scholar] [CrossRef][Green Version]
  85. Lee, J.; Kim, S.; Choi, K.; Ji, K. Effects of bisphenol analogs on thyroid endocrine system and possible interaction with 17β-estradiol using GH3 cells. Toxicol. In Vitro 2018, 53, 107–113. [Google Scholar] [CrossRef]
  86. Zhang, Y.H.; Wei, F.; Zhang, J.; Hao, L.; Jiang, J.; Dang, L.; Mei, D.; Fan, S.; Yu, Y.; Jiang, L. Bisphenol A and estrogen induce proliferation of human thyroid tumor cells via an estrogen-receptor-dependent pathway. Arch. Biochem. Biophys. 2017, 633, 29–39. [Google Scholar] [CrossRef]
  87. Strack, S.; Detzel, T.; Wahl, M.; Kuch, B.; Krug, H.F. Cytotoxicity of TBBPA and effects on proliferation, cell cycle and MAPK pathways in mammalian cells. Chemosphere 2007, 67, S405–S411. [Google Scholar] [CrossRef] [PubMed]
  88. English, J.; Pearson, G.; Wilsbacher, J.; Swantek, J.; Karandikar, M.; Xu, S.; Cobb, M.H. New insights into the control of MAP kinase pathways. Exp. Cell Res. 1999, 253, 255–270. [Google Scholar] [CrossRef]
  89. Gentilcore, D.; Porreca, I.; Rizzo, F.; Ganbaatar, E.; Carchia, E.; Mallardo, M.; De Felice, M.; Ambrosino, C. Bisphenol A interferes with thyroid specific gene expression. Toxicology 2013, 304, 21–31. [Google Scholar] [CrossRef]
  90. Cao, J.; Guo, L.-H.; Wan, B.; Wei, Y. In vitro fluorescence displacement investigation of thyroxine transport disruption by bisphenol A. J. Environ. Sci. (China) 2011, 23, 315–321. [Google Scholar] [CrossRef]
  91. Ishihara, A.; Sawatsubashi, S.; Yamauchi, K. Endocrine disrupting chemicals: Interference of thyroid hormone binding to transthyretins and to thyroid hormone receptors. Mol. Cell. Endocrinol. 2003, 199, 105–117. [Google Scholar] [CrossRef]
  92. Meerts, I.A.T.M. Potent competitive interactions of some brominated flame retardants and related compounds with human transthyretin in vitro. Toxicol. Sci. 2000, 56, 95–104. [Google Scholar] [CrossRef][Green Version]
  93. Marchesini, G.R.; Meimaridou, A.; Haasnoot, W.; Meulenberg, E.; Albertus, F.; Mizuguchi, M.; Takeuchi, M.; Irth, H.; Murk, A.J. Biosensor discovery of thyroxine transport disrupting chemicals. Toxicol. Appl. Pharmacol. 2008, 232, 150–160. [Google Scholar] [CrossRef]
  94. Dong, H.; Wade, M.G. Application of a nonradioactive assay for high throughput screening for inhibition of thyroid hormone uptake via the transmembrane transporter MCT8. Toxicol. In Vitro 2017, 40, 234–242. [Google Scholar] [CrossRef]
  95. Friesema, E.C.; Kuiper, G.G.; Jansen, J.; Visser, T.J.; Kester, M.H. Thyroid hormone transport by the human monocarboxylate transporter 8 and its rate-limiting role in intracellular metabolism. Mol. Endocrinol. 2006, 20, 2761–2772. [Google Scholar] [CrossRef][Green Version]
  96. Strømme, P.; Groeneweg, S.; Lima de Souza, E.C.; Zevenbergen, C.; Torgersbråten, A.; Holmgren, A.; Gurcan, E.; Meima, M.E.; Peeters, R.; Visser, W.E.; et al. Mutated Thyroid Hormone Transporter OATP1C1 Associates with Severe Brain Hypometabolism and Juvenile Neurodegeneration. Thyroid 2018, 28, 1406–1415. [Google Scholar] [CrossRef][Green Version]
  97. Trajkovic, M.; Visser, T.J.; Mittag, J.; Horn, S.; Lukas, J.; Darras, V.M.; Raivich, G.; Bauer, K.; Heuer, H. Abnormal thyroid hormone metabolism in mice lacking the monocarboxylate transporter 8. J. Clin. Investig. 2007, 117, 627–635. [Google Scholar] [CrossRef] [PubMed][Green Version]
  98. Johannes, J.; Jayarama-Naidu, R.; Meyer, F.; Wirth, E.K.; Schweizer, U.; Schomburg, L.; Köhrle, J.; Renko, K. Silychristin, a Flavonolignan Derived From the Milk Thistle, Is a Potent Inhibitor of the Thyroid Hormone Transporter MCT8. Endocrinology 2016, 157, 1694–1701. [Google Scholar] [CrossRef] [PubMed]
  99. Lee, S.; Kim, C.; Youn, H.; Choi, K. Thyroid hormone disrupting potentials of bisphenol A and its analogues - in vitro comparison study employing rat pituitary (GH3) and thyroid follicular (FRTL-5) cells. Toxicol. In Vitro 2017, 40, 297–304. [Google Scholar] [CrossRef] [PubMed]
  100. Wu, Y.; Beland, F.A.; Fang, J.L. Effect of triclosan, triclocarban, 2,2′,4,4′-tetrabromodiphenyl ether, and bisphenol A on the iodide uptake, thyroid peroxidase activity, and expression of genes involved in thyroid hormone synthesis. Toxicol. In Vitro 2016, 32, 310–319. [Google Scholar] [CrossRef][Green Version]
  101. Porreca, I.; Ulloa Severino, L.; D’Angelo, F.; Cuomo, D.; Ceccarelli, M.; Altucci, L.; Amendola, E.; Nebbioso, A.; Mallardo, M.; De Felice, M.; et al. “Stockpile” of Slight Transcriptomic Changes Determines the Indirect Genotoxicity of Low-Dose BPA in Thyroid Cells. PLoS ONE 2016, 11, e0151618. [Google Scholar] [CrossRef][Green Version]
  102. da Silva, M.M.; Gonçalves, C.F.L.; Miranda-Alves, L.; Fortunato, R.S.; Carvalho, D.P.; Ferreira, A.C.F. Inhibition of Type 1 Iodothyronine Deiodinase by Bisphenol A. Horm. Metab. Res. 2019, 51, 671–677. [Google Scholar] [CrossRef]
  103. Chan, S.; Kachilele, S.; Hobbs, E.; Bulmer, J.N.; Boelaert, K.; McCabe, C.J.; Driver, P.M.; Bradwell, A.R.; Kester, M.; Visser, T.J.; et al. Placental iodothyronine deiodinase expression in normal and growth-restricted human pregnancies. J. Clin. Endocrinol. Metab. 2003, 88, 4488–4495. [Google Scholar] [CrossRef][Green Version]
  104. Zoeller, R.T.; Bansal, R.; Parris, C. Bisphenol-A, an environmental contaminant that acts as a thyroid hormone receptor antagonist in vitro, increases serum thyroxine, and alters RC3/neurogranin expression in the developing rat brain. Endocrinology 2005, 146, 607–612. [Google Scholar] [CrossRef]
  105. Zhang, J.; Zhang, X.; Li, Y.; Zhou, Z.; Wu, C.; Liu, Z.; Hao, L.; Fan, S.; Jiang, F.; Xie, Y.; et al. Low dose of Bisphenol A enhance the susceptibility of thyroid carcinoma stimulated by DHPN and iodine ecxcess in F344 rats. Oncotarget 2017, 8, 69874–69887. [Google Scholar]
  106. Silva, M.M.D.; Xavier, L.L.F.; Gonçalves, C.F.L.; Santos-Silva, A.P.; Paiva-Melo, F.D.; Freitas, M.L.D.; Fortunato, R.S.; Alves, L.M.; Ferreira, A.C.F. Bisphenol A increases hydrogen peroxide generation by thyrocytes both in vivo and in vitro. Endocr. Connect. 2018, 7, 1198–1207. [Google Scholar] [CrossRef][Green Version]
  107. Saegusa, Y.; Fujimoto, H.; Woo, G.H.; Inoue, K.; Takahashi, M.; Mitsumori, K.; Hirose, M.; Nishikawa, A.; Shibutani, M. Developmental toxicity of brominated flame retardants, tetrabromobisphenol A and 1,2,5,6,9,10-hexabromocyclododecane, in rat offspring after maternal exposure from mid-gestation through lactation. Reprod. Toxicol. 2009, 2, 456–467. [Google Scholar] [CrossRef] [PubMed]
  108. Kobayashi, K.; Miyagawa, M.; Wang, R.S.; Suda, M.; Sekiguchi, S.; Honma, T. Effects of in utero and lactational exposure to bisphenol A on thyroid status in F1 rat offspring. Ind. Health 2005, 43, 685–690. [Google Scholar] [CrossRef] [PubMed][Green Version]
  109. Bansal, R.; Zoeller, R.T. CLARITY-BPA: Bisphenol A or Propylthiouracil on Thyroid Function and Effects in the Developing Male and Female Rat Brain. Endocrinology 2019, 160, 1771–1785. [Google Scholar] [CrossRef] [PubMed]
  110. Osimitz, T.G.; Droege, W.; Hayes, A.W. Subchronic toxicology of tetrabromobisphenol A in rats. Hum. Exp. Toxicol. 2016, 35, 1214–1226. [Google Scholar] [CrossRef] [PubMed]
  111. Xu, X.; Fan, S.; Guo, Y.; Tan, R.; Zhang, J.; Zhang, W.; Pan, B.X.; Kato, N. The effects of perinatal bisphenol A exposure on thyroid hormone homeostasis and glucose metabolism in the prefrontal cortex and hippocampus of rats. Brain Behav. 2019, 9, e01225. [Google Scholar] [CrossRef][Green Version]
  112. Xu, X.; Liu, Y.; Sadamatsu, M.; Tsutsumi, S.; Akaike, M.; Ushijima, H.; Kato, N. Perinatal bisphenol A affects the behavior and SRC-1 expression of male pups but does not influence on the thyroid hormone receptors and its responsive gene. Neurosci. Res. 2007, 58, 149–155. [Google Scholar] [CrossRef]
  113. Jiang, W.; Cao, L.; Wang, F.; Ge, H.; Wu, P.C.; Li, X.W.; Chen, G.H. Accelerated reduction of serum thyroxine and hippocampal histone acetylation links to exacerbation of spatial memory impairment in aged CD-1 mice pubertally exposed to bisphenol A. Age (Dordr) 2016, 38, 405–418. [Google Scholar] [CrossRef]
  114. Van der Ven, L.T.M.; Van de Kuil, T.; Verhoef, A.; Verwer, C.M.; Lilienthal, H.; Leonards, P.E.G.; Schauer, U.M.D.; Cantón, R.F.; Litens, S.; De Jong, F.H.; et al. Endocrine effects of tetrabromobisphenol-A (TBBPA) in Wistar rats as tested in a one-generation reproduction study and a subacute toxicity study. Toxicology 2008, 245, 76–89. [Google Scholar] [CrossRef]
  115. Silva, B.S.; Bertasso, I.M.; Pietrobon, C.B.; Lopes, B.P.; Santos, T.R.; Peixoto-Silva, N.; Carvalho, J.C.; Claudio-Neto, S.; Manhães, A.C.; Cabral, S.S.; et al. Effects of maternal bisphenol A on behavior, sex steroid and thyroid hormones levels in the adult rat offspring. Life Sci. 2019, 218, 253–264. [Google Scholar] [CrossRef]
  116. Ahmed, R.G.; Walaa, G.H.; Asmaa, F.S. Suppressive effects of neonatal bisphenol A on the neuroendocrine system. Toxicol. Ind. Health 2018, 34, 397–407. [Google Scholar] [CrossRef]
  117. Fernandez, M.O.; Bourguignon, N.S.; Arocena, P.; Rosa, M.; Libertun, C.; Lux-Lantos, V. Neonatal exposure to bisphenol A alters the hypothalamic-pituitary-thyroid axis in female rats. Toxicol. Lett. 2018, 285, 81–86. [Google Scholar] [CrossRef] [PubMed]
  118. Delclos, K.B.; Camacho, L.; Lewis, S.M.; Vanlandingham, M.M.; Latendresse, J.R.; Olson, G.R.; Davis, K.J.; Patton, R.E.; da Costa, G.G.; Woodling, K.A.; et al. Toxicity Evaluation of Bisphenol A Administered by Gavage to Sprague Dawley Rats From Gestation Day 6 Through Postnatal Day 90. Toxicol. Sci. 2014, 139, 174–197. [Google Scholar] [CrossRef] [PubMed]
  119. Matos, L.P.L.; Penha, R.C.C.; Cardoso-Weide, L.C.; Freitas, M.L.; Silva, D.L.S.G.; Ferreira, A.C.F. Regulation of thyroid sodium-iodide symporter in different stages of goiter: Possible involvement of reactive oxygen species. Clin. Exp. Pharmacol. Physiol. 2018, 45, 326–334. [Google Scholar] [CrossRef] [PubMed]
  120. Fortunato, R.S.; Lima de Souza, E.C.; Ameziane-el Hassani, R.; Boufraqech, M.; Weyemi, U.; Talbot, M.; Lagente-Chevallier, O.; de Carvalho, D.P.; Bidart, J.M.; Schlumberger, M.; et al. Functional consequences of dual oxidase-thyroperoxidase interaction at the plasma membrane. J. Clin. Endocrinol. Metab. 2010, 95, 5403–5411. [Google Scholar] [CrossRef] [PubMed][Green Version]
  121. Yafune, A.; Taniai, E.; Morita, R.; Akane, H.; Kimura, M.; Mitsumori, K.; Shibutani, M. Immunohistochemical cellular distribution of proteins related to M phase regulation in early proliferative lesions induced by tumor promotion in rat two-stage carcinogenesis models. Exp. Toxicol. Pathol. 2014, 66, 1–11. [Google Scholar] [CrossRef] [PubMed]
  122. Viguié, C.; Collet, S.H.; Gayrard, V.; Picard-Hagen, N.; Puel, S.; Roques, B.B.; Toutain, P.L.; Lacroix, M.Z. Maternal and fetal exposure to bisphenol A is associated with alterations of thyroid function in pregnant ewes and their newborn lambs. Endocrinology 2013, 154, 521–528. [Google Scholar] [CrossRef]
  123. Guignard, D.; Gayrard, V.; Lacroix, M.Z.; Puel, S.; Picard-Hagen, N.; Viguié, C. Evidence for bisphenol A-induced disruption of maternal thyroid homeostasis in the pregnant ewe at low level representative of human exposure. Chemosphere 2017, 182, 458–467. [Google Scholar] [CrossRef]
  124. Fisher, D.A.; Polk, D.H.; Wu, S. Fetal thyroid metabolism: A pluralistic system. Thyroid 1994, 4, 367–371. [Google Scholar] [CrossRef]
  125. Marelli, F.; Persani, L. How zebrafish research has helped in understanding thyroid diseases. F1000Res. 2017, 6, 2137. [Google Scholar] [CrossRef][Green Version]
  126. Terrien, X.; Fini, J.B.; Demeneix, B.A.; Schramm, K.W.; Prunet, P. Generation of fluorescent zebrafish to study endocrine disruption and potential crosstalk between thyroid hormone and corticosteroids. Aquat. Toxicol. 2011, 105, 13–20. [Google Scholar] [CrossRef]
  127. Raldúa, D.; Thienpont, B.; Babin, P.J. Zebrafish eleutheroembryos as an alternative system for screening chemicals disrupting the mammalian thyroid gland morphogenesis and function. Reprod. Toxicol. 2012, 33, 188–197. [Google Scholar] [CrossRef] [PubMed]
  128. Zhu, B.; Zhao, G.; Yang, L.; Zhou, B. Tetrabromobisphenol A caused neurodevelopmental toxicity via disrupting thyroid hormones in zebrafish larvae. Chemosphere 2018, 197, 353–361. [Google Scholar] [CrossRef] [PubMed]
  129. Zhang, D.; Zhou, E.; Yang, Z. Waterborne exposure to BPS causes thyroid endocrine disruption in zebrafish larvae. PLoS ONE 2017, 12, e0176927. [Google Scholar] [CrossRef] [PubMed]
  130. Tang, T.; Yang, Y.; Chen, Y.; Tang, W.; Wang, F.; Diao, X. Thyroid Disruption in Zebrafish Larvae by Short-Term Exposure to Bisphenol AF. Int. J. Environ. Res. Public Health 2015, 12, 13069–13084. [Google Scholar] [CrossRef] [PubMed][Green Version]
  131. Naderi, M.; Wong, M.Y.L.; Gholami, F. Developmental exposure of zebrafish (Danio rerio) to bisphenol-S impairs subsequent reproduction potential and hormonal balance in adults. Aquat. Toxicol. 2014, 148, 195–203. [Google Scholar] [CrossRef] [PubMed]
  132. Baumann, L.; Ros, A.; Rehberger, K.; Neuhauss, S.C.F.; Segner, H. Thyroid disruption in zebrafish (Danio rerio) larvae: Different molecular response patterns lead to impaired eye development and visual functions. Aquat. Toxicol. 2016, 172, 44–55. [Google Scholar] [CrossRef]
  133. Chan, W.K.; Chan, K.M. Disruption of the hypothalamic-pituitary-thyroid axis in zebrafish embryo–larvae following waterborne exposure to BDE-47, TBBPA and BPA. Aquat. Toxicol. 2012, 108, 106–111. [Google Scholar] [CrossRef]
  134. Kwon, B.; Kho, Y.; Kim, P.G.; Ji, K. Thyroid endocrine disruption in male zebrafish following exposure to binary mixture of bisphenol AF and sulfamethoxazole. Environ. Toxicol. Pharmacol. 2016, 48, 168–174. [Google Scholar] [CrossRef]
  135. Berto-Júnior, C.; Santos-Silva, A.P.; Ferreira, A.C.F.; Graceli, J.B.; de Carvalho, D.P.; Soares, P.; Romeiro, N.C.; Miranda-Alves, L. Unraveling molecular targets of bisphenol A and S in the thyroid gland. Environ. Sci. Pollut. Res. Int. 2018, 25, 26916–26926. [Google Scholar] [CrossRef]
  136. Liang, Y.Q.; Huang, G.Y.; Ying, G.G.; Liu, S.S.; Jiang, Y.X.; Liu, S. Progesterone and norgestrel alter transcriptional expression of genes along the hypothalamic–pituitary–thyroid axis in zebrafish embryos-larvae. Comp. Biochem. Physiol. C Toxicol. Pharmacol. 2015, 167, 101–107. [Google Scholar] [CrossRef]
  137. Bianco, A.C.; Salvatore, D.; Gereben, B.Z.; Berry, M.J.; Larsen, P.R. Biochemistry, cellular and molecular biology, and physiological roles of the iodothyronine selenodeiodinases. Endocr. Rev. 2002, 23, 38–89. [Google Scholar] [CrossRef] [PubMed]
  138. Lévy-Bimbot, M.; Major, G.; Courilleau, D.; Blondeau, J.P.; Lévi, Y. Tetrabromobisphenol-A disrupts thyroid hormone receptor alpha function in vitro: Use of fluorescence polarization to assay corepressor and coactivator peptide binding. Chemosphere 2012, 87, 782–788. [Google Scholar] [CrossRef] [PubMed]
  139. Aung, M.T.; Johns, L.E.; Ferguson, K.K.; Mukherjee, B.; McElrath, T.F.; Meeker, J.D. Thyroid hormone parameters during pregnancy in relation to urinary bisphenol A concentrations: A repeated measures study. Environ. Int. 2017, 104, 33–40. [Google Scholar] [CrossRef] [PubMed]
  140. Kim, U.J.; Oh, J.E. Tetrabromobisphenol A and hexabromocyclododecane flame retardants in infant–mother paired serum samples, and their relationships with thyroid hormones and environmental factors. Environ. Pollut. 2014, 184, 193–200. [Google Scholar] [CrossRef]
  141. Wang, F.; Hua, J.; Chen, M.; Xia, Y.; Zhang, Q.; Zhao, R.; Zhou, W.; Zhang, Z.; Wang, B. High urinary bisphenol A concentrations in workers and possible laboratory abnormalities. Occup. Environ. Med. 2012, 69, 679–684. [Google Scholar] [CrossRef]
  142. Przybyla, J.; Geldhof, G.J.; Smit, E.; Kile, M.L. A cross sectional study of urinary phthalates, phenols and perchlorate on thyroid hormones in US adults using structural equation models (NHANES 2007–2008). Environ. Res. 2018, 163, 26–35. [Google Scholar] [CrossRef]
  143. Chevrier, J.; Gunier, R.B.; Bradman, A.; Holland, N.T.; Calafat, A.M.; Eskenazi, B.; Harley, K.G. Maternal urinary bisphenol A during pregnancy and maternal and neonatal thyroid function in the CHAMACOS study. Environ. Health Perspect. 2013, 121, 138–144. [Google Scholar] [CrossRef]
  144. Sriphrapradang, C.; Chailurkit, L.; Aekplakorn, W.; Ongphiphadhanakul, B. Association between bisphenol A and abnormal free thyroxine level in men. Endocrine 2013, 44, 441–447. [Google Scholar] [CrossRef]
  145. Meeker, J.D.; Ferguson, K.K. Relationship between urinary phthalate and bisphenol A concentrations and serum thyroid measures in U.S. adults and adolescents from the National Health and Nutrition Examination Survey (NHANES) 2007–2008. Environ. Health Perspect. 2011, 119, 1396–1402. [Google Scholar] [CrossRef]
  146. Minatoya, M.; Sasaki, S.; Araki, A.; Miyashita, C.; Itoh, S.; Yamamoto, J.; Matsumura, T.; Mitsui, T.; Moriya, K.; Cho, K.; et al. Cord Blood Bisphenol A Levels and Reproductive and Thyroid Hormone Levels of Neonates. Epidemiology 2017, 28, S3–S9. [Google Scholar] [CrossRef][Green Version]
  147. Andrianou, X.D.; Gängler, S.; Piciu, A.; Charisiadis, P.; Zira, C.; Aristidou, K.; Piciu, D.; Hauser, R.; Makris, K.C. Human Exposures to Bisphenol A, Bisphenol F and Chlorinated Bisphenol A Derivatives and Thyroid Function. PLoS ONE 2016, 11, e0155237. [Google Scholar] [CrossRef] [PubMed]
  148. Romano, M.E.; Webster, G.M.; Vuong, A.M.; Thomas Zoeller, R.; Chen, A.; Hoofnagle, A.N.; Calafat, A.M.; Karagas, M.R.; Yolton, K.; Lanphear, B.P.; et al. Gestational urinary bisphenol A and maternal and newborn thyroid hormone concentrations: The HOME study. Environ. Res. 2015, 138, 453–460. [Google Scholar] [CrossRef] [PubMed][Green Version]
  149. Wang, T.; Lu, J.; Xu, M.; Xu, Y.; Li, M.; Liu, Y.; Tian, X.; Chen, Y.; Dai, M.; Wang, W.; et al. Urinary bisphenol A concentration and thyroid function in Chinese adults. Epidemiology 2013, 24, 295–302. [Google Scholar] [CrossRef] [PubMed]
  150. Meeker, J.D.; Calafat, A.M.; Hauser, R. Urinary Bisphenol A Concentrations in relation to serum thyroid and reproductive hormone levels in men from an infertility clinic. Environ. Sci. Technol. 2010, 44, 1458–1463. [Google Scholar] [CrossRef] [PubMed][Green Version]
  151. Sugiura-Ogasawara, M.; Ozaki, Y.; Sonta, S.; Makino, T.; Suzumori, K. Exposure to bisphenol A is associated with recurrent miscarriage. Hum. Reprod. 2005, 20, 2325–2329. [Google Scholar] [CrossRef] [PubMed][Green Version]
  152. Geens, T.; Dirtu, A.C.; Dirinck, E.; Malarvannan, G.; Van Gaal, L.; Jorens, P.G.; Covaci, A. Daily intake of bisphenol A and triclosan and their association with anthropometric data, thyroid hormones and weight loss in overweight and obese individuals. Environ. Int. 2015, 76, 98–105. [Google Scholar] [CrossRef]
  153. Takeuchi, T.; Tsutsumi, O.; Nakamura, N.; Ikezuki, Y.; Takai, Y.; Yano, T.; Taketani, Y. Gender difference in serum bisphenol A levels may be caused by liver UDP-glucuronosyltransferase activity in rats. Biochem. Biophys. Res. Commun. 2004, 325, 549–554. [Google Scholar] [CrossRef]
  154. Takeuchi, T.; Tsutsumi, O. Serum bisphenol A concentrations showed gender differences, possibly linked to androgen levels. Biochem. Biophys. Res. Commun. 2002, 291, 76–78. [Google Scholar] [CrossRef]
  155. Sur, U.; Erkekoglu, P.; Bulus, A.D.; Andiran, N.; Kocer-Gumusel, B. Oxidative stress markers, trace elements and endocrine disrupting chemicals in children with Hashimoto’s thyroiditis. Toxicol. Mech. Methods 2019, 29, 1–30. [Google Scholar] [CrossRef]
  156. Chailurkit, L.; Aekplakorn, W.; Ongphiphadhanakul, B. The Association of Serum Bisphenol A with Thyroid Autoimmunity. Int. J. Environ. Res. Public Health 2016, 13, 1153. [Google Scholar] [CrossRef][Green Version]
  157. American Thyroid Association (ATA) Guidelines Taskforce on Thyroid Nodules and Differentiated Thyroid Cancer; Cooper, D.S.; Doherty, G.M.; Haugen, B.R.; Kloos, R.T.; Lee, S.L.; Mandel, S.J.; Mazzaferri, E.L.; McIver, B.; Pacini, F.; et al. Revised American Thyroid Association management guidelines for patients with thyroid nodules and differentiated thyroid cancer. Thyroid 2009, 19, 1167–1214. [Google Scholar] [CrossRef] [PubMed][Green Version]
  158. Wang, N.; Zhou, Y.; Fu, C.; Wang, H.; Huang, P.; Wang, B.; Su, M.; Jiang, F.; Fang, H.; Zhao, Q.; et al. Influence of Bisphenol A on Thyroid Volume and Structure Independent of Iodine in School Children. PLoS ONE 2015, 10, e0141248. [Google Scholar] [CrossRef] [PubMed][Green Version]
  159. Li, L.; Ying, Y.; Zhang, C.; Wang, W.; Li, Y.; Feng, Y.; Liang, J.; Song, H.; Wang, Y. Bisphenol A exposure and risk of thyroid nodules in Chinese women: A case-control study. Environ. Int. 2019, 126, 321–328. [Google Scholar] [CrossRef] [PubMed]
  160. Zhou, Z.; Zhang, J.; Jiang, F.; Xie, Y.; Zhang, X.; Jiang, L. Higher urinary bisphenol A concentration and excessive iodine intake are associated with nodular goiter and papillary thyroid carcinoma. Biosci. Rep. 2017, 37, BSR20170678. [Google Scholar] [CrossRef][Green Version]
  161. Marotta, V.; Russo, G.; Gambardella, C.; Grasso, M.; La Sala, D.; Chiofalo, M.G.; D’Anna, R.; Puzziello, A.; Docimo, G.; Masone, S.; et al. Human exposure to bisphenol AF and diethylhexylphthalate increases susceptibility to develop differentiated thyroid cancer in patients with thyroid nodules. Chemosphere 2019, 218, 885–894. [Google Scholar] [CrossRef]
  162. Puzianowska-Kuznicka, M.; Nauman, A.; Madej, A.; Tanski, Z.; Cheng, S.; Nauman, J. Expression of thyroid hormone receptors is disturbed in human renal clear cell carcinoma. Cancer Lett. 2000, 155, 145–152. [Google Scholar] [CrossRef]
  163. Chen, Q.; Yu, L.; Yang, L.; Zhou, B. Bioconcentration and metabolism of decabromodiphenyl ether (BDE-209) result in thyroid endocrine disruption in zebrafish larvae. Aquat. Toxicol. 2012, 110–111, 141–148. [Google Scholar] [CrossRef]
  164. Jia, P.P.; Ma, Y.B.; Lu, C.J.; Mirza, Z.; Zhang, W.; Jia, Y.F.; Li, W.G.; Pei, D.S. The Effects of Disturbance on Hypothalamus-Pituitary-Thyroid (HPT) Axis in Zebrafish Larvae after Exposure to DEHP. PLoS ONE 2016, 11, e0155762. [Google Scholar] [CrossRef]
  165. Arnaldi, L.A.; Borra, R.C.; Maciel, R.M.; Cerutti, J.M. Gene expression profiles reveal that DCN, DIO1, and DIO2 are underexpressed in benign and malignant thyroid tumors. Thyroid 2005, 15, 210–221. [Google Scholar] [CrossRef]
  166. Li, C.G.; Nyman, J.E.; Braithwaite, A.W.; Eccles, M.R. PAX8 promotes tumor cell growth by transcriptionally regulating E2F1 and stabilizing RB protein. Oncogene 2011, 30, 4824–4834. [Google Scholar] [CrossRef][Green Version]
  167. Zhang, X.; Tian, H.; Wang, W.; Ru, S. Exposure to monocrotophos pesticide causes disruption of the hypothalamic–pituitary–thyroid axis in adult male goldfish (Carassius auratus). Gen. Comp. Endocrinol. 2013, 193, 158–166. [Google Scholar] [CrossRef]
  168. Latina, A.; Gullo, D.; Trimarchi, F.; Benvenga, S. Hashimoto’s thyroiditis: Similar and dissimilar characteristics in neighboring areas. Possible implications for the epidemiology of thyroid cancer. PLoS ONE 2013, 8, e55450. [Google Scholar] [CrossRef] [PubMed]
  169. Lai, X.; Xia, Y.; Zhang, B.; Li, J.; Jiang, Y. A meta-analysis of Hashimoto’s thyroiditis and papillary thyroid carcinoma risk. Oncotarget 2017, 8, 62414–62424. [Google Scholar] [CrossRef] [PubMed][Green Version]
  170. Ginabreda, M.G.P.; Cardoso, L.C.; Nobrega, F.M.; Ferreira, A.C.F.; Gonçalves, M.D.C.; Vaisman, M.; Carvalho, D.P. Negative correlation between thyroperoxidase and dual oxidase H2O2-generating activities in thyroid nodular lesions. Eur. J. Endocrinol. 2008, 158, 223–227. [Google Scholar] [CrossRef] [PubMed][Green Version]
  171. Wang, F.; Wang, Y.; Wang, L.; Wang, X.; Sun, C.; Xing, M.; Zhao, W. Strong association of high urinary iodine with thyroid nodule and papillary thyroid cancer. Tumour Biol. 2014, 35, 11375–11379. [Google Scholar] [CrossRef]
  172. Guan, H.; Ji, M.; Bao, R.; Yu, H.; Wang, Y.; Hou, P.; Zhang, Y.; Shan, Z.; Teng, W.; Xing, M. Association of High Iodine Intake with the T1799A BRAF Mutation in Papillary Thyroid Cancer. J. Clin. Endocrinol. Metab. 2009, 94, 1612–1617. [Google Scholar] [CrossRef]
  173. Filetti, S.; Bidart, J.; Arturi, F.; Caillou, B.; Russo, D.; Schlumberger, M. Sodium/iodide symporter: A key transport system in thyroid cancer cell metabolism. Eur. J. Endocrin. 1999, 141, 443–457. [Google Scholar] [CrossRef][Green Version]
Figure 1. Bisphenol A, its analogues bisphenol F and bisphenol S, and the halogenated derivatives tetrabromobisphenol A and tetrachlorobisphenol A show a high degree of similarity with the thyroid hormones in regards the chemical structure.
Figure 1. Bisphenol A, its analogues bisphenol F and bisphenol S, and the halogenated derivatives tetrabromobisphenol A and tetrachlorobisphenol A show a high degree of similarity with the thyroid hormones in regards the chemical structure.
Ijerph 17 02654 g001
Table 1. Concentration of bisphenols in the environment and human body, and estimated exposure by age groups to bisphenol A (a), principal bisphenol A substitutes (b), and halogenated derivatives of bisphenol A (c).
Table 1. Concentration of bisphenols in the environment and human body, and estimated exposure by age groups to bisphenol A (a), principal bisphenol A substitutes (b), and halogenated derivatives of bisphenol A (c).
(a) Bisphenol A
Environmental MatrixConcentrationReference
Surface waternd-1.95 µg/L[47]
Sediments (industrialized areas)nd-13,370 µg/kg dry weight[41]
Soil<0.01–1000 µg/kg[29]
Indoor dustnd-39.1 µg/g[48]
Atmosphere10−3–1.74 ng/m3[49]
Landfill leachate (hazardous waste site)Up to 17,200 µg/L[50]
Human BodyConcentrationReference
BrainMean: 0.91 ng/g[51]
LiverMean: 1.30 ng/g[5]
Adipose tissueMean: 3.78 ng/g[51]
Breast milkMean: 0.61 µg/L[52]
Blood (adults)Mean: 0.20 µg/L[36]
Cord bloodMean: 0.13 µg/L[36]
Urine (European adult population)Geometric mean: 2.5–3.6 µg/L[31]
Urine (North America children)Geometric mean: 1.3–3.7 µg/L[31]
Urine (North America adults)Geometric mean: 1.0–2.6 µg/L[31]
Age Group/Source of ExposureAverage External ExposureReference
Infants (0–3 month)/Formula fed from polycarbonate bottles2.4 µg/kg/day[53]
Infants (0–6 month)/Formula fed from non- polycarbonate bottles0.03 µg/kg/day[31]
Infants (6–12 month) and toddlers (12–36 month)/Diet0.375 µg/kg/day[31]
Infants (6–12 month) and toddlers (12–36 month)/Oral dust and toys0.007–0.009 µg/kg/day[31]
Infants (0–12 month) and toddlers (12–36 month)/Inhalation0.7 µg/kg/day[31]
General population (>3 years)/Diet0.116–0.290 μg/kg/day[31]
General population (>3 years)/Thermal paper0.059–0.094 µg/kg/day[31]
General population (>3 years)/Cosmetics0.002 µg/kg/day[31]
General population (>3 years)/Inhalation0.2–0.4 µg/kg/day[31]
(b) Principal Bisphenol A Substitutes
Environmental MatrixConcentrationReference
Surface water (BPF)nd-2.850 µg/L[47]
Sediments in industrialized areas (BPF)nd-9650 µg/kg dry weight[41]
Indoor dust (sum of several bisphenols including BPF, BPS, BPZ)0.00083–26.6 μg/g[49]
Human BodyConcentrationReference
Urine (BPS: general population—USA/Asian countries)Geometric mean: 0.030–1.18 µg/L[54]
Age GroupEstimated ExposureReference
Children and adolescents (<20 years)—USA/Asian countries (BPS)Median: 0.009 μg/kg/day[54]
Adults (≥20 years) – USA/Asian countries (BPS)Median: 0.004 μg/kg/day[54]
(c) Tetrabromobisphenol A
Environmental MatrixConcentrationReference
Atmosphere (e-waste dismantling site)66.01–95.04 ng/m3[55]
Indoor dust42.21–46,191 ng/g dry weight[46]
SedimentsUp to 518 ng/g[56]
Soil (industrialized areas)1.64–7758 ng/g dry weight[57]
Surface water0.85–4.87 μg/L[56]
Human BodyConcentrationReference
Breast milk4.110 ng/g lipid weight[58]
Cord serumMean: 0.199 ng/g fresh weight[58]
Age group/Source of ExposureAverage External ExposureReference
Infants/Breast-feeding<0.00018–0.171 μg/kg/day[59]
Infants/Dust ingestion (e-waste recycling site)0.00031–0.054 μg/kg/day[46]
Adults/Dust ingestion (e-waste recycling site)0.00004–0.0075 μg/kg/day[46]
Adults/High fish consumers0.00026 μg/kg/day[59]
Table 2. Summary of in vitro studies analyzing effects of bisphenols on thyroid hormoneresponsive cell lines.
Table 2. Summary of in vitro studies analyzing effects of bisphenols on thyroid hormoneresponsive cell lines.
SpeciesModelMethodExposure TimeDoses TestedPrincipal ResultsReference
Interference with T3 transcriptional Activity
Yeast (Saccharomyces
cerevisiae Y190)
Yeast cellsRecombinant two-hybrid yeast assay2.5 h0.005 nM–50 μM BPA/BPS/TBBPA/TBBPS ±10−4 M T3Antagonistic activity of BPs toward TRβ in a dose-dependent manner, with TBBPS showing the strongest antagonistic activity.
IC10 BPA = 884 ± 65.3 nM
IC10 BPS = 312 ± 25.9 nM
IC10 TBBPA = 21.1 ± 9.6 nM
IC10 TBBPS = 10.1 ± 5.1 nM
[68]
Yeast (Saccharomyces
cerevisiae Y190)
Yeast cellsYeast two-hybrid assay4 h10−8–10−4 M BPA/TCBPA/TBBPA
± rat liver S9 preparation
Agonistic activity of TBBPA toward TRα with a dose-dependent response curve. After exposure to S9 metabolic activation, increase of agonistic activity of TBBPA and TCBPA. No activity of BPA.[69]
0/1.6*10−7/8*10−7/4*10−6/2*10−5 M BPA/TCBPA/TBBPA ±100 nM T3 ± rat liver S9 preparationWith T3, significant antagonistic activity of TBBPA and TCBPA toward TRα, enhanced by exposure to S9 metabolic activation at the same concentration.
Zebrafish
(Danio rerio)
Hepatocyte
(ZFL cells)
Luciferase reporter gene assay24 h5/10/25/37.5% LC50 BPA/TBBPANo induction of TR transcriptional activity by BPA or TBBPA alone.[75]
1/2.5/5/10/25% LC50 BPA/TBBPA +0.1 nM T3With T3, decrease of transcriptional activity by BPA.
Amphibian (Xenopus laevis)Tadpole tail cultureSemi-quantitative RT-PCR5 days10−7–10−5 M BPAInhibition of Trα and Trβ mRNA expression with a greater effect on the expression of Trβ than Trα. Moderate suppression of RXRγ mRNA expression.[66]
10−5 M ±2.5*10−8/10−7/4*10−7 T3T3 counteracts the inhibitory effects of BPA on Trα and Trβ mRNA expression, and, in the case of Trβ, dose-dependently. Dose-dependent suppressive effect of T3 on RXRγ gene expression independently of the presence of BPA.
Amphibian (Xenopus
laevis)
XL58-TRE-Luc
cells
Luciferase reporter gene assay24 h10−8–10−6 M BPA/TBBPA ±2 nM T3With T3, inhibition of transcription in a dose-dependent manner. In the absence of T3, agonistic activity.[70]
Amphibian
(Xenopus laevis)
XL58-TRE-Luc
cells
Luciferase reporter gene assay24 h0/10−8–10−6 TBBPA ±2 nM T3With T3, inhibition of transcription in a dose-dependent manner.[74]
Chinese hamsterOvary
(CHO-K1 cells)
Luciferase reporter gene assay24 h10−10–10−4 M BPA/TBBPA/TCBPASuppression of transcription in cell transfected with TRα1 or TRβ1 by both TBBPA and TCBPA[10]
0/3.1/6.3/13/25/50/100 µM TBBPA/TCBPA +10 nM T3With T3, inhibition of transcriptional activities by TBBPA and TCBPA/
MouseCerebellum
(C17.α cells)
Luciferase reporter gene assay24 h0/10−9–10−5 M TBBPA ±0.1/1/10
nM T3
Antagonistic effect at least in part independent from T3 concentration.[64]
MouseOligodendrocyte precursors cellsStimulation/inhibition48 h0/10−5 M BPA ±100 nM T3No variation in TRα levels; TRβ1 levels significantly decreased compared to controls.[67]
RatAdrenal medulla
pheochromocytoma
(PC12 cells)
Luciferase reporter gene assay16 h0/10/20/40/60/100 µM TBBPA
±1/100 nM T3
Agonistic activity in the absence of T3. With 1 nM T3, antagonistic activity counteracted by large excess of T3.[65]
RatThyroid pituitary
tumor (GH3 cells)
Luciferase reporter gene assay24 h0–500 µM BPA/0–100 µM TBBPA/TCBPA ±0.25 nM T3With T3, slight induction of luciferase activity at doses up to 1 µM. Without T3, no effect from TBBPA and TCBPA.[76]
0.25 nM T3 ±0/0.5/1/5/10/15 µM AMAM induced T3-mediated response up to 1 µM.
RatThyroid pituitary
tumor (GH3 cells)
Luciferase reporter gene assay24 h0/0.1/1/5/10/50 µM BPA/BPS/BPF ±1 nM T3Agonistic activity of all chemicals on TH signaling in the absence of T3 and of BPA and BPF in the presence of T3.[80]
African green monkey
(Cerchopitecus aethiops)
Kidney
(CV-1 cells)
Luciferase reporter gene assay24 h10−6–10−4 M TBBPA/TCBPA/BPA
+10 nM T3
With T3, antagonistic activity in cells transfected with TRβ1. In the absence of T3, no effects of the three chemicals.[73]
African green monkey
(Cerchopitecus aethiops)
Kidney
(CV-1 cells)
Luciferase reporter gene assayn.d.10−9–10−7 M BPA ±0.1 nM T3With T3, suppression of TR-mediated transcription also in the presence of SRC1. No effects of BPA on transcription in the absence of T3.[77]
Mammalian two-hybrid assayn.d.10−8 M BPA ±0.1 nM T3No effects of BPA on T3-mediated binding of SRC1 to TRβ1.
10−9–10−7 M BPA ±0.1 nM T3/±10 nM T4Transcription activated by increasing concentrations of BPA in the presence of both T3/T4 and NCor/SMRT1.
10−8 M BPA ±0.1 nM T3/±10 nM T4Overexpression of either β-integrin or c-Src reduced recruitment of N-CoR or SMRT to TR-β1 stimulated by BPA in the presence of T3/T4.
HumanHepatoblastoma
(HpeG2 cells)
Luciferase reporter gene assay
Mammalian two-hybrid
assay
24 h10−9/10−7/10−5 M BPA +10 nM T3With T3, dose-dependent inhibition of transcription mediated by native TRα1 and TRβ1.[2]
n.d.10−9/10−7/10−5 M BPA ±1/3/6 nM T3Enhancement of interaction of TRs with N-CoR in a dose-dependent manner.
HumanHepatocarcinoma
(HepG2 cells)
Luciferase reporter gene assay24 h10−11–10−5 M TBBPA ±1 nM T3Activation of expression in the absence of T3 and antagonistic effect with T3 at the same dose (10−4M).[72]
qRT-PCR24 h10−5 M TBBPA ±1 nM T3Antagonistic effect on T3-induced DIO1 expression.
HumanEmbryonic kidney
(HEK293 cells)
Luciferase reporter gene assay24 h0, 10−9–10−5 M TBBPA ±0.1/1/10
nM T3
Antagonistic effect stronger at lower T3 concentration.[64]
Cell Proliferation
RatThyroid pituitary
tumor (GH3 cells)
WST-1 cell proliferation assay48/96 h10−9–10−6 M BPA/BPAF/BPAP/BPB
/BPC/BPF/BPM/BPP/BPS/BPZ
±6.4*10−10 M T3-EC50
All BPA analogues alone stimulated cell proliferation at the highest concentration. BPAF had the strongest effect. With T3, inhibition of cell proliferation at 48 h; agonistic effects at 96 h by high doses of BPA, BPAF, BPF, BPS, BPZ.[85]
10−9–10−6 M BPA/BPAF
±10−12 M E2/±6.4*10−10 M T3-EC50
Additive like-effects of co-treatment with BPA analogues and E2. With T3, inhibition of analogues alone and enhancement of cell proliferation by co-treatment with E2.
RatThyroid pituitary
tumor (GH3 cells)
WST-1 cell proliferation assay7 days10−8–10−4 M TTBPA/TCBPA ±0.1/1 nM T3Stimulation of cell growth and, with T3, no inhibition of induction of GH3 cell growth.[71]
GH-production assay48 h10−8–10−4 M TTBPA/TCBPAStimulation of GH release from cells.
RatThyroid pituitary
tumor (GH3 cells)
GH production assay48 h10−8–10−5 M BPA/TTBPA/TCBPAStimulation of GH release from cells by only TTBPA and TCBPA. With T3, no inhibition of cell growth.[83]
RatThyroid pituitary
tumor (GH3 cells)
T-screen assayn.d.0/0.1/1/5/10/50 µM BPA/BPS/BPF ±1 nM T3 ±2 µM AMFor all chemicals, induction of cell proliferation only with T3, and inhibition of growth in the absence of T3. Agonistic actions of BPs were antagonized by AM.[80]
RatThyroid pituitary
tumor (GH3 cells)
T-screen assay6 days10−8–10−5 M BPA/BPA-DM/TBBPA
±0.5 nM T3
Stimulation of growth by all tested chemicals. In presence of T3, potentiating effect on T3-induced growth.[81]
0.5/1 nM T3; 5*10−7–5*10−6 BPA/BPA-DM;
1*10−5/2.5*10−5 M TBBPA ±1 nM ICI
Suppression of induced cell proliferation by the antiestrogen ICI. None of the compounds able to counteract the inhibitory effects of ICI.
RatThyroid pituitary
tumor (GH3 cells)
T-screen assay96 h10−7–10−5 M BPA/TBBPA/TCBPA
±0.25 nM T3
No effects on growth for all compounds in the absence of T3. With T3, BPA stimulated growth with maximum potentiation at 10−6M, then cytotoxicity.[82]
RatThyroid pituitary
tumor (GH3 cells)
T-screen assay96 h10−12–10−6 M TBBPA ±0.25 nM T3With T3, potentiation of T3-mediated cell growth. In the absence of T3, no effects on cell proliferation.[84]
HumanPTC
(BHP10-3 cells)
Cell Counting Kit-824/48/72 h10−8–10−3 M BPA
10−9–10−4 M E2
Similar proliferative effects of BPA and E2 with non monotonic dose-response curve and progressive effects over time.[86]
Cytotoxicity
Zebrafish
(Danio rerio)
Hepatocyte
(ZFL cells)
Fluorescence
(AlamarBlueTM assay)
24/96 h0/10–1000 µM BPA24 h LC50 of BPA: 367.1 µM
96 h LC50 of BPA: 357.6 µM
[75]
0/3.16/10 µM TBBPA24 h LC50 of TBBPA: 4 µM
96 h LC50 of TBBPA: 4.2 µM
Amphibian (Xenopus laevis)XL58-TRE-Luc
cells
Cell Count Reagent SF kit48 h0/0.5/1/2/4/8/16 µM BPA/TBBPACell viability not compromised up to 4 µM for both chemicals.[70]
Chinese hamsterOvary
(CHO-K1 cells)
EGFP fluorescence24 h0/3.1/6.3/13/25/50/100 µM TBBPA/TCBPA +10 nM T3Cytotoxicity at the highest concentrations tested for all chemicals.[10]
African green monkey
(Cerchopitecus aethiops
Kidney
(CV−1 cells)
MTT assay24 h1/10/20/50/100 µM TBBPA/TCBPA/BPA
±10 nM T3
Cytotoxicity of all chemicals at the highest concentration tested in the absence and in the presence of T3.[73]
RatAdrenal medulla
pheochromocytoma
(PC12 cells)
MTT assay16 h100 µM TBBPA/TCBPANo significant effects on cell viability.[65]
RatThyroid pituitary
tumor (GH3 cells)
Fluorescence (AlamarBlueTM) assay4 h0–500 µM BPA/0–100 µM TBBPA/TCBPA ±0.25 nM T3At doses >10 µM TBBPA and TCBPA or 100 µM BPA visible cytotoxicity.[76]
RatImmortalized
thyroid
follicular cells
(FRTL-5 cells)
MTT-assay24/72 h10−9–10−4 M BPANo effects on cell survival at any dose at either 1 day or 3 days of treatment.[79]
HumanThyroid anaplastic
carcinoma
(Cal-62 cells)
MTT assay
(on each cell type)
24 h0/25/50/75/100/150/200 µM BPA/TBBPATBBPA EC50
Cal 62 cells: 200 µM
A549 cells: 168 µM
NRK cells: 52 µM
No toxic effects of BPA in the tested concentration range.
[87]
RatKidney epithelial
(NRK cells)
HumanEpithelial alveolar
type II-like lung
(A549 cells)
DNA synthesis by BrdU-assay
(on each cell type)
24/48/72/
96/120 h
0/25/50/75/100/150/200 µM TBBPA
±10 µM U0126
NRK cells the most sensitive to TBBPA (decreased growth at >10 µM). In Cal-62 cells, significant inhibition of growth after 24 exposure to TBBPA >100 µM or 10 µM U0126.
Competitive Binding With Thyroid Hormone Binding Proteins
Amphibian (Xenopus
laevis)
XL58-TRE-Luc
cells
TTR and TR competitive binding assay1–1.5 h10−10–10−5 M BPA/TBBPA +0.1 nM 125I-T3Inhibition of T3 binding to TTR (TBBPA IC50 = 3.7+0.29 nM; BPA IC50 = 1670+30 nM) and, with weaker affinity, to TR.[70]
Chinese hamsterOvary
(CHO-K1 cells)
Competitive binding assay40 min.10−7–10−4 M BPA/TTBPA/TCBPA
+0.1 nM 125I-T3
Inhibition of binding to TR (IC50TBBPA = 3.5 µM; IC50TCBPA = 9.5 µM).[10]
RatThyroid pituitary
(MtT/E-2 cells)
Competitive binding assay40 min.10−7–10−4 M TTBPA/TCBPA;
10−5–10−4 M BPA +0.1 nM 125I-T3
Inhibition of T3 binding to TR by TBBPA and TCBPA. Little effect by BPA.[71]
RatThyroid pituitary
tumor (GH3 cells)
T4-TTR competition binding assayOvernight1 nM–1 µM TBBPA
+ 55 nM (125 I-T4+T4)
Potent antagonism with T4 in TTR binding. IC50 = 0.031 µM.[85]
RatLiver microsomesT4-TTR competition binding assayOvernight1.95–500 nM TBBPA/TCBPA
+ 55 nM (125I-T4+T4)
For TBBPA, maximum displacement (96.5%) of T4 from TTR at 500 nM. IC50 = 7.7 ± 0.9 nM[92]
Perturbation of Thyroid Hormone Uptake
DogKidney tubule
(MDCK cells)
MCT8HTS assay10 min.2/4/8/18/32/62/125/250 µM BPA
+ 3.3 µM T3
Inhibition of T3 uptake mediated by MCT8.[94]
MousePrimary astrocytesNonradioactive uptake assay15 min.10 µM BPA + 10 µM T3Decrease in MCT8-mediated T3 uptake.[98]
Dysregulation of Gene Expression
Zebrafish
(Danio rerio)
Hepatocyte
(ZFL cells)
qRT-PCR24 h10/25/50% LC50 BPA/TBBPAInhibition of expression of Dio1, Dio3, Trb, Sult1-st1, -st2, -st3, -st-5 and Ugt2a1, and induction of Ugt1ab genes by BPA. Inhibition of expression of Dio3, and up-regulation of Ttr, Sult1-st2, sult1-st5, and Ugt2a1 by TBBPA.[75]
Amphibian (Xenopus laevis)Tadpole tail cultureSemi-quantitative RT-PCR5 days10−7–10−5 M BPA ±2.5*10−8/10−7/4*10−7 T3Inhibition of Trα and Trβ mRNA expression. T3 counteracts the inhibitory effects of BPA on Trα and Trβ mRNA expression dose-dependently.[66]
RatLiver and brown
adipose tissue
Deiodinase 1 assay1 h0/0.005/0.05/0.5/5 mmol/L BPAInhibition of both hepatic DIO1 and brown adipose tissue DIO2 activities, with a greater effect on DIO1.
IC50 (D1 activity) = 0.183 mmol/L
IC50 (D2 activity) = 1.11 mmol
[102]
Deiodinase 2 assay3 h
RatThyroid pituitary
tumor (GH3 cells)
qRT-PCR48 h10−9–10−6 M BPA/BPAF ±10−12 M E2Inhibition of transcription of Tshβ, Trα, and Trβ, Dio1 and Dio2. With E2, a more pronounced decrease of Trα, Trβ and Dio2, and increase of Tshβ transcription[85]
RatImmortalized
thyroid follicular
cells
(FRTL-5 cells)
qRT-PCR24 h0/1/10/100 mg/LBPA/BPB/BPF/BPS
0/0.1/1/10 mg/L BPAF/BPAP/BPC/BPM/BPP/BPZ
Stimulation of transcription of Tsh-r, Pax8, Nkx2-1, S lc5a5, Tg, Tpo by BPA, BPAF, BPAP, BPM, BPS.[99]
Thyroid pituitary
Tumor
(GH3 cells)
48 h0/0.01/0.1/1/10 mg/L BPA/BPAF/BPAP/BPB/BPC/
BPF/BPM/BPP/BPS/BPZ
Inhibition of transcription of Tshβ, Trα, and Trβ, and Dio2 by BPA, BPF, BPM, and BPZ. Some analogues but not BPA down-regulated Dio1.
RatImmortalized
thyroid follicular
cells
(FRTL-5 cells)
qRT-PCR6/24/48 h0/10/30/100 µM BPAUp-regulation of Tg, Pax-8, Foxe-1 and down-regulation of Slc5a5, Tpo, and Nkx2-1 transcripts at the highest dose.[100]
Iodine uptake assay1 h10−7–10−4 M BPA +10 µM NaIConcentration-dependent decrease of iodine uptake.
24/48 h0/10/30/100 µM BPASignificant decrease in iodine uptake at non-cytotoxic doses of BPA in the absence of NaI
RatImmortalized
thyroid follicular
cells
(FRTL-5 cells)
Microarray analysis/
qRT-PCR
1/3/7 days10−9 M BPADeregulation of 372 and 1041 genes after 3 and 7 days, respectively. Most genes had a fold change >2 at both time points. Following exposure longer than 7 days, inhibition of genes involved in the DNA replication and repair network.[101]
Alkaline comet assay/
TUNEL assay
28 days + 5 days UV10−9 M BPAAfter irradiation at 48 and 96 h, higher content of DNA damage in the BPA-treated cells. Until 120 h post irradiation, higher apoptotic levels in the BPA-treated cells.
RatImmortalized
thyroid
follicular cells
(FRTL-5 cells)
Luciferase reporter gene assay24 h10−15–10−4 µM BPA
±1.78/3.44/6.87/13.7/27.5 ng/µl TSH
Enhancement of Tg-promoter activity also in the presence of the highest dose of TSH.[89]
10−9 M BPA ±1 µM ICI/TAMNo effect of the two antiestrogen on the activity of Tg-promoter induced by BPA.
HumanOvary cells
(SVKO3 cells)
qRT-PCR24 h/72 h10−9–10−4 M BPAIncrease of transcription levels of Slc5a5, Tpo, Tsh-r, Tg, Pax8, Nkx2-1, Foxe 1. Increase of transcription of PAX8 also in SVKO3 cells.
Table 3. Summary of in vivo studies analyzing effects of exposure to bisphenols on thyroid function.
Table 3. Summary of in vivo studies analyzing effects of exposure to bisphenols on thyroid function.
SpeciesMethodWindow of ExposureDoses TestedPrincipal Results Reference
Rodents
Male and female CD-1 miceELISAPND28-PND560/10/100 mg/L BPA in waterSignificant reduction of FT4 but not FT3 levels at both doses. No effects of sex on FT3 and FT4 levels. [113]
Pregnant female rats (Crj: CD (SD) IGS strain)Chemiluminescence
immunoassay
GD6-PND200/4/40 mg/kg BW BPA per day by dietIn male and female offspring no significant variations in T4 levels at 1, 3, 9 weeks of age.[108]
TSH stimulation assayOffspring at 9 weeks of age; 1 day treatmentTSH 25 mIU/5µL/g BW BPA intraperitoneally + 125 mIU 5µL/g BW BPA intramuscularlyIn response to exogenous TSH, elevation of T4 levels, but any significant difference between control and BPA groups of both sexes.
Pregnant female Sprague Dawley ratsRadioimmunoassayGD6-PND200/1/10/50 mg/kg BW BPA per day by dietIncrease of TT4 levels in both male and female pups only on PND15. No effects on serum TSH in male pups on PND15 among the different treated-groups. [104]
Pregnant female Sprague Dawley ratsElectrochemiluminescence
immunoassay
GD10-PND200/100/1000/10,000 ppm TBBPA by dietIn male pups on PND20, dose-unrelated, but statistically significant decrease of serum T3 levels whereas no significant variations of T4 and TSH. At PNW11, any changes of THs levels in any groups.[107]
NecropsyNo significant changes in thyroid weights of treated dams and offspring compared with controls but dose-unrelated increased thyroid weight in all treated groups of dams.
HistologyNo significant increased incidence of diffuse thyroid follicular cell hypertrophy in dams at the highest dose.
Pregnant female Sprague Dawley rats
(strain code 23)
RadioimmunoassayGD6-PND150/2.5/25/250/2500/25,000 μg/kg BW BPA per day by dietNo effects on T4 and TRH levels in male and females pups on PND15.[109]
Pregnant female Sprague Dawley ratsELISA GD11-PND210/0.1/50 mg/L BPA per day in waterIn dams, at 0.1 mg/L reduction of FT4 levels at delivery and on PND7.
In male pups on PND7, increased FT4 levels at 0.1 mg/mL and decreased FT4 levels at 50 mg/L. In females no effects at each dose at all days.
[112]
Sprague Dawley rat damsRadioimmunoassayGD6-PND15
GD6-PND21
GD6-PND90
2.5–2700/100,000/300,000 μg/kg BW BPA per day by dietNo effects on THs levels, thyroid weight, or thyroid histology in the “low-dose” region. On PND15, elevation of T3 at both high doses. On PND90, increase of TSH in females at both high doses and of T4 in males at the highest dose.[118]
Female Sprague Dawley ratsELISAGD11-PND210.1 mg/L BPA per day in waterIn dams, after 10 days from exposure, significant decrease in TT4 and FT4 levels, but no variation of TT3 and FT3 levels.
On PND21 but not on PND90, significant decrease of TT4, TT3, FT4, and FT3 levels in male pups.
[111]
Female Sprague Dawley ratsRadioimmunoassay/ELISAPND1-PND100, 5 μg/50μL BPA (B5), 50 μg/50 μL BPA (B50), 500 μg/50 μL L BPA (B500) in castor oilOn PND13, no differences in TSH levels. In estrus, on PND90, increased TSH levels following exposure to B50, but not B5 or B500. In adult females, lower T4 levels at B5 and B500, but not B50. No significant differences of T3 among groups.[117]
Neonatal males R. norvegicus (Wistar strain)ELISAPND15-PND300/20/40 mg/kg BW/BPA per day by diet On PND30, significant elevation of TSH levels, accompanied by a notable reduction of T3, T4, and GH levels in a dose-dependent manner.[116]
Male and female CD® ratsElectrochemical luminescence immunoassay13 consecutive weeks.
6-week recovery period of animals for both control and 1000 mg/kg/
day groups.
0/100/300/1000 mg/kg BW TBBPA per day by dietNo effects on TSH and T3 levels at any dose or time in both sexes. Decrease of T4 levels at all doses in both males and females.
Following recovery period, T4 levels in males but not in females at 1000 mg/kg were comparable to controls.
[110]
Necropsy/HistologyNo effects of treatment on thyroid weight and histopathology
Wistar rats damsRadioimmunoassayGD1-PND210/10 (BPA10)/50 μg/kg BW per day (BPA50) by dietOn PND21, no change in THs levels in dams and in female pups, whereas in the BPA10 group of male pups lower T3 levels without any variation in T4 levels.
On PND180, decrease of T3 levels in females and T4 levels in males among the BPA10 group.
[115]
Adult female Wistar ratsRadioimmunoassay15 days40 mg/kg BW per day BPA by dietHigher T4 levels in BPA-exposed animals, whereas no variations of T3 levels.[106]
Thyroid iodine uptake/TPO activitySignificant reduction of TPO and NIS activity.
ROS generationIn BPA-treated animals, significant generation of H2O2 generation in the thyroid.
qRT-PCRSignificant reduction of Tshβ mRNA levels in the pituitary of the treated rats.
Adult male Wistar ratsRIA15 days0/40 mg/kg BW/BPA per day by dietAfter 15 days of treatment, significant reduction of liver DIO1 activity, whereas no effects on brown adipose tissue DIO2 activity. Significant increase of TT4 levels but no variations of TT3 levels. Significant reduction of T3/T4 ratio.[102]
Wistar rats (HsdCpb:WU) of both sexesRadioimmunoassay70 or 14 days before mating – after mating (males) or PND21 (females)
28 days
0/3/10/30/100/300/1000/3000 mg/kg BW TBBPA per day by diet (reproduction study)
0/30/100/300 mg/kg BW TBBPA per day by diet (subacute toxicity study)
In the reproduction study, decrease of T4 levels in pups of both sexes, and increase of T3 levels only in females.
In the subacute toxicity study, significant decrease of T4 and increase of T3 levels in males, whereas in females parallel though not significant trends.
[114]
NecropsyDose-dependently increase of pituitary weight in male pups in the reproduction study. No effects in the subacute toxicity study.
HistologyNo changes observed in the histology of the pituitary gland both in the reproduction and in the subacute toxicity studies.
Female F344 ratsNecropsy64 weeks250/1000 μg/kg BW per day BPA by diet ±2800 mg/kg sc. DHPN
±1000 μg/L KI in water
In the group exposed to DHPN, statistical significances among all groups, and the KI group had the heaviest thyroid weights. In the group not exposed, no significant differences were found among groups.[105]
HistologyIn the group exposed to DHPN + KI + 1000BPA, all thyroids had a tumor or focal hyperplasia. Significant difference in the total number of hyperplasia lesions among all groups of animals exposed to DPNA.
Chemiluminescence immunoassay/ELISAIn the groups exposed to DHPN, TSH was significantly higher in the KI group than in the controls and the highest FT4 concentration was in the BPA1000 group. In the groups not exposed to DHPN, the highest concentration of TSH was in the controls whereas FT4 increased with increasing doses of BPA.
Western blotting detectionIn the groups exposed to DPNA, increased protein levels of ERα in the BPA250 and BPA1000 groups compared to the control.
Sheep
Lacaune ewesRadioimmunoassayGD28-GD1280/0.5/50/5000 μg/kg per day sc. BPAIn mothers, no effects on TT4 and TSH levels, but significant decrease of FT4 (at the lowest dose) and TT3 (at the lowest and middle doses) throughout pregnancy. No changes in TT4 and FT4 levels in fetal jugular blood on GD132-GD134. [123]
Lacaune ewesRadioimmunoassayGD28–GD1450/5 mg/kg BW per day sc BPAIn pregnant ewes, reduction with time of TT4 but not of FT4. Decrease of jugular blood TT4 and FT4 concentration within the 1st hour of life and of TT4 concentration in cord blood. Slight decrease of TT3 in the 1st hour of life. At 2 months of life no changes in THs levels.[122]
Zebrafish
GFP-positive transgenic zebrafish embryosFluorescence24–48hpf/24–72 hpf10−7/5×10−7/10−6/5*10−6/10−5 M BPA ±10−8 M T3In the presence of T3, the two highest doses of BPA inhibited T3-induced transcriptional activity during 48 h exposure. No effects of BPA or T3 in the presence of T3 during 24h exposure.[126]
Wild-type zebrafish (Danio rerio) embryos qRT-PCR72 h0.01/0.1/1.0 μM BPA/BPS/TBBPA/TBBPSAt 0.1 μM, BPA and TBBPS up-regulated Trβ transcripts whereas BPS and TBBPS showed no significant effect. At 1.0 μM BPS and TBBPS up-regulated Trβ mRNA levels, while BPA had a down-regulating effect.[68]
Wild-type zebrafish (Danio rerio) embryosqRT-PCR24–48 hpf10−8–10−6 M BPAInduction of Tg expression at 10−8 and 10−6 M. Up-regulation of Pax8 transcripts at low and high doses and of Pax2a and Tsh transcripts only at high dose. [89]
Wild type zebrafish (Danio rerio) embryosELISA
qRT-PCR
2–168 hpf0/5/50/500 μg/L BPAFSignificant decrease of TT3, FT4 and TT4 levels at 50 and 500 μg/L. Reduction of FT3 levels in all treated groups.[13])
Up-regulation of Tshβ at 50 μg/L and significant decrease of transcription at the highest dose. Up-regulation of Tg and Dio2 at 50 μg/L, Dio1 at 50 and 500 μg/L, and Ttr at all doses. Down-regulation of transcription of Trβ at 50 μg/L, Slc5a5 and Trα at 50 and 500 μg/L.
Wild type zebrafish (Danio rerio) embryosELISA75 dpf0/0.1/1/10 and 100 μg/L BPSLower levels of T3 and T4 in males exposed to 10 and 100 μg/L. Lower levels of T3 and T4 in females exposed to 100 μg/L.[131]
Wild-type zebrafish (Danio rerio) embryos-larvae ELISA<4–120 hpf0.08/0.4/2 mg/L BPA/BPF;
2/10/50 mg/L BPS;
0.04/0.18/0.68 mg/L BPZ
Significant increase of T3 levels at 0.4 mg/L BPA and at 50 mg/L BPS (with a dose-response trend) and of T4 at 2.0 mg/L BPF (with a dose-response trend).[37]
qRT-PCR0.4<72 mg/L BPA or BPF; 10/50 mg/L BPS; 0.08/0.4 mg/L BPZUp-regulation of Hhex, Tg, Ttr, Dio1, Ugt1ab genes by BPA. Up-regulation of Hhex, Ugt1ab genes by BPF, of Crh, Tshβ, Tsh-r, Hhex, Tpo, Ttr, Ugt1ab by BPS, and of Tshβ by BPZ.
Wild-type zebrafish (Danio rerio) embryos-larvaeELISA2–144 hpf0.2/2/20/200 µg/L BPFDose-dependent decrease of TT4 levels in BPF treated groups. Significant elevation of TT3 at 200 µg/L and TSH at 20 and 200 µg/L BPF.[38]
qRT-PCRUp-regulation of Crh and Tg at 2,20, 200 µg/L. Induction of transcription of Slc5a5, Dio2, Ugt1ab at 20 and 200 µg/L. Down-regulation of Ttr at 20 and 200 µg/L.
Wild-type zebrafish
(Danio rerio) embryos-larvae
qRT-PCR0/1/5 dpf; exposure for 24/48h10−5 M BPA ±10−8 M T3Weak effects of BPA alone on gene expression compared with controls, except for the induction of TSH expression in the group 1day/48 h.
With T3, reduction of Trα, Trβ, and Tsh expression in 1-day-old embryos at both 24 and 48 h, but up-regulation of Trα and Trβ, by 24-h exposure in 0-day-old embryos and of Tsh by 48-h exposure in 5-day-old larvae.
[126]
Wild-type zebrafish (Danio rerio) embryos-larvae ELISA2–144 hpf50/100/200/400 μg/L TBBPADose-dependent increase of T4 levels and dose-dependent decrease of T3 levels.[128]
200 μg/L TBBPA/20 μg/L T3/200 μg/L TBBPA+20 μg/L T3After exposure to T3, significant decrease of T4 and significant increase of T3 contents. After co-treatment TBBPA and T3, decrease of T4 and increase of T3 contents, which were significantly different from the control group (only for T3 increase) and the TBBPA treated group.
qRT-PCR50/100/200/400 μg/L TBBPAUp-regulation of Tsh and Tg and down-regulation of Ttr and Trβ transcript levels.
200 μg/L TBBPA/20 μg/L T3/200 μg/L TBBPA+20 μg/L T3After exposure to T3 and TBBPA + T3 significant up-regulation of Tsh and Tg whereas no changes in Ttr and Trβ mRNA levels.
Wild-type zebrafish (Danio rerio) embryos-larvaeELISA2–168 hpf1/3/10/30 μg/L BPSSignificant decrease of TT4 levels at 10 and 30 μg/L and TT3 levels at the highest dose. Significant increase of TSH in the 10-, and 30 μg/L exposure groups.[129]
qRT-PCRUp-regulation of Crh, Tg, Dio1, and Ugt1ab at 10 and 30 μg/L. Induction of transcription of Pax8, Slc5a5, Tg, and Dio2 at 30 μg/L. Down-regulation of Ttr mRNA at 3, 10, and 30 μg/L. No effects on transcription of Trα, Trβ, and Dio3.
Wild-type zebrafish (Danio rerio) embryos-larvaeqRT-PCR96–192 hpf0%/10%/50%/75% of the 96 h -LC50 BPA/TBBPA Induction of Trα, Tshβ, and Ttr in larvae and of Trα and Ttr transcripts in embryos by TBBPA. Down-regulation of Trβ and Tshβ mRNA in embryos by TBBPA. Up-regulation of Tshβ mRNA in larvae by BPA. No effects on Slc5a5 and Tg expression in larvae neither on Tpo in embryos.[133]
Wild type zebrafish (Danio rerio) larvaeqRT-PCR2–120 hpf0/100/200/300/400 μg/L TBBPASlight up-regulation of Dio1, Trβ, and Tsh, and significant up-regulation of Trα at low doses. Significant down-regulation of Tpo. No significant effects on expression of Dio2 and Dio3 transcripts.[132]
Wild-type adult zebrafish (Danio rerio)qRT-PCR72 h50 μg/L/100 μg/L BPA or BPSAfter BPA exposure, increase of Slc5a5 mRNA levels at both doses and Tpo transcript levels at the lowest dose. No effects on Tg expression.
After BPS exposure, increased expression of Slc5a5 and Tg transcripts at the highest dose and Tpo transcripts at the lowest dose.
[135]
Adult male zebrafish (Danio rerio)ELISA21 days0/24.7 µg/L BPAF/5.6 µg/L SMX/24.7 µg/L BPAF + 5.6 µg/L SMXSlight decrease of T4 levels in fish exposed to BPAF. Significant increase of T4 in fish exposed to the mixture BPAF + SMX.[134]
qRT-PCRUp-regulation of Trh, Trhr, Tshβ, Dio2 and down-regulation of Tpo, Slc5a5, Tg mRNA levels in fish exposed to BPAF.
Up-regulation of Trα, Trβ, Dio1, Dio2, Tpo, Tg, Slc5a5 and down-regulation of Trh, Trhr, Tshβ transcript in fish exposure to mixture.
Table 4. Summary of human studies on the association between bisphenols exposure and thyroid parameters.
Table 4. Summary of human studies on the association between bisphenols exposure and thyroid parameters.
Study Design CountryStudy SampleSample Size (N)AgePrincipal ResultsBPA ConcentrationConfoundersReference
Prospective JapanWomen with a history of three or more (3–11) first-trimester miscarriages. Blood samples collected 5–9 days after ovulation in at least two cycles.45 patients27–36No difference in serum BPA levels between patients with and without hypothyroidism.
Serum TSH levels not estimated.
Patients with hypothyroidism:
Mean (SD): 2.99 ± 3.04 µg/L
Patients without hypothyroidism:
Mean (SD): 2.50 ± 5.70 µg/L
-[151]
ProspectiveBelgiumOverweight and obese individuals.
Lean individuals.
For obese individuals, urine samples collected at baseline, before starting a weight loss program (N = 151) and after 3 (N = 95), 6 (N = 53), 12 months (N = 39).
151 obese individuals
43 lean individuals
≥18The obese group had higher urinary levels of BPA. Positive relationship of urinary BPA with serum TSH in lean subjects.Obese individuals
0—median: 1.7 µg/L
3 months—median: 2.0 µg/L
6 months—median: 1.7 µg/L
12 months—median: 1.5 µg/L
Lean individuals
Median: 1.2 µg/L
[1,7,34][152]
Prospective birth cohortUSAPregnant women from the CHAMACOS study. Urine samples collected at 12 and 26 weeks of gestation. 476≥18In mothers, no association of urinary BPA (average) with FT4 and TSH levels, and negative association (BPA 26 week) with serum TT4. Inverse association between maternal BPA (average, 26 week) and TSH in male newborns but not in females.LOD: 0.4 μg/L
Mothers:
GM: 1.3 µg/g cr
Median: 1.2 µg/g cr
[1,2,4,8,10,12,13,14,15,16,17,18,19,20,21][143]
Prospective birth cohortUSAPregnant women from the HOME study. Urine samples collected at both 16 and 26 weeks of gestation (N = 237).249≥18Neither association of maternal BPA (16 week) with maternal THs or TSH levels nor of maternal BPA (average, 16 week, or 26 week) with THs or TSH levels in newborns. Significant inverse association of maternal BPA with TSH levels (average and 26 week BPA) and slight positive association with TT3 levels (26 week BPA) in females. Stronger relationship of BPA–TSH among girls born from iodine-deficient mothers.LOD: 0.4 μg/L
16 weeks
GM: 2.0 (95%CI 1.8–2.2) µg/g cr
26 weeks
GM: 2.3 (95%CI 2.1–2.5) µg/g cr
[1,2,8,9,10,15,16,17,19,20,22,23,24,25][148]
Prospective birth cohortJapan Pregnant women at 23–35 weeks of gestation (singleton babies). Cord blood obtained at delivery.283 ≥18No association between BPA concentration in cord blood and TSH or FT4 levels in newborns of both sexes.LOQ: 0.04 µg/L
GM: 0.051 µg/L
IQR: <LOQ–0.076 µg/L
[19,38][146]
Nested case-controlUSAWomen who delivered preterm
(< 37 weeks of gestation) and controls of women who delivered a singleton infant after 37 weeks of gestation. Urine samples collected at up to 4 visits (median for each visit: 9.64, 17.9, 26.0, and 35.1 weeks of gestation).
116 cases
323 controls
≥18IQR increase in BPA concentrations across study visits was significantly associated with lower TSH and higher FT4 levels. No effect on FT3, and inverse but not significant association of BPA with TT4 levels. No association of BPA with serum FT4 at visit 3. Significant inverse association of BPA with TSH levels at visits 3 and 4 and a slight increase of serum TT3 at visit 4.Total: GM ± SD: 1.18 ± 2.82 µg/L
1 visit: GM ± SD: 1.33 ± 2.84 µg/L
2 visit: GM ± SD: 1.04 ± 2.85 µg/L
3 visit: GM ± SD: 1.22 ± 2.84 µg/L
4 visit: GM ± SD: 1.12 ± 2.70 µg/L
[2,3,4,8,17,19,25,35,36,37],[139]
Case-control KoreaInfants with congenital hypothyroidism
and their mothers; healthy infants with their mothers.
Blood samples collected.
26 congenital hypothyroidism mother–infant pairs
12 normal mother–infant pairs
<24 monthsTBBPA levels not significantly different in the two infant groups.
No significant correlation between TBBPA and any of the THs levels in infants with congenital hypothyroidism. In their mothers, positive weak correlation of TBBPA with serum FT4 and thyroid stimulating immunoglobulin.
Normal group and their mothers
TBBPA mothers: 10.93 ng/g lipid
TBBPA infants: 77.65 ng/g lipid
Congenital hypothyroidism group and their mothers
TBBPA mothers: 8.89 ng/g lipid
TBBPA infants: 83.4 ng/g lipid
[1,47,48,49][140]
Case-controlCyprus (n = 122)
Romania
(n = 90)
Females with thyroid nodules (diameter >3mm). Females without nodules.
Two spot urine samples collected in Cyprus (7 day apart from each other). In Romania one spot sample collected.
212:
106 cases
106 controls
≥18In the whole study population, median TSH and BPA levels were significantly lower in the cases. Significant positive association of BPA with TSH levels and TNs. Neither association of BPA, BPF, or ClxBPA with FT4 levels nor of BPF and ClxBPA with serum TSH. No association of BPF and ClxBPA with TNs.LOD (BPA): 10 μg/L
LOD (BPF): 13 μg/L
LOD (ClxBPA): 10–17 μg/L
Median:
BPA: 2.25 (1.10–4.61) μg/L
BPF: 0.46 (0.32–0.72) μg/L
ClxBPA: 0.16 (0.15–0.19) μg/L
BPA Cases: 1.75 (1.11–3.56) μg/L
BPA Controls: 2.71 (1.08–5.91) μg/L
[1,3,10,11,39,40,41][147]
Case-controlTurkeyChildren with HT.
Children without HT.
Spot urine samples collected.
29 cases (25 females and 4 males)
29 controls
8–16No significant difference in urinary BPA levels between the two groups. Significant negative correlation between BPA and FT4 levels in HT group. No correlation between urinary BPA concentration and TPOAb levels.LOD: 0.5 ng/mL
Mean (± standard error of the mean)
Cases: 7.31 ± 1.46 µg/g cr
Controls: 7.72 ± 1.74 µg/g cr
-[155]
Case-control ChinaWomen with TNs.
Women without nodules.
First morning urine collected.
1416:
705 cases
711 controls
≥18Urinary BPA was significantly higher in cases than in controls. Increased prevalence of TNs with increasing urinary BPA quartiles.
Significant association between urinary BPA and TNs in all age groups and in the thyroid autoantibody positive group.
LOD: 0.1 µg/L
Median:
Total: 3.08 (1.60–5.81) µg/g cr
Cases: 3.27 (1.77–6.53) µg/g cr
Controls: 2.92 (1.44–5.27) µg/g cr
[1,3,8,10,11,29,30,31,44,45,46][159]
Multicentre, cross-sectionalItalyPatients with TNs.
Patients with DTC.
Blood collected from each patient.
27 with TNs
28 with DTC
≥18Significant correlation between urinary BPAF concentration and risk of DTC in patients with TNs. BPS and BPB concentrations higher in patients with TNs, as compared with DTCs. TSH levels higher in patients with DTCs and in subjects exposed to BPE and BPA. Subjects with TNs (median ± SD) BPAF: 12.47 ± 0 ng
BPS: 59.29 ± 50.29 ng
BPB: 29.92 ± 35.60 ng
Subjects with DTC (median ± SD)
BPAF: 9.44 ± 5.41 ng
BPS: 34.79 ± 41.86 ng
BPB: 14.36 ± 15.31 ng
[50][161]
Cross-sectional USAMen who are partners of subfertile couples. Single spot urine (N = 167), second (N = 75), and third (N = 4) urine samples collected.16718–55Inverse relationship of BPA with TSH levels.
No effects on T3 and T4 levels.
LOD: 0.4 µg/L
GM and median: 1.3 µg/L
[1,2,3,4,5,6][150]
Cross-sectionalUSAAdult and adolescents from the NHANES 2007–2008. Single spot urine collected.1346 adults
329 adolescents
≥20
12–19
In adults, inverse relationship of BPA with TT4 levels. Inverse trends between BPA quintiles and both TT4 and TSH. GM: 2.03 µg/g cr
GM: 1.88 µg/g cr
[1,2,3,7,8,9,10][145]
Cross-sectionalUSAAdults and adolescents from the NHANES 2007–2008. Urine sample collected.710 females; 850 males12–85Negative association between urinary multiple EDCs including BPA and TT4 levels in males but not in females. Positive but not statically significant association of EDCs with T3 levels in females.LOD (BPA): 0.13 µg/L
Males:
GM: 2.19 (95% CI 1.94–2.47) µg/L
Females:
GM: 2.00 (95% CI 1.80–2.23) µg/L
[1,2,4,9,10,11,26][142]
Cross-sectional ChinaWorkers in two semiautomatic epoxy resin factories. Spot urine collected at the end of the shift on Friday.28 (21 males and
7 females)
22–62The workers with the highest BPA concentrations (feeding position) had higher FT3, TT3, TT4 levels, and lower TSH levels. Urinary BPA significantly associated with higher FT3 levels (when office workers were excluded). Weak positive association between BPA and serum FT4. Total workers:
GM ± SD: 31.96 ± 4.42 μg/g cr
Feeding operators:
GM ± SD: 192.45 ± 2.78 μg/g cr
Crushing and packing:
GM ± SD: 17.08 ± 2.33 μg/g cr
Office workers:
GM ± SD: 11.60 ± 1.70 μg/g cr
[11][141]
Cross-sectionalChinaPopulation-based study.
Spot morning urine collected.
3394:
1354 males
2040 females
≥40Significant positive association of urinary BPA with serum FT3 and inverse association with TSH levels both in men and in women.
Positive association between high thyroid function and high urinary BPA levels.
LOD: 0.3 μg/L
Median: 0.81 µg/L
IQR: 0.47–1.43 µg/L
Overt and subclinical
hypothyroidism subjects:
GM: 0.63 (95% CI 0.52–0.77) µg/L
Euthyroid subjects:
GM: 0.81 (95% CI 0.78–0.83) µg/L
Overt and subclinical hypothyroidism subjects:
GM: 1.05 (95% CI 0.84–1.32) µg/L
[1,3,4,8,11,17,27][149]
Cross-sectional China Students of primary schools. First morning urine samples collected.7189–11BPA levels similar among boys and girls but increased with age. Significant inverse association between urinary BPA and thyroid volume. Risk of TNs increased with age without any association with sex or urinary iodine level. BPA inversely associated with risk of multiple TNs.Urinary iodine:
Median: 159 μg/L
Urinary BPA:
Median (IQR): 2.45 (1.09–5.97) µg/g cr
[1,3,7,11,42,43][158]
Cross-sectionalChinaPatients with NG.
Patients with PTC.
Healthy controls.
Spot blood and urine samples collected in the morning.
53
60
65
≥18Urinary BPA and urinary iodine levels in NG and PTC groups were significantly higher than those in controls.
Urinary BPA levels in the females of NG group and both the male and female PTC groups were higher than those in the control group of the same sex. Urinary BPA concentration was significantly lower in the female PTC group than in the female NG group.
Urinary iodine in the PTC or NG groups was higher than that of controls of the same sex.
Significant correlation between urinary BPA and iodine concentrations in all groups.
LOQ for BPA in urine: 0.1 µg/L
LOQ for BPA in serum: 0.2 µg/L
LOD for iodine in urine: 3 µg/L
Serum BPA
GM: 7.42 (4.03–13.82) µg/L
Urinary BPA:
GM: 2.82 (0.016–59.78) µg/g cr
Urinary iodine:
GM: 335.05 (71.25–2995.74) µg/g cr
BPA—Control group
GM: 1.06 (0.015–27.88) µg/g cr
BPA—NG group
GM: 5.22 (0.022–50.78) µg/g cr
BPA—PTC group
GM: 4.68 (0.032–29.30) µg/g cr
[11][160]
Cross-sectional ThailandSubjects from the National survey NHES 2009. Serum sample collected.2340≥15Significantly inverse association of serum BPA with FT4 levels in males but not in females after exclusion subjects of thyroid autoantibodies. No association with serum TSH in both sexes.LOD: 0.3 μg/L
Median: 0.33 (0–66.91) µg/L
[1,3,7][144]
Cross-sectional ThailandSubjects from the National survey NHES 2009. Serum sample collected.2361≥15Significant association of increasing BPA quartiles with positivity for TgAb and TPOAb both in men and women but not for TRab. Age, sex, and BMI were independent predictors of TgAb and TPOAb positivity.LOD: 0.3 μg/L
Median: 0.32 (0–66.9) µg/L
-[156]
[1]: age; [2]: race and ethnicity; [3]: BMI; [4]: smoking; [5]: timing of collection of blood/urine samples by season; [6]: timing of collection of blood/urine samples by time of day; [7]: sex; [8]: education level; [9]: serum cotinine; [10]: urinary iodine; [11]: urinary creatinine; [12]: family income; [13]: country of birth; [14]: number of years spent in the United States; [15]: parity; [16]: gestational age at the time of blood collection; [17]: alcohol consumption; [18]: illegal drug use during pregnancy; [19]: newborn sex; [20]: delivery mode; [21]: age at the time of heel stick; [22]: prenatal vitamin use; [23]: Log10-PCB 153; [24]: delivery by Cesarean section; [25]: gestational week at delivery; [26]: menopausal status; [27]: occupation; [28]: total cholesterol; [29]: triglycerides; [30]: HDL-cholesterol; [31]: LDL-cholesterol; [32]: thyroglobulin antibody; [33]: thyroid peroxidase antibodies; [34]: weight loss; [35]: maternal age; [36]: health insurance provider, [37]: urinary specific gravity; [38]: days of mass screening test; [39]; thyroid hormones; [40]: study site; [41]: disease status; [42]: BSA; [43]: iodized salt consumption; [44]: total cholesterol; [45]: TgAb; [46]: TPOAb; [47]: obesity and other related diseases; [48]: medication; [49]: medical history; [50]: other EDCs.
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