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In the last few decades, there is substantial evidence that male reproductive function is deteriorating in humans and wildlife and this is associated with unintentional exposure to widely used synthetic chemicals. Subsequently, much has been done to show that certain chemicals in the environment adversely interfere with the developing fetal gonads of the laboratory animals. Some in vitro studies have demonstrated treatment-induced reproductive problems in offspring exposed to endocrine disrupting compounds (EDC) which are similar to those observed in wildlife and human population. Few EDC studies have demonstrated that there are certain periods of gestation when the developing fetus is highly sensitive and at risk of small endocrine changes. Similar observations have been made in the sewage sludge model, however, while animal studies have been insightful in providing valuable information about the range of effects that can be attributed to in utero exposure to EDCs, varying levels of maternal doses administered in different studies exaggerated extrapolation of these results to human. Thus the EDC concentration representative of fetal exposure levels is uncertain because of the complexities of its nature. So far, the level of fetal exposure can only be roughly estimated. There is substantial evidence from animal data to prove that EDCs can adversely affect reproductive development and function in male and more has accumulated on the mechanisms by which they exert their effects. This paper therefore, reviews previous studies to highlight the extent to which testis development can be disrupted during fetal life.
The adverse effects of environmental disrupting compound (EDC) exposure on various aspects of human health and, especially, reproductive development during fetal and early post-natal life, have been a growing concern in most parts of the world. This is particularly evident from the emerging trends in human reproductive health such as testicular cancer, decreasing sperm counts and or hypospadias/cryptorchidism, which are collectively 'termed testicular dysgenesis syndrome' (TDS), over the last few decades. Clinical and epidemiological evidence have shown declines in human semen quality during the last 5-6 decades (Leto and Frensilli, 1981; Bostofte et al., 1983). Several studies have reported diverse trends in male reproductive health, including increasing incidence of testicular cancer (Forman and Moller, 1994), declining semen quality (Andersen et al., 2000). Reports have shown significant decreases in sperm concentration (113 million/ml vs. 66 million/ml) and semen volume (3.40 ml vs. 2.75 ml) over the period between 1938 and 1990 (Carlsen et al., 1992). A number of reports on the available data from cancer registries have been reviewed (Toppari et al., 1996) with evidence of an increase in testicular cancer in many countries including England and Wales (Pike et al., 1987), Scotland (Hakulinen et al., 1986), the Nordic and Baltic countries (Adami et al., 1994; Stone et al., 1991), Australia (Pearce et al., 1987), New Zealand (Wilkinson et al., 1992; Spitz et al., 1986), and the United States (Harris and Steinberg, 1954).
Studies on wildlife species have revealed various effects of environmental compounds (Toppari et al., 1996). These include some key observations in gastropods, fish, reptiles, and mammals. Generally, some of the reproductive failures reported in wildlife include decreased fertility, decreased hatching success, birth deformities, metabolic abnormalities, behavioural abnormalities, demasculinisation/feminisation of males, and defeminisation/masculinisation of females (Hollander, 1997). A number of reproductive dysfunctions which were reported in male offspring from animal studies have been associated with maternal EDC exposure (Sweeney and Brooks 1996; Imajima et al., 1997). Experimental evidence from many animal studies has also explained some of the anatomical and physiological changes which may occur as a result of EDC exposed in humans. These includes oviductal malformations (Newbold et al., 1983) and a high incidence of uterine fibroids (Baird and Newbold, 2005; Cook et al., 2005).
Environmental disrupting compounds (EDCs) constitute a diverse range of anthropogenic compounds, including organochlorine pesticides, polychlorinated bisphenyls (PCB), alkylphenol polyethoxylates, phytoestrogens, bisphenol-A, phthalates, dioxins, polybrominated diphenyl ethers and heavy metals (Rhind et al., 2002) (Table 1(Tab. 1); References in Table 1: Hunt et al., 2003; Herath et al., 2004; Farr et al., 2004; Gray et al., 2001; Cobellis et al., 2003; Couse and Korach, 2004; Venners et al., 2005; Miller et al., 2004; Denham et al., 2005; Lau et al., 2004). They are ubiquitous, persist in the environment at low concentrations, however, they appear to exert a range of adverse effects, which include growth inhibition, reproductive dysfunction and immune system impairment (Rhind, 2002) on many animal species including ruminants and humans. They are often referred to as endocrine disruptors; indicating their potential ability as either hormone agonists, or antagonists of the endogenous compounds.
Their adverse effects may include impaired testosterone secretion, (certain phthalates), altered metabolism (PCBs, polychlorinated bisphenyls hydrocarbons), blockage of hormone action (pesticides) or direct activation of androgen or estrogen receptors (several EDCs) (Rhind, 2002). Animals may be exposed to relatively high concentrations of EDCs mostly through feeding and water; they could be stored and concentrated mainly in the fat tissues (Ekelund et al., 1990; Ahel et al., 1993; Pojana et al., 2007). The accumulated fats may be utilised in periods of pregnancy and lactation when the animals' energy requirements are particularly very high. This could exert endocrine disrupting effects on the animals (Bigsby et al., 1997) thus exposing their embryos and neonates to relatively high concentrations of EDCs. Detectable concentrations of EDCs were reported in body tissues from adults, young children and fetuses (Fowler et al., 2008, 2009; Choi et al., 2008), following absorption of the EDCs from the environment.
Reproductive and developmental abnormalities associated with EDC exposures have been well documented in wildlife. These include birds, frogs, seals, polar bears, marine mollusks, and many other wildlife species (Table 2(Tab. 2); References in Table 2: Degen and Bolt, 2000; Hughes, 1988; Tyler et al., 1998; Safe et al., 2000; Puga et al., 2009; Kung et al., 2009; Clarke et al., 2000; Newbold et al., 2000; Bryan et al., 1989; Guillette et al., 1994; Guillette et al., 1999; Willingham and Crews, 1999; Howell et al., 1980). For example, alligators from Lake Apopka in Florida, which was highly polluted due to extensive farming activities around the lake, the presence of a sewage treatment plant, and the past spills of organochlorine pesticides, were reported to have been feminized (Hood, 2005; Milnes et al., 2008). Over time, many of the adverse effects observed in wildlife populations have been induced in laboratory animals, supporting the role of EDCs in their occurrence. For instance, reduced testosterone synthesis, plasma steroid concentrations and male phallus size were reported in juvenile alligators from seven Florida lakes following EDC exposure (Guillette et al., 1999). The mechanism by which Di(n-butyl)phthalate (DBP) caused reduced testosterone levels was through decreased production of androgen and the associates sex steroids by the fetal Leydig cells (Lambright et al., 2003). Exposure of rat testes on gestation days 12-21 caused downregulation of mRNA expression for SRB1, StAR, P450scc, 3β-HSD, P450C17 and c-kit and upregulation of mRNA expression for TRPM-2 (Barlow et al., 2003).
Many studies in a variety of species have shown that there is a tendency for reproductive success to be jeopardized not only by direct effects of pollutants on reproductive pathways but also by adversely affecting the general health status of the individual. EDCs are known to have the potential to disrupt processes as diverse as immune function (Markman et al., 2008), thyroid function (Langer et al., 1998; Newbold et al., 2007), bone structure (Fox et al., 2008), mammary structure and function (Moral et al., 2008), cardiovascular function (Ha et al., 2007) and social behaviours (Markman et al., 2008). Perturbation of any one of these systems has the potential to adversely affect an animal's reproductive success (Rhind, 2009). The complexity of EDCs mechanism could be implicated in processes ranging from the increased incidence of breast cancer (Kortenkap 2006) and a variety of male reproductive effects (Sharpe and Skakkebaek, 2003) to metabolic disturbances. A number of developmental abnormalities from laboratory studies have been associated with EDC exposures. Many chemicals have been associated with the aetiology of various reproductive disorders which are thought to originate in fetal life (Sharpe and Skakkebaek 2003; Skakkebaek et al., 2001) and can be induced in animal models by fetal exposure to environmental chemicals (Fisher et al., 2003; Mylchreest et al., 1999; Parks et al., 2000). Prolonged exposure of rats to Di-2-ethylexyl phthalate (DEHP) caused reduced testosterone production (Akingbemi et al., 2004). There is also evidence of obstruct gonocyte development in rats exposed to DBP or DEHP leading to significant reduction in the number of germ cells per Sertoli cell at age 25 days compare with controls, as well as some evidence of altered Sertoli cell function and proliferation after such exposures (Hutchison et al., 2008). DBP exposed rats at days 4-6 postnatally showed reduced numbers of spermatogonia and their resumption of proliferation was delayed. Another study reported increased damage to the DNA in the rats spermatozoa as a result of monoethylphthalate (MEP) exposure (Duty et al., 2005). In addition, some phthalates such as DEHP can inhibit aromatase activities (Davis et al., 1994) and may thus interfere with estrogen production in fetal testis. During gestation, exposed human maternal-fetal unit and maternal tissues contain levels of EDCs that are associated with many in utero effects (Ikezuki et al., 2002; Younglai et al., 2002; Tsutsumi, 2005; Barr et al., 2007; Chao et al., 2007; Huang et al., 2007; Thundiyil et al., 2007). Testes exposed to dieldrin caused a reduction in LH-induced testosterone secretion, tissue protein concentrations of LH receptor, steroid acute regulatory protein and induced proteins associated with cancer and apoptosis (Fowler et al., 2007). In addition, protein expression of WNT-2B in the Sertoli and Leydig cells was significantly reduced. The 'anti-androgenicity' of DBP was shown in the suppression of fetal Leydig cell androgen production and consequently the occurrence of cryptorchidism and hypospadias (Johnston et al., 2004). Studies have shown that Polychlorinated bisphenyls (PCBs) can alter estrogen levels in the body and contribute to reproduction problems such as feminisation of males and intersex (Venners et al., 2005).
Testis development is accompanied by the expression and activation of a large number of genes. Perturbation of some of these genes has been reported following in utero exposure of developing fetuses to EDCs. The chief of these is sex-determining gene located on the Y chromosome (Sry gene), which dictates the extent of sex determination and favours testis development. Sheep Sry transcripts persist after the full differentiation of the testis as opposed to what happens in mice, (disappears after differentiation), indicating that its role is not limited to initiating sex determination and Sertoli cell differentiation (Payen et al., 1996). In addition, some other genes are involved in mammalian sex determination including Wilms' tumour gene (WT-1), Steroidogenic factor gene (SF-1), and some growth factors such as anti-Mullerian hormone (AMH). Interference with the expression of these genes might result in impaired testis development (Yao et al., 2002).
In humans, disrupted DHH gene is also correlated with gonadal dysgenesis (Canto et al., 2004). Insulin-like factor 3 (INSL3) acts through the receptor LGR8 to mediate testicular descent, enhancing the growth gubernaculum's primodia and caudal genitoringuinal ligament. Mutation of the two genes is associated with failure of testicular descent in developing males (Ferlin et al., 2008; Adham and Agoulnik, 2004). Several studies have provided more evidence for testosterone and/or dihydrotestosterone (DHT) playing a role in testis descent, this include extensive expression of AR in the gubernaculum (Staub et al., 2005), the expression of 5α reductase (George, 1989), and interaction of Insl3 and androgens in vitro to regulate gubernaculum growth (Emmen et al., 2000). Exposure of rats to flutamide a synthetic antiandrogen between ER 15.5 and 18.5 caused incomplete inguino-scrotal descent (Mylchreest et al., 1999; Amann and Veeramachaneni, 2007).
There are numerous studies on trends of changes in human reproductive health, evident in declining male fertility and associated developmental disorders (Skakkebaek et al., 2001). However, there appears to be less concern about the risks associated with exposure of farm animals to EDCs as there is little evidence of a defined risk to farm animal fertility as a result of exposure to EDC, however, emerging preliminary observations are suggesting that risks may yet become apparent (Rhind, 2005). Rhind (2009) reported that subtle perturbation of underlying processes associated with EDC exposure is not significantly apparent under field observations however, it may be devastating to animal health or reproductive performance. The possibility that the increases in the incidence of poor performance and ill health may become significant in future is not negligible, particularly if exposure to EDCs is increased (Rhind, 2005). For instance, reduced immune cell numbers in fetal tissues was evident in the sewage sludge model, suggesting that effects are present and that animal performance may be influenced by small, but potentially economically-significant reduction in immune capacity. The subtle nature of the effects of EDC exposure in farm animals may take a long time to establish whether there are measurable consequences associated with it. There is a need for more evidence of subtle differences in performance due to EDC exposure.
Substantial evidence accumulated from epidemiological studies to support the human health risk related with exposure to endocrine disruptors. Most studies on the effects of EDCs were based on rodent models, and the impacts of such studies have led to the understanding of potential effects and the mechanisms of actions of individual EDCs from such studies. However, such studies are of limited empirical value in the assessment of health risks in human development because the patterns of experimental exposure are not representative of normal human exposure. The majority of the laboratory studies have used a number of selected chemicals, which were administered at doses higher than environmental levels (Parks et al., 2000; Gray et al., 2001; Hayes et al., 2002). Nevertheless, the importance of environmental relevance of these compounds to exert reproductive abnormalities in mammals remains. This will certainly involve the study of the effects of multi-component mixtures of compounds to determine the effects on mammalian reproduction.
In mammals, gonad formation is initiated by the migration of primordial germ cells from the proximal epiblast of the extraembryonic mesoderm, via the hindgut into the gonad (Adams and McLaren, 2002). The somatic cells which constitute about 80 % of the testicular cells originate from either the coelomic epithelium or mesonephros adjacent to the gonad. However, the origin of both fetal and adult Leydig cells remains controversial and recent studies have suggested that these cells do not have a common source. However, it is not unlikely that both the coelomic epithelium and mesonephros have contributed to the fetal Leydig cell population.
Sertoli cells main functions during testis development include cord formation and secretion of anti-Mullerian hormone (AMH) during fetal life (Mackay, 2000), and provide the germ cells with the physical and metabolic support needed for spermatogenesis during postnatal life (Sharpe, 1994). The pre-Sertoli cells populations are derived from the coelomic epithelium and are stimulated by Sry to differentiate into Sertoli cells. Sertoli cells express a number of genes that play important role in testis development which include SOX9, WT1, DAX1, FGF9, DHH and DMRT1. Many other genes are being expressed by the Sertoli cells including WNT-4, LHX-1, EMX-1, LHX-9 and SF1 (Wilhelm et al., 2007).
Sertoli cell proliferation forms essential part of testis development as there is finite number of germ cells which each of the Sertoli cells can support through spermatogenesis in adulthood and consequently, the number of Sertoli cells per testis determines both the testis size and maximum number of sperm that it can produce (Sharpe and Skakkebaek, 2003). These cells are no longer mitotic after puberty, so the population at that time is definitive.
Proliferation of Sertoli cells occurs during two periods of life: fetal or neonatal and peripubertal, which is morphologically indifferent in most species. In sheep, sexual differentiation and postnatal testicular growth are separated by a period of at least five months giving a more precise analysis (Hochereau-de Reviers et al., 1995). In sheep there are two periods of mitotic activity of Sertoli cells, first after sexual differentiation and second after birth. By contrast, in the fetal rat testis, mitotic activity of Sertoli cells is maximal just before birth, while gonocytes divide earlier (Hilscher et al., 1972), making the two periods overlap (Sharpe and Skakkebaek, 2003). Only one peak of DNA synthesis in rat Sertoli cells has been observed at the end of gestation (Orth, 1982).
Mitotic divisions of Sertoli cells are more numerous before birth but functional maturation of Sertoli cells occurs around the onset of puberty (Sharpe and Skakkebaek, 2003), coinciding with the time they exit the cell cycle (Gondos and Berndston, 1993). They undergo morphological changes which include enlargement of nucleus to become tripartite and nucleolus to become more distinct (Sharpe and Skakkebaek, 2003) and between each Sertoli cell the formation of specialized tight junctions to create the blood-testis barrier (Gondos and Berndston, 1993).
FSH has been shown to stimulate Sertoli cell proliferation in both around and after birth in rat testis (Orth and Boehm, 1990). However, very few FSH binding sites per Sertoli cell were present in the postnatal testis (Barenton et al., 1983). Furthermore, Sertoli cell number has been examined in fetal and postnatal hypophysectomy sheep and hypogonadal (hpg) mice, lacking GnRH and therefore no circulating gonadotrophins (FSH and LH). Fetal Sertoli cell proliferation is independent of gonadotrophins, whereas postnatal Sertoli cell proliferation requires gonadotrophins (Hochereau-de Reviers et al., 1995; Baker and O'Shaughnessy, 2001).
Androgens also play an important role in Sertoli cell proliferation in the fetal testis which may be direct or indirect (Johnston et al., 2004). In addition to the endocrine functions, some growth factors have been found to support Sertoli cell proliferation. This includes epidermal growth factor (EGF) and transforming growth factor-α (TGF-α) which stimulate postnatal Sertoli cell proliferation, at least in culture (Petersen et al., 2001) and testis organ cultures (Cupp and Skinner, 2001). Furthermore, TGF and EGFR expression can be regulated through growth stimulatory hormones such as FSH and testosterone (Cupp and Skinner, 2001). While FSH and androgens were reported to have stimulatory effects on Sertoli cell proliferation, thyroid hormone has been reported to have inhibitory effect on the Sertoli cell proliferation in rodents as hypothyroidism prolonged Sertoli cell proliferation (Van Haaster et al., 1992), and conversely, shortens the period of Sertoli cell proliferation in rodents (van Haaster et al., 1993). In addition, thyroid hormone was found to inhibit Sertoli cell proliferation by increasing the expression of the cycling-dependent kinase inhibitors (CDKIs), P27kip and P21cip, which disrupt the advancement of the Sertoli cell through the cell cycle and consequently result into premature maturation (Holsberger et al., 2003).
The peritubular myoid cells are flat, smooth-muscle-like cells that migrate into the gonad from the mesonephros and contribute to testis cord formation by surrounding the clusters of Sertoli cells enclosing germ cells, and cooperating with the Sertoli cells to form the base lamina membrane (Martineau et al., 1997). They proliferate during fetal life but decline rapidly after birth (Palombi et al., 1992). The age at which peritubular myoid cells differentiate is not clear but it was reported that these cells do not differentiate until around puberty when they become flatter and longer (Skinner, 1991). Peritubular myoid cells express all known markers of differentiation including desmin, α-smooth muscle actin (SMA) and alkaline phosphatase, shortly after birth (Palombi et al., 1992). SMA expression has long been reported in the peritubular myoid cells of ER19 fetal rat testes (Fisher et al., 2003). Expression of dhh and Protein patched homolog 1 (ptch1) is important in peritubular myoid cells differentiation and consequently cord formation as inhibition of the dhh/ptch1 signaling pathway results in disrupted cord formation (Yao et al., 2002) and mice with a null mutation for dhh have impaired differentiation of the peritubular myoid cells (Clarke et al., 2000). This is suggesting that DHH/PTCH1 transduction between SC and PTM cells may play a role in peritubular myoid cell migration and differentiation. Similarly, PTM cells have also been shown to express the androgen receptor during fetal and postnatal life (You and Sar, 1998); hence, they may likely be involved in testicular development (Anderson et al., 2002).
Primordial germ cells are the embryonic precursors of the gametes which are responsible for the transfer of genetic information between generations. Unlike in somatic cells of the testis, PGC neither arise from the coelomic epithelium nor mesonephros, but emerge from a small population of epiblast cells, which are derived from the embryonic endoderm lining the yolk sac. The yolk sac situated on the ventral surface of the embryo forms the developmental circulatory system during early embryo development. It provides nourishment and protection for the developing embryo (Ginsburg et al., 1990).
PGCs migrate along the hindgut, before colonizing the genital ridge. These cells were first thought to migrate to the genital ridge independently (De Felici and Dolci, 1987), however, studies have shown that they relate with one another through cytoplasmic processes called filopodia, which form extensive networks interlinking the cells (Bendel-Stenzel et al., 2000). Cadherins, a family of cell adhesion molecules were shown to be involved in the association of the primordial germ cells during the migration since the absence of E-cadherin has caused an increase in the number of ectopic primordial germ cells (Bendel-Stenzel et al., 2000). The PGCs proliferate rapidly during their migration to the genital ridge (Tam and Snow, 1981). After colonizing the genital ridge, they undergo the process of maturation which involves sequence of transition into fetal germ cells and express germ cell nuclear antigen-1 protein (GCNA1 protein), a marker of post-migratory germ cells (Enders and May, 1994). The germ cells at this stage are bipotential, capable of developing as primary meiotic oocytes or mitotic spermatocytes. Whether they become oocytes or spermatocytes, is dependent upon the sex of the gonad (Ford et al., 1975) that is their surrounding environment rather than the chromosomal sex of the germ cells themselves. For instance, XY germ cells can develop as oocytes in a phenotypically female chimaeric embryo and XX germ cells can develop as spermatocytes in a phenotypically male chimaeric embryo (Palmer and Burgoyne, 1991; Kocer et al., 2009). In other word entry into meiosis is inherently based on a cell-autonomous programme (McLaren and Southee, 1997). The embryonic testis was thought to produce an unknown factor that inhibits entry into meiosis and rather initiates mitotic arrest, therefore establishing a spermatogenic fate (McLaren and Southee, 1997). Retinoic acid is usually produced by the mesonephros of the bipotential gonad (Bowles et al., 2006) inducing germ cells to enter meiosis and establish the fate of female embryo but the male germ cells have been said to be protected from retinoic acid effect by the Sertoli cells, which express P45026, an enzyme that catabolises retinoic acid and consequently acts as a male-specific meiosis-inhibiting factor (Bowles et al., 2006). Li et al. 2009 also reported that P45026 in Sertoli cells acts as a masculinising factor to arrest male germ cells in the G0 phase of the cell cycle and prevents them from entering meiosis. The gonocytes remain mitotically arrested until after birth when they resume proliferation (McLaren, 1984). They then migrate from the centre of the cord to the basement membrane and start to differentiate into spermatogonia (Boulogne et al., 2003).
The primary function of Leydig cell in the testis includes steroid synthesis. Two types of Leydig cells have been identified, both of which are responsible for steroidogenesis; the fetal Leydig cells and adult Leydig cells, arising from different cell lines (Habert et al., 2001; Kerr and Knell, 1988). Both the coelomic epithelium (Yao et al., 2002; Luo et al., 1994) and mesonephros (Buehr and McLaren, 1993; Nishino et al., 2001) were suggested to contribute to the precursors of Leydig cells as the coelomic epithelium is known to give rise partly to the Sertoli cells and a significant number of interstitial cells (Karl and Capel, 1998). These two cell lines are structurally similar, but their functional properties differ considerably (Huhtaniemi, 1989). The main origin of fetal Leydig cells remains controversial as many studies have been involved in this subject and no definitive evidence was shown. They were thought to differentiate from mesenchyme-like stem cells (Byskov, 1986). In addition, neural crest has been suggested to contribute to the fetal Leydig cell population, as these cells express the neural cell adhesion molecule (NCAM) (Mayerhofer et al., 1996). The primary role of the fetal Leydig cells is to produce androgens for masculinisation of the embryo and to secrete insulin-like growth factor 3 (Insl3), which, combine with androgen action to induce testicular descent (Klonisch et al., 2004). The adult Leydig cells differentiate after birth, and are thought to evolve from undifferentiated precursor cells from the mesenchymal cells of the interstitial compartment (Hardy et al., 1993). However, Brennan et al. (2003) reported that coelomic epithelium is not the main origin of Leydig cells although; some of them may differentiate from the coelomic epithelium.
Fetal Leydig cell differentiation and development requires activation of sf1 and dhh (Park et al., 2007). Fetal DHH gene could be a target for EDCs' action during testis development. Maternal smoking during pregnancy specifically reduced human fetal DHH expression during testis development (Fowler et al., 2008). Sertoli cells, peritubular myoid cells, endothelial cells and interstitial fibroblasts are also involved in Leydig cell differentiation. Sertoli cells activate dhh and pdgf-α that promote Leydig cell differentiation while others express the X-linked aristaless related homebox gene (arx), which has been shown to contribute to Leydig cell development (Kitamura et al., 2002). The fetal Leydig cells are more active and steroid production per cell is much greater than in the adult Leydig cells (Huhtaniemi et al., 1982). This may be because of the non-regulatory nature of the testosterone synthesis from the fetal Leydig cells. In sheep, mitotic activity of Leydig cells is similar to that of Sertoli cells; at least, seven and six mitotic divisions were reported before birth and before day 110 of gestation respectively (Hochereau-de Reviers et al. 1995). However, Leydig cells decrease in size with increasing fetal age, indicating likely decrease in their secretion during the last month of gestation. Adult Leydig cell steroidogenesis is regulated by luteinizing hormone (LH), component of the hypothalamus pituitary gonadal axis (HPG-axis). Perinatal regulation of steroidogenesis requires LH (O'Shaughnessy et al., 1998) indicating, there must be a switch, around the time of birth, from gonadotrophins independent to gonadotrophins dependent steroidogenesis (O'Shaughnessy et al., 1998).
This review has shown various reproductive health risks associated with EDC exposure. Testicular cells can be a target for EDC adverse effects and EDC exposure responses maybe different among testicular cells. The EDC effects can be directly on the cells number or shape through several other mechanisms which can influence cell function. There is need to investigate what other mechanism plays a role in disrupting the development and functions of the two primary cells in the testis with respect to EDC exposure.