Nanoparticles and female reproductive system: how do nanoparticles affect oogenesis and embryonic development

By TEM analysis, Kertschanska et al. (1997) demonstrated that the placental channels that begin from the basal trophoblastic plasmalemma and terminate on the maternal surface range from 15-25 nm in diameter under normal intravascular pressure [ 92 ]. Therefore, this pore size would allow the NPs of size under 25 nm to cross the PB by passive diffusion. It was demonstrated that NPs of polystyrene beads with 50, 80 or 240 nm in diameter could cross the barrier without impairing its function. In contrast, 500-nm beads were significantly blocked. The authors suggested that the fast transport of NPs with diameters of 50 and 80 nm may occur by diffusion [ 64 ]. These results are similar to those of previous studies on rodent placenta where size was also a factor. Silicon NPs with a size of 519 nm passed the PB, while those of sizes 834 and 1000 nm were unable to penetrate it [ 93 ]. The permeability of NPs is also related to the various NP coatings. Myllynen et al. studied PEGylated gold NPs in both open and recirculating dual human placental perfusion systems. These NPs aggregated in the syncytiotrophoblast cell layer rather than crossing the PB [ 60 ]. A recent study showed that the intravenous administration gold NPs (20-nm and 50-nm NPs) were transported by endocytosis into placental cells [ 62 ]. Chun et al. also showed that QDs could be internalized by endocytosis and then migrate into fetal blood through fetal capillary pores [ 88 ]. The possible mechanism of endocytosis was related to clathrin and caveolin as the placenta has increased expression of clathrin and decreased expression of caveolin [ 62 ]. Therefore, although the mechanism of NP transport through the placenta is not fully understood, according to existing results, the main pathway of NP transport seems to be that of endocytosis [ 62 ]. In addition, diffusion has also been mentioned to be related to size-dependent transport of NPs. Selective permeability and passive and active transport must also be taken into account. Another possible mechanism relating to cell structure, called the ‘transtrophoblastic channel’, has also been suggested [ 64 ]. Due to the different results in various type, coating, or diameter of NPs, several of the above mechanisms may need to be considered in combination. The toxicity of NPs in pregnancy and embryonic development is shown in Figure 3 [ 63 , 64 ]. The mechanisms that are responsible for the transport of NPs across the PB should be investigated to prevent damage to the development embryos. Meanwhile, understanding of the molecular transport mechanisms is important for accelerating the development of new therapeutic tools. However, there is some evidence suggesting that certain NPs cannot pass through the PB. CdTe QDs coated with polyethylene glycol or mercaptopropionic acid, for example, were injected into Wistar rats, and subsequent penetration through the placental barrier was observed [ 94 ]. These QDs were mostly found in the complex cell structure of the placenta [ 94 ]. PEGylated gold NPs (size: 10-30 nm) could not cross the perfused human placenta in detectable amounts into the fetal circulation within 6 h [ 60 ]. In future studies of transport of NPs across the PB, rodent placenta and placenta perfusion models may be efficient techniques to investigate the transport of NPs between the mother and fetus [ 61 , 63 , 83 ]. Unfortunately, recent data on the cellular mechanisms underlying the variable permeability of NPs across the PB are still unclear. Thus, there is a need to balance the application of the NPs during pregnancy to prevent impeding embryogenesis.

In murine fetuses, the concentration of NPs was markedly decreased in a manner concurrent to the maturation of placental barrier (PB). This suggested that the PB prevents the penetration of NPs [ 55 ]. Nonetheless, the concern for the potential effect of NPs on fetal health remains due to the sensitivity of the fetus to many toxins. Several studies found that NPs could traverse the rodent PB and result in varying levels of fetal harm (Tables 1 - 4 ). The PB consists of three different layers of cells, namely, the syncytiotrophoblast, cytotrophoblast and fetal capillary endothelium. The PB is an important system in the exchange of materials between the mother and fetus. Additionally, the placental barrier acts as a natural barrier, as it prevents harmful substances from invading the fetus [ 56 ]. Generally, the placental barrier is formed at approximately GD10-12 in mice and at approximately 4 months of pregnancy in humans [ 27 ]. However, some NPs may cross the placental barrier and harm the fetus. In several studies, NPs were observed to penetrate the PB, while in other studies, the NPs were seen to be trapped in the PBs. For NPs that could reach the fetal tissues, some were suspected to harm fetal development and alter gene expression in the fetus, while some had no influence on the fetus [ 57 , 58 ]. These diverse results are mainly due to the different size, coatings, and types of NPs [ 59 ]. Additionally, in order to study the effects of NPs on embryonic development as well as their application in fetal treatment, in vivo and ex vivo models of the human PB have been recommended [ 60 , 61 ]. Nevertheless, the molecular transport mechanisms of NP penetration across the placental barrier are still poorly understood. There could be many potential pathways such as diffusion, passive transport, active transport, or the hypothetical ‘transtrophoblastic channel’ [ 62 - 64 ]. Pregnant (20 days old) and lactating (14-16 days old) female Wistar rats were intragastrically administered with [ 110m Ag]-labeled Ag NPs (34.9 ± 14.8 nm) at doses of 1.69-2.21 mg/kg. After labeling for the following 24 and 48 h, a low-background semiconductor gamma-ray spectrometer was used to evaluate the accumulation of Ag NPs in the offspring and nursing pups consuming their mother’s breastmilk [ 65 ]. The results showed that the average level of accumulation of NPs in the fetuses was 0.085-0.147% of the administered dose, which exceeded the accumulation of NPs in the brains of females by at least 10-100 times and was comparable to the penetration of the NPs into tissues such as the liver, blood and muscles [ 65 ]. During the 48 h period of lactation, the total accumulation of [ 110m Ag]-labeled Ag NPs in the milk was at least 1.94 ± 0.29% of the administered dose, and the amount absorbed by the pups from the lactating mother was at least 25%, which indicated that Ag NPs could penetrated the PB and get transferred from the mother to offspring through breastmilk [ 65 ]. To evaluate the potential developmental toxicity of silver in both Ag NPs and Ag + ionic forms, pregnant rats (7-20 days old) were orally administered both ionic Ag + (AgNO 3 , 20 mg Ag/kg/day) and Ag NPs (55 nm, from 0.2 to 20 mg/kg/day). The results showed that oral administration of AgNO 3 led to an increase in glutathione peroxidase (GPx) activity in both the adult and offspring brains resulting in hippocampal neuronal damage. Moreover, the Ag level in both maternal and offspring blood in the AgNO 3 -treated group was significantly higher than that of the Ag NP-treated group, which indicated that 1. both Ag+ ions and Ag NPs could translocate across the PB and 2. The reproductive toxicity of AgNO 3 was higher than that of Ag NPs [ 66 ]. In a similar study, pregnant mice (7-, 8- and 9-days old) were intravenously injected with 10 nm Ag NPs or AgNO 3 at a dose of 66 mg Ag/mouse. The results showed that the accumulation of NPs in the different tissues of mice treated with 10 nm Ag NPs was more on gestation day (GD) 10 than that on GD16, and the Ag concentration in the visceral yolk sac (VYS) of AgNO 3 -treated group was 2-fold that in the Ag NP-treated group. The only significant reproductive parameter was that approximately 80 percent fetuses in the experimental groups appeared small for their age compared to only 9 percent fetuses in the control group, which may have been due to the accumulation in embryos. These results indicated that a large amount of Ag in maternal tissues and a small amount in embryos may impact embryonic growth, but the mechanism is unclear [ 67 ]. Exposure to Ag NPs increases the risk of damage to the nervous system of fetuses. Thirty first-time pregnant NMRI mice were subcutaneously administered with 0, 0.2 and 2 mg/kg of body weight of Ag NPs once every three days from gestation day 3 until delivery. The Morris water maze (MWM) test showed that the spatial learning and memory of the offspring were impaired, which indicated that prenatal exposure to Ag NPs might have adverse effects on the central nervous system development in the fetus [ 68 ]. Intraperitoneal injection of Ag NPs (20-50 nm, 0.427 mg/g) every two days from GD10 to GD18 in prenatal rats also demonstrated that Ag exposure in maternal rats could result in cognitive impairment in the offspring. Histological assessment showed that the hippocampal structure of the offspring was deformed compared to those in control groups, and the MWM test demonstrated impaired spatial cognition in the male offspring [ 69 ]. Sprague Dawley female rats were orally administered with Ag NPs (7.9 ± 0.95 nm) at a dosage of 250 mg/kg from 14 days before mating to the fourth day after delivery (along with synchronous lactation). The results of ICP-MS and electron microscopy showed that the Ag NPs had abundantly accumulated in the tissues of the offspring compared with the tissue in the control groups (12.3-fold in the kidneys, 7.9-fold in the liver, 5.9-fold in the lungs, and 5.4-fold in the brain), which also indicated that the possible transfer of Ag NPs from pregnant rats to offspring occurs mainly through the placenta or breastmilk [ 27 ]. The size and coating of metal NPs are important factors in determining whether they can penetrate the PB and result in developmental toxicity. Three different-sized Au NPs (3 nm (Au3), 13 nm (Au13) and 32 nm (Au32)) were administered to pregnant mice with intrauterine inflammation. The results showed that Au3 and Au13 NPs could cross the PB and accumulate in the fetuses, resulting in increasing intrauterine inflammation. However, Au32 NPs could not cross the PB in either the mice with intrauterine inflammation or healthy mice, which indicated that particle size is an important factor in the penetration of PB [ 70 ], consistent with the results of Yang et al. (2014). The surface composition of metal NPs also showed differences in different placental damage and fetotoxicity. Pregnant mice were intravenously administered with 13 nm Au NPs with the following three types of surface modifications: Au-Ft (coated with ferritin, treatment concentration 1.1*10 17 /ml), Au13-PEG (coated with PEG, treatment concentration 8.3*10 12 /ml) and Au13-CT (coated with citrate, treatment concentration 8.3*10 12 /ml) at E5.5-15.5. The amount of accumulated Au-Ft and Au13-PEG NPs was significantly greater than that of Au13-CT NPs in the fetus and extraembryonic tissues; however, none of the groups showed developmental toxicity in the fetuses [ 55 ]. Adult female rats gavaged with 100 mg/kg TiO 2 NPs (10 nm) from GD2-21 exhibited effects on offspring in various aspects, such as memory impairment and decrease in hippocampal cell proliferation [ 71 , 72 ], while oral treatment with the same dose during lactation on the same days resulted in a decline in spatial recognition memory and deficiency in learning of offspring [ 73 ]. Exposure to polyalcohol-coated TiO 2 dust (21 nm) via inhalation for 1 h/day at a concentration of 42 mg/m 3 could induce long-term lung inflammation accompanied by differential cell counts of bronchoalveolar lavage fluid in pregnant mice and cause moderate neurobehavioral alterations in the offspring, while the cognitive function was unaffected [ 57 ]. Prenatal TiO 2 (∼25-75 nm) exposure, via injection of 100 µl/time four times on days 6, 9, 12 and 15, could result in alteration of the olfactory bulb, cerebral cortex and regions related to the dopamine systems in the offspring. Gene expression in the offspring was also dysregulated, including genes related to the striatum, dopamine neuron system and the prefrontal lobe [ 74 ]. Pregnant mice were exposed to 42 mg of titanium dioxide (UV-Titan)/m 3 via inhalation for 1 h/day from GD8 to GD18. A comet assay revealed that the pregnant mice and offspring did not have any DNA strand breaks. While transcriptional profiling of offspring livers demonstrated that the expression of genes related to the retinoic acid signaling pathway was changed in the female offspring, which indicated that the inhaled UV-Titan could cross the PB and disturb gene expression of the offspring [ 75 ]. Coincidence with the abov study that slight neurobehavioral alterations were noted in the fetus of mice treated with UV-Ti NPs (of an average size of 21 nm) via inhalation [ 57 ]. The same study also found that TiO 2 NPs could affect the development of the fetal central nervous system [ 58 ]. Silica particles nSP70, nSP300 and mSP1000 and TiO 2 NPs of diameters of 70 nm, 300 nm, 1000 nm and 35 nm, respectively, were intravenously injected into the placenta at a dose of 0.8 mg per mouse. Transmission electron microscope (TEM) analysis revealed that the nSP70 NPs could accumulate in the fetus and maternal placenta, and the TiO 2 NPs had also accumulated in the fetal liver and brain and placental trophoblasts. The mice treated with 70 nm silica particles and 35 nm TiO 2 NPs showed 20% and 30% respective decrease in uterine weight, smaller fetuses (∼10%) and smaller amniotic sacs. A TdT-mediated dUTP Nick-End Labeling (TUNEL) assay indicated that nSP70 could induce apoptotic cell death of spongiotrophoblasts resulting in variable structural abnormalities of the mouse placenta. However, the silica particles in the other groups exhibited no accumulation in the placenta, fetal liver or fetal brain and displayed no fetotoxicity or placental dysfunction. All of these results indicated that nSP70 and 35 nm TiO 2 NPs might affect maternal-fetal exchange, resulting in fetal resorption and restricted fetal growth. Therefore, these detrimental effects of NPs in fetuses and placenta may be linked to the size of NPs [ 76 ]. With the increase in the application of iron oxide NPs in photocatalysis, drug delivery and biomedical imaging, the risk of exposure to iron oxide NPs in humans, especially pregnant women and developmental fetuses, is of great concern. To assess the reproductive toxicity of Fe 3 O 4 NPs, dimercaptosuccinic acid (DMSA)-coated Fe 3 O 4 NPs were intraperitoneally injected into pregnant mice. At doses higher than 50 mg/kg, the weight of infants showed a significant decrease, and the male pups exhibited significant decrease in spermatogenic cells (spermatogonia, spermatocytes, spermatids and mature sperm) by testicular histological results, which indicated that DMSA-coated Fe 3 O 4 NPs can disrupt embryonic development at doses higher than 50 mg/kg [ 77 ]. CD-1 mice were intraperitoneally injected with PEI-Fe 2 O 3 NPs (∼28 nm, zeta potential: 51 mV) or PAA-Fe 2 O 3 NPs (∼30 nm, zeta potential: -52 mV), which were coated with the hydrophilic ligands polyethyleneimine (PEI) or poly(acrylic acid) (PAA), respectively. The results indicated that both positively charged PEI-Fe 2 O 3 NPs and negatively charged PAA-Fe 2 O 3 NPs had the ability to cross the placenta and accumulate in the fetus, though multiple doses of positively charged PEI-Fe 2 O 3 NPs resulted in significantly accumulation of iron in the placenta and increased fetal death over several days [ 78 ]. Whether Fe 2 O 3 NPs can cross the human PB also depends on their diameter. In vitro analysis showed that large (50 and 78 nm) but not small (15 nm) α-Fe 2 O 3 could increase cell death and ROS resulting in disruption of BeWo epithelial barrier functions [ 79 ]. To study the effects of ZnO NPs, pregnant rats were treated with 500 mg/kg body weight of ZnO NPs of less than 100 nm in diameter. The ZnO NPs were distributed in mammary tissues of the dams together with the liver and kidneys of pups. The accumulation of ZnO NPs could increase fetal resorption and decrease the body weight of pups [ 80 ]. Liu et al. found that ZnO NPs exposure (ZnSO 4 -200 mg/kg and ZnO-NP-200 mg/kg of diet) in hens could increase γ-H2AX and decrease NF-κB to decrease cell proliferation or increase apoptosis in embryos. The underlying reason was that ZnO NPs may damage DNA replication and repairmen machinery in hen oocytes, which subsequently inhibited embryonic development [ 81 ]. To detect the toxicity of cadmium oxide (CdO) NPs in pregnant mice and offspring, pregnant CD-1 mice were exposed to CdO NPs (15.3 nm ± 1.6 nm, 230 μg/m 3 ) via inhalation from GD4.5 through GD16.5, and the nephrotoxic indexes were examined. The results showed that mRNA expression of kidney injury molecule-1 (Kim-1) in the urinary tract was five-times higher in the pregnant mice at GD10.5 and 3.2-times higher in the neonatal offspring at PND14 than the levels in the corresponding controls, which demonstrated that inhaled CdO NPs could enter circulation and penetrate the PB resulting in their accumulation and renal injury in fetuses and mothers [ 82 ]. Similarly, a study on CdO NPs by inhalation also demonstrated that the decrease in fetal weight was due to the accumulation of NPs in the placenta [ 83 ]. To simulate the in vivo human placenta, a well-organized 3D co-culture microtissue (MT) model was developed, which consisted of placental fibroblasts surrounded by a trophoblast cell layer. The results showed that incubation with CuO NPs (4 nm) could decrease the viability of the MT and reduce the release of human chorionic gonadotropin (hCG) [ 84 ]. Additionally, the ex vivo human placental model provides a convenient method for studying the mechanism by which NPs cross the human PB. Exposure of prenatal mice to carbon black NPs (CB-NPs; 95 mg/kg; particle size: 14 nm; surface area: 300 m 2 /g) by intranasal instillation on GD9 and GD15 could increase total thymocyte and total lymphocyte counts, promote immune responses and alter gene expression associated with the induction of peripheral tolerance in male offspring. These results indicated that respiratory exposure to CB-NPs during pregnancy may result in inflammatory or allergic effects in the offspring [ 85 ]. Moreover, intranasal instillation of CB-NPs in pregnant mice on GD5 and GD9 could decrease CD3+ (T), CD4+ and CD8+ T cells in the spleens of 1- to 5-day-old offspring. In addition, CB-NPs could also significantly upregulate the expression level of ll15 in the newborn male offspring as well as Ccr7 and Ccl19 in the female offspring. These results indicated that exposure of pregnant mice to CB-NPs may suppress the development of the immune system in the offspring [ 86 ]. Exposure of pregnant mice to CB-NPs (95 mg/kg; particle size: 14 nm) by intratracheal administration on GD7 and GD14 resulted in partial vacuolation of seminiferous tubules and reduction in cellular adhesion of seminiferous epithelia and in daily sperm production (DSP) in male offspring. In addition, the body, testis and epididymis weights and concentration of serum testosterone were also different between the control and CB-NP groups, which suggested that exposure to CB-NPs could affect the reproductive function of male offspring [ 87 ]. In another study, 200 μg of 14-nm carbon NPs was administered by inhalation into pregnant mice on days 7 and 14. The daily sperm production was significantly decreased in the carbon nanoparticle-exposed fetuses [ 87 ]. Currently, quantum dots are gaining popularity in their application in both biomedical imaging and targeted therapeutics. Whether QDs are transferred from the pregnant mother to its fetus may depend on their size, dose, charge, capping material properties and inorganic components. To evaluate the clinical safety of CdTe/CdS QDs, Chu et al. studied pregnant mice that were intravenously injected with four different doses (20, 50, 86, or 125 mg), three different sizes (MPA-coated QDs (532), MPA-coated QDs (599), MPA-coated QDs (656)), and three different coatings (MPA-coated, PEG-coated and SiO 2 -coated QDs (656)) of Cd-containing QDs. The results showed that abundant Cd atoms derived from the QDs were accumulated in the pups, and the amount of Cd atoms increased with increasing doses of QDs. An analysis of the size dependence of Cd-QD NPs demonstrated that smaller QDs were more efficiently transferred into the pups, which implied the presence of extracellular transport pathways across the placenta. Assessment of three different coatings of Cd-QDs showed that the average concentration of Cd in the MPA-coated QD-treated pups was higher than that of the PEG-coated and SiO 2 -coated QD-treated groups. The authors of this study concluded that the PB could not prevent Cd-QDs from entering the pups, and the ability of QDs to travel from the mothers to pups depend on the dosage, size and coating components [ 88 ]. Mice were intraperitoneally injected with PEG-coated CdSe QDs (4 nm) suspended in PBS at the dosage of 150 μg/kg body weight (containing 3.75 μg Cd/Te-cores) or 750 μg/kg body weight (containing 18.75 μg Cd/T-cores) every 3 days for 5 weeks. A small amount of Cd was found in the placenta of the high concentration group, which indicated that the ability of the PEG-coated CdSe QDs to cross the PB was dose-dependent [ 89 ]. Pregnant mice were injected with CdSe/ZnS QDs (∼20 nm) or CdSe QDs (∼15 nm) at a concentration of 0.5 µM, 100 µL/mice/day at GD16 and GD17. RT-PCR assay showed that in both treatment groups, the expression of symbolic genes, such as p53 and bax (related to apoptosis), IGF-1 and EGF (related to tissue development), MT-1 (related to metal transport), was significantly altered. The CdSe/ZnS QD-treated group exhibited milder toxicity compared with the CdSe QD-treated group, which could be attributed to the protection of the ZnS surface coating [ 90 ]. The results from another previous in vitro study were consistent with the finding above. To assess the cytotoxic effect of CdSe-core QDs on embryonic development, blastocysts were obtained from mouse uterine horn on the fourth day of pregnancy and treated with CdSe-core QDs (0, 25, 250 and 500 nmol/L) for 24 h. TUNEL staining analysis showed that mouse blastocysts underwent apoptosis in response to CdSe-core QD in a dose-dependent manner. Dual differential staining revealed that proliferation in blastocysts was decreased by CdSe-core QDs, resulting in the inhibition of post-implantation embryonic development. However, the ZnS coating of CdSe QDs could significantly decrease these cytotoxic effects on embryonic development [ 91 ]. Generally, the PB is formed at approximately GD10-12 in mice and at approximately 4 months of pregnancy in humans [ 27 ]. After the formation of PB, the toxic NPs with less than 50nm particles showed injury to placenta and accumulated in the fetus, which indicating that less than 50nm of NPs can penetrate the PB. While, the size of NPs penetrated the BTB is smaller than 4 nm. Compared with BTB, the penetrability of PB may be attribute to its function, which is an important system in the exchange of nutriment or excretory metabolism between the mother and fetus. In summary, damage by the NPs to the PB and embryo is related to the following aspects: 1. the physicochemical properties of NPs (size, dosage, shape, charge, material and surface-coating). There is a negative correlation between the rate of passage through the PB and size of the nanomaterials, which may be closely related to the pore size of the placental barrier. Surface modification materials affect the penetration of NPs by changing their physicochemical properties. After NPs enter a pregnant woman’s body through inhalation, venous injection, ingestion or skin permeation, maternal toxic stress reactions such as ROS, inflammation, apoptosis and endocrine dyscrasia are induced. During pregnancy, NPs may across the placenta into the fetus by passive diffusion or endocytosis. The toxic effect of NPs can trigger fetal inflammation, apoptosis, genotoxicity, cytotoxicity, low weight, reproductive deficiency, nervous damage, and immunodeficiency, among other mechanisms, which can result in abnormal embryonic development and fetal death (Figure 3 ). 2. the health of the uterus, NPs are more likely to pass through the PB in an inflamed uterus. Thus, more attention should be paid to avoid exposure to NPs, especially in pregnant females. These toxicity profiles of NPs in embryonic development will provide the latest information for reasonable applications of NPs. Factors affecting the toxicity of NPs are their size, dosage, shape, charge, material and surface-coating. After NPs enter a pregnant woman’s body through inhalation, venous injection, ingestion or skin permeation, maternal toxic stress reactions such as ROS, inflammation, apoptosis and endocrine dyscrasia are induced. During pregnancy, NPs may across the placenta into the fetus by passive diffusion or endocytosis. The toxic effect of NPs can trigger fetal inflammation, apoptosis, genotoxicity, cytotoxicity, low weight, reproductive deficiency, nervous damage, and immunodeficiency, among other mechanisms, which can result in abnormal embryonic development and fetal death.

With the increased application of engineered NPs in cosmetics and textiles, together with the inhalation of NPs polluting the air, understanding the reproductive toxicity and transferable adverse effects of next generation is necessary. Interestingly, NPs are a double-edged sword: on one hand, owing to their peculiar physical and chemical properties, NPs can be used in commodities (such as cosmetics and textiles), in drug delivery systems and in clinical therapy and can provide substantial advantage and effectiveness in these fields [ 95 ]; on the other hand, due to the non-degradable properties of NPs, increasing evidence from research has shown the potential of many adverse health effects relating to the use of or contact with NPs. Many of these concerns have been highlighted from both in vivo and in vitro studies. However, while the studies on the toxicity of NPs have been far fewer than those on the positive application of NPs, the small size of NPs allows them to easily enter the body, particularly via the skin, eyes, gastrointestinal tract and nasal olfactory structures, at which point many potential harmful effects may occur. Subsequently, these NPs can enter systemic circulation and traverse tissues, cells and organelles as well as the reproductive organs [ 96 , 97 ]. This review has discussed the present knowledge on the influence of NPs on oogenesis, ovarian structure, hormonogenesis and embryonic development (Table 1 - 4 ). Recent studies have shown that NPs can cause genotoxicity, cytotoxicity and abnormal development of the embryo. With the application of ENPs in commercial and industrial products, the risk of environmental exposure is growing. However, it is rather difficult to compare reproductive toxicity between studies, especially because the variety and dosage of NPs are very diverse. The application of NPs in pregnant women and fetuses still needs more in-depth studies. This review also provided a reference for the application of NPs in the clinic for gynecological disease.

Nanoparticles (NPs) are characterized as particles with sizes between 1 to 100 nm. NPs exist in the natural environment due to biological, physical and chemical processes [ 1 ]. Moreover, due to their properties, including small particle size and a relatively high surface area, numerous applications of NPs are likely to further increase human exposure to NPs through inhalation, ingestion and dermal absorption, among other mechanisms [ 2 , 3 ]. It cannot be ignored that the exposure to nanomaterials is potentially hazardous to the human body and environment. The negative impact of NPs on human health depends on individual factors, such as genetics and existing diseases as well as on the properties of NPs such as shape, size, structure, and inorganic and organic coatings [ 4 , 5 ]. In recent years, many studies have reported toxic effects of NPs, mainly consisting of metal nanomaterials, nanometer oxides, carbon NPs and quantum dots [ 6 ]. Recent studies have shown that NPs can penetrate cells and subsequently disrupt their biological structures and normal functions via generation of ROS or by increasing intracellular oxidative stress [ 3 ]. The toxic effects induced by NPs include tissue inflammation and the imbalance of the cellular redox state, resulting in apoptosis or cell death [ 7 - 9 ]. Moreover, some NPs can penetrate the blood-testis barrier, placental barrier and blood-brain barrier and accumulate in different cells [ 10 - 12 ]. Reproductive toxicity caused by NPs is gradually rising in importance. The studies on the toxicity of NPs in the female reproductive system mainly include effects on reproductive ability, teratogenic effects during embryonic development and impact on the offspring during the perinatal period [ 12 , 13 ]. Recently, studies have shown that inhaled, ingested or dermally absorbed NPs are able to translocate through the circulatory system and even accumulate in different reproductive organs and in the fetus [ 14 , 15 ]. Moreover, the reproductive toxicity of NPs in different germ cell lines in vitro and animal models in vivo are being increasingly reported. For example, in vitro studies showed that some NPs could be swallowed by granulosa cells, resulting in changes in the secretion of hormones and dysplasia of the ovum [ 16 ]. There are well-documented studies showing that NPs can enter both thecal cells and granule cells and affect their normal function, particularly relating to their key role in hormone secretion [ 16 ]. Before ovulation, androgens and androstenedione secreted by thecal cells diffuse into granule cells and are transformed into steroid hormones. During this process, NPs can directly affect the secretion of sex hormones by destroying these secretory cells in the ovaries [ 17 , 18 ]. In vivo studies have shown that long-term (90 consecutive days) exposure to titanium dioxide NPs (TiO 2 NPs) in female mice results in an imbalance of sex hormones and mineral element distribution, leading to a reduction in pregnancy rate and oxidative stress and disruption of ovarian gene expression [ 19 , 20 ]. Moreover, in vivo experiments in rats showed that silver NPs of 34.9 ± 14.8 nm in size could get transferred from the mother to offspring through the placenta and breast milk [ 20 ]. Oogenesis, or ovum production, is the process of development from oogonia to a mature egg occurring in ovarian follicles [ 21 ]. Follicular atresia is a natural physiological process for follicle development, follicle maturation and ovulation in mammals. The regulated hormones of follicle atresia include estrogen, gonadotropin-releasing hormone (GnRH), gonadotropic hormone, androgen and growth hormone, among others [ 22 , 23 ]. A typical follicle consists of the following layers (from the outside to inside): a thecal cell layer, basement membrane, granulosa cell layer, zona pellucida and oocyte. Recent reports showed that NPs could be endocytosed by thecal cells and granulosa cells, leading to abnormal hormone secretion and termination of oocyte development in vivo [ 17 ]. In vitro experiments also suggested that the engulfment of 10 nm nanogold particles by granulosa cells could result in steroidogenesis imbalance and ovum dysplasia [ 16 ]. In other words, NPs of a particular size can accumulate in secretory cells and directly affect hormone secretion in the ovaries. However, there is no evidence showing that NPs can actually penetrate oocytes and accumulate inside them as of yet. The reason for this may be attributed to the multiple layers of follicles and the special structure of zona pellucida [ 24 ]. NPs may cross or circumvent the blood-brain barrier (BBB) and accumulate in the central nervous system (CNS) [ 25 ]. One of the potential harmful impacts from such stimulation of the nervous system by NPs is the disruption of hormone secretion. The neurohormones such as GnRH, follicle stimulating hormone (FSH) and luteinizing hormone (LH) secreted by the hypothalamus and pituitary play crucial roles in positive and negative feedback regulation during oogenesis. NPs may indirectly affect oogenesis and ovarian health by disturbing the balance of these sex hormones [ 25 ]. As commercial uses for nanotechnology and nanomaterials continue to increase across the world, the risk for unintentional exposure or purposeful application of NPs in the workplace increases, and more and more NPs can have potential generational impacts or disrupt embryonic development [ 27 ]. For instance, exposure to gold NPs (Au NPs) was reported to alter the expression of 19 genes in human fetal lung fibroblasts [ 26 ]. In this review, we mainly focus on the toxic effect of NPs on the female reproductive system and embryonic development. This review will provide guidelines for taking care of vulnerable populations such as women working in manufacturing industries. Additionally, it will provide appropriate references for reducing the risk of nanomaterial application and support reasonable industry development.