Next Article in Journal
Special Issue on “Insights on Ecotoxicological Effects of Anthropogenic Contaminants in Aquatic Organisms”
Next Article in Special Issue
Protective Role of Kelulut Honey against Toxicity Effects of Polystyrene Microplastics on Morphology, Hormones, and Sex Steroid Receptor Expression in the Uterus of Rats
Previous Article in Journal
Aflatoxin-B1-Exposure-Induced Hepatic Injury Could Be Alleviated by Polydatin through Reducing Oxidative Stress, Inhibiting Inflammation and Improving Mitophagy
Previous Article in Special Issue
First Evidence of Microplastics in Human Urine, a Preliminary Study of Intake in the Human Body
 
 
Search for Articles:
Title / Keyword
Author / Affiliation / Email
Journal
Article Type
 
 
Advanced Search
 
Section
Special Issue
Volume
Issue
Number
Page
 
Journals
Toxics
Volume 11
Issue 4
10.3390/toxics11040310
toxics-logo
Submit to this Journal Review for this Journal Propose a Special Issue
► Article Menu

Article Menu

share Share announcement Help format_quote Cite question_answer Discuss in SciProfiles thumb_up
...
Endorse textsms
...
Comment
first_page
settings
Order Article Reprints
Font Type:
Arial Georgia Verdana
Font Size:
Aa Aa Aa
Line Spacing:
Column Width:
Background:
Article

Investigation of Microplastics (≥10 μm) in Meconium by Fourier Transform Infrared Microspectroscopy

by
Zhiming Li
1,†,
Jiamin Wang
2,†,
Xia Gao
2,
Jiaxin Du
1,
Haixia Sui
3,
Jieling Wu
4,
Yizhou Zhong
1,
Boxuan Liang
1,
Yuji Huang
1,
Rongyi Ye
1,
Yanhong Deng
1,
Xingfen Yang
1 and
Zhenlie Huang
1,*
1
NMPA Key Laboratory for Safety Evaluation of Cosmetics, Guangdong Provincial Key Laboratory of Tropical Disease Research, Department of Toxicology, School of Public Health, Southern Medical University, Guangzhou 510515, China
2
Beijing Key Laboratory of Organic Materials Testing Technology & Quality Evaluation, Institute of Analysis and Testing, Beijing Academy of Science and Technology (Beijing Center for Physical and Chemical Analysis), Beijing 100089, China
3
Division III of Risk Assessment, China National Center for Food Safety Risk Assessment, Beijing 100022, China
4
Department of Healthcare, Guangdong Women and Children Hospital, Guangzhou 511442, China
*
Author to whom correspondence should be addressed.
†
These authors contributed equally to this work.
Toxics 2023, 11(4), 310; https://doi.org/10.3390/toxics11040310
Submission received: 2 March 2023 / Revised: 22 March 2023 / Accepted: 23 March 2023 / Published: 27 March 2023
(This article belongs to the Special Issue Toxicity and Health Effects of Environmental Nano-/Microparticle Exposure)
Browse Figures
Versions Notes

Abstract

:
Microplastics are prevalent emerging pollutants with widespread distribution in air, land and water. They have been detected in human stool, blood, lungs, and placentas. However, human fetal microplastic exposure remains largely under-studied. To assess fetal microplastic exposure, we investigated microplastics using 16 meconium samples. We used hydrogen peroxide (H2O2), nitric acid (HNO3) and a combination of Fenton’s reagent and HNO3 pretreatment methods respectively to digest the meconium sample. We analyzed 16 pretreated meconium samples with an ultra-depth three-dimensional microscope and Fourier transform infrared microspectroscopy. The result showed that H2O2, HNO3 and Fenton’s reagent combined with HNO3 pretreatment methods could not digest our meconium samples completely. Alternatively, we developed a novel approach with high digestion efficiency using petroleum ether and alcohol (4:1, v/v), HNO3 and H2O2. This pretreatment method had good recovery and non-destructive advantages. We found no microplastics (≥10 μm) in our meconium samples, indicating that microplastic pollution levels in the fetal living environment are miniscule. Different results between previous studies’ and ours underscore that comprehensive and strict quality control are necessary for further studies on microplastic exposure using human bio-samples.

1. Introduction

Plastics are mass-produced and widely used due to their positive properties and convenience [1]. With imperfect waste plastic management, plastic pollution is inevitable [2]. It has been estimated that plastic waste generation in 2010 was 274 metric tons (Mt), and by the end of 2015, all plastic waste ever generated from primary plastics had surpassed 5800 Mt [3]. Over time, plastics can be broken down into fragments as they undergo various physicochemical processes [4]. Microplastics (MPs, diameter <  5  mm) and nanoplastics (NPs, diameter <  100 nm) are prevailing fragments [5]. In addition to the secondary MPs generated by cracking large mass plastics by force, primary MPs are manufactured to improve the quality of products such as toothpaste and cosmetics [6]. Not only have MPs been detected in aqueous and terrestrial environments, as well as atmospheric ecosystems, but they have also been discovered in human stool [7], blood [8], lung tissue [9], and placenta [10,11]. Several experimental studies have explored the relationship between MP exposure and adverse health effects [12,13,14,15,16]. Nasal exposure to MPs causes MP deposition in the airway and induces an increase in pulmonary inflammatory cells in mice [14]. What is worse, a growing body of evidence indicates that maternal prenatal exposure to MPs increases the risk of progeny injury in mice [12,13,15,16].
Exposure to environmental pollutants in utero is especially concerning because the fetal immune and metabolic systems are still developing, and thus, are more vulnerable to the adverse effects of MPs [17]. The placenta usually protects the fetus by forming a barrier between the matrix and the fetus [18]. A recent study has unveiled an association between human MP exposure and progeny injury [10]. Despite this initial attempt, we cannot determine whether it is directly caused by fetal MP exposure, or indirectly caused by placental MP exposure. Meconium appears in utero around the 13th week of gestation and accumulates thereafter. It is the most common biological sample for in utero drug exposure assessment due to its wide detection window [19]. The composition of meconium contains mucopolysaccharides, water, bile, salts, bile acids, epithelial cells, and other lipids. Meconium is usually excreted in the first 72 h after birth, ranging in quantity from 20 to 70 g [19,20]. Up to 80% of the meconium accumulates after 38 weeks of pregnancy [19,21]. Thus, analysis of meconium provides a direct overview of the fetal exposure, primarily during the last trimester of pregnancy [22]. Due to these advantages, meconium has been used to investigate titanium dioxide nanoparticles’ materno-fetal transfer [23]. Recent studies have shown MPs in placentas and meconium samples [10,11,24,25], and support the link between high MP concentrations and microbiota genera [26]. However, there have been suspicions of contaminated meconium samples in these studies [24,25]. Moreover, they have used limited sample sizes of 2 meconium samples [24] and 4 placental samples [11]. Therefore, the assessment of fetal MP exposure in humans is a crucial unmet challenge, particularly regarding stricter quality control methods and sample sizes [27,28].
In the present study, we established an effective pretreatment method, being suitable to the MP study on meconium. To assess fetal MP exposure, we collected a total of 37 meconium samples and investigated any MPs with diameter > 10 μm in 16 meconium samples using an ultra-depth three-dimensional microscope and Fourier transform infrared microspectroscopy (micro-FTIR). This study finally provides new insight into fetal MP exposure.

2. Materials and Methods

2.1. Chemicals

Chemicals were purchased from Thermo Fisher Scientific (Waltham, MA, USA), YONGDA (Tianjin, China), Sinopharm Chemical Reagent (Shanghai, China), unless otherwise indicated. All reagents were of analytical grade or higher.

2.2. Sample Collection

The Guangdong Women and Children Hospital Scientific Research Committee on Ethics in the Care and Use of Human Samples has approved this study’s protocol (Permit No. 201801057). We collected meconium samples from 37 newborns in November 2021 at the Guangdong Maternal and Child Health Hospital. We obtained the meconium samples by scraping the top portion of meconium from cloth diapers using sterile fecal collectors. We also collected diaper controls for each meconium sample from clean parts of the same diaper. An overview of our study is shown in Figure 1.

2.3. Pretreating the Meconium Samples

We initially pretreated meconium samples using hydrogen peroxide (H2O2), nitric acid (65%, HNO3) and a combination of Fenton’s reagent and HNO3, which have been applied in previous studies on feces of various species and of human meconium [7,24,25,29]. However, these methods were not suitable for meconium samples in our study. The information of these protocols and samples can be found in the supplementary Table S1. The detailed findings are available in the corresponding Results section in the present study. Thus, we established an effective pretreatment method for meconium. In our experiment, we used ultra-pure water (resistivity ≥ 18.2 MΩ·cm) throughout. First, the samples were freeze-dried under a vacuum at −53 °C. Then, we weighed the samples (0.4038–4.6835 g) and loaded them into prewashed 50 mL transparent glass tubes. After mashing them with glass rods, we added a solution composed of petroleum ether and alcohol (4:1, v/v) to each tube, and sonicated them repeatedly. After that, the samples were allowed to stand still until they became layered. Then, we discarded the supernatant, added new solution, and sonicated them. We repeated the supernatant exchange operation until the solution became colorless. Next, we discharged the colorless supernatant and completely dried the substrates under nitrogen gas blow. We added HNO3 (65%, 5 mL/g meconium) to the substrates and left them overnight in cold water bath. Then, we used a digestion furnace to digest the dissolved substrates for 4 h at 80 °C. For muddy liquid, we added 2 mL HNO3 each time and prolonged the digestion time for 30 min until a clear transparent solution was produced, followed by the addition of 5 mL of 30% H2O2 for 30 min at 80 °C to produce a clear colorless and transparent solution. Next, we filtered the digestion solution with a stainless-steel filter membrane (10 μm) and a suction device. To remove any remaining grease and promote the MP recovery rate, we rinsed the filters and containers several times in 70 °C water. Finally, we used toothless stainless-steel tweezers to remove the filter membranes, placed them into petri dishes, and either air-dried or dried them with a 50 °C heating element. We set three procedure blank controls (without meconium) and pretreated them in the same way. Finally, we only pretreated 16 meconium samples from 37 newborns due to the limited quality (sample weight was small) of the meconium sample from 21 newborns to assess fetal MP exposure.

2.4. Recovery Experiment

We performed the recovery experiment using 50 μm diameter and 200 μm diameter polystyrene (PS) standard before sample detection. We added PS standard to 10 mL HNO3, then left it at room temperature overnight. Then, we conducted digestion at 80 °C for 4 h. We added 2 mL H2O2 to the solution and conducted digestion again at 80 °C for 1 h. Then, we added 70 °C ultra-pure water to the digestion solution until there was 50 mL of it and filtered it using a 10 μm stainless-steel filter membrane and a suction device. In addition, we rinsed the container and filtered the membrane several times using 70 °C hot water. Finally, we used toothless stainless-steel tweezers to remove the filter membrane and put it into a petri dish, and either air-dried or dried it with a 50 °C heating element. After treatment, the number of MPs was counted with an ultra-depth three-dimensional microscope and the recovery rates of MPs were calculated. Three replicates were conducted.

2.5. Analysis of Samples by Ultra-Depth Three-Dimensional Microscope and Micro-FTIR

We observed the color, size, and shape of the targets (potential MPs) on a stainless-steel membrane with an ultra-depth three-dimensional microscope (VHX-600, Keyence, Osaka, Japan). Before observation, we adjusted the white balance for color correction. Next, we put the filter membrane under the objective lens. Then, we performed micro-FTIR (HYPERION2000, Bruker, Karlsruhe, Germany) to identify the target objects (potential MPs). We analyzed in the attenuated total reflectance mode with a mercury–cadmium–telluride detector, with a wavenumber range of 400–4000 cm−1 and a resolution of 4 cm−1. We examined the background of the air by aligning the beam with air, scanned the target objects, and collected the infrared characteristic spectra. The collected infrared characteristic spectra had been reduced from the background spectra of the air. We compared the target objects’ infrared spectra with the Omnic and Bruker reference spectra database, and conducted qualitative analysis to determine the suitability of the fit. If the spectral similarity exceeded 70% when compared with the reference MPs, and infrared expert could detect the presence of characteristic infrared peaks, we defined the particles as MPs.

2.6. Quality Control

To minimize the risk of MP contamination from other sources, we applied various measures. Our colleagues received training to familiarize them with the experimental process, including meconium collection. We handled the samples in an isolated, clean, and windowless room with restricted access. Throughout every step of the laboratory work, we wore clean cotton laboratory coats and natural latex gloves. Additionally, we rinsed all utensils with ultra-pure water and dried them in an oven before use. We also collected diaper controls to exclude the possible contamination during meconium sampling. The diaper controls were collected by clean scissor (rinsed with prefiltered water) from the surface of cloth diapers into sterile fecal collectors. The details about the diapers can be found in the supplementary Figure S1. At the meanwhile, 3 procedure blank controls were performed to rule out the possibility of contamination from sample pretreatment and the examination process.

3. Results

After H2O2 pretreatment for nine months, the meconium samples had yet to fully digest, and this affected the MP observation (Figure 2A). In addition, the meconium samples were also not fully digested after treatment with HNO3, nor with a combination of Fenton’s reagent and HNO3, respectively (Figure 2B,C). However, with our new pretreatment methods, meconium samples could be completely digested (Figure 2D). A comparison of these pretreatment methods is shown in Table 1.
In the recovery experiment, 50 μm and 200 μm PS-MP standard particles initially showed a spherical shape (Figure 3A,B). After pretreatment, two types of PS-MP standard particle also appeared as spheres (Figure 3C,D). The average recoveries of 50 μm and 200 μm PS-MP particles were 84.69% and 66.80%, respectively (Table 2). These results suggested that the pretreatment method was feasible.
Then, we identified several potential MPs via an ultra-depth three-dimensional microscope (Figure 4) within 16 meconium samples. Furthermore, we measured all the collected microparticles by micro-FTIR. However, micro-FTIR did not detect MPs in any of the meconium samples, whereas we observed muscovite, octanoic hydrazide, and palmitic acid in some of the meconium samples (Figure 5). Additionally, the FTIR spectra of other potential MPs in the meconium samples could be found in the supplementary Figure S2. However, these FTIR spectra could not be characterized as defined chemical compounds based on spectral similarity when compared with Omnic and Bruker reference spectra databases. Details about the sample and the results are presented in Table 3.

4. Discussion

A growing body of literature has revealed that MPs are present in humans. However, human fetal MP exposure remains an under-researched topic. We found no MPs > 10 μm in any of the meconium samples, under strict quality control. This suggests that the MP pollution levels in the fetal living environment were miniscule in at least the samples analyzed.
Most MP exposure has been discovered in marine life [34]. Thus, we speculate that pregnant women living near bodies of water may be more likely to inadvertently ingest MPs via seafood than those people living far from water. Hence, our meconium samples are likely to present MPs due to the fact that the Guangdong Maternal and Child Health Hospital is located near the Pearl River in which MPs have been reported [35,36]. In a recent study, plastic particles in human blood were investigated, and it was estimated that the mean of the sum of the MP concentrations for each donor was 1.6 μg total plastic particles/mL blood sample [8,27,28]. Another study showed that MP fragments with diameter ranging from 5 to 10 μm can reach human placenta tissues at all levels [11]. Therefore, we speculate that MPs enter the placenta via maternal blood because the placenta connects the fetus and matrix via the bloodstream [37]. Maternal blood delivering nutrients to the fetus may also deliver MPs to the fetus, which would be detrimental to health. PS-MPs have caused adverse effects on pregnancy outcomes in mice via immune disturbance [38]. Given that immune disturbance has weakened placenta barrier function [39], MP exposure may weaken placenta barrier function and allow MPs to penetrate it to arrive at fetus. Besides, amniotic fluid is considered a transudate of plasma from the mother across the uterine decidua and/or the placenta surface [40]. The fetus consumes an average of 210–760 mL of amniotic fluid per day [41]. The detection of MPs in the placenta hints that amniotic fluid could be another source of fetal MP exposure. Once MPs intrude the amniotic fluid, they are detectable in meconium. However, to date there has been no report on amniotic fluid MPs. This requires further study and will clarify fetal exposure routes.
Digestion is the first step in separating MPs from environmental and biological samples. Various chemicals have been used for the digestion. For instance, 30% H2O2 has been used to digest biological tissue and meconium, and the result has shown that 30% H2O2 at 25 °C takes about 5 weeks to eliminate the organic matter from the meconium samples [24]. However, it failed to digest our meconium samples completely under the same conditions (Figure 2A). In our study, after 30% H2O2 had digested for nine months, a considerable amount of residue remained in the solution, which affected MP detection. Different sample sources may cause varying H2O2 digestive capacity in meconium. Meconium consists of water, lipids, protein, sterols, and cholesterol precursors derived from swallowed amniotic fluid, shed epithelial cells, and intestinal secretions [20]. We found that there was a considerable amount of grease after 30% H2O2 digestion, which could be explained by the wealth of lipids in our meconium samples, and the limited ability of H2O2 in removing organic matter [42]. HNO3 digestion, applied in a recent MP study on meconium [25], also showed limited digestive capacity in our study (Figure 2B). HNO3 digestion is an efficient method for removing organic matter [33], whereas it failed to digest our meconium samples completely. This might also have been attributed to the different sample sources. The wealth of lipids in our meconium samples made HNO3 difficult to completely digest. Moreover, we attempted to digest meconium using Fenton’s reagent, combined with HNO3, which have been used in an MP study on the feces of various species [29]. Fenton’s reagent has shown high digestion efficiencies on organic matter [42]. Nevertheless, the attempt did not succeed in completely digesting our meconium samples. Rather, it behaved as grease residue in the solution and subsequently affected MP separation (Figure 2C). After these trials, we established an effective method for meconium pretreatment. Foremost, we selected a petroleum ether and alcohol (4:1, v/v) mixed solution at the initial pretreatment step to extract any grease which had previously hindered digestion. After that, we chose HNO3 to digest any remaining solid matter. Finally, we added H2O2 to digest any remaining organic matter and obtained a clear solution for further MP extraction and detection. Our pretreatment methods showed good recovery (Table 2) and no significant changes in the MP properties after the extraction process (Figure 3). This indicated that our methods for extracting MPs from meconium with no damage had been effective. We also compared several attempted methods with our methods in Table 1. In sum, our pretreatment methods were effective and time-saving in the MP meconium study.
In the present study, we did not detect MPs in any of the 16 meconium samples. Conversely, a previous study has identified MPs in two meconium samples [24]. However, the number of samples is a limitation of their generalizability. In our study, we used a similar amount of samples as other well-designed meconium studies [23,43]. A most recent study also identified MPs ranging from 20 to 500 μm in 12 meconium samples (median: 51.4 particles/g) [25]. These results were inconsistent with ours, which may have been due to different sample sources and detection methods. Furthermore, contamination during sample collection and analysis could not be excluded in existing meconium MP studies [24,25], whereas we found no sample contamination in our study. Our pretreatment method showed good recovery but we found no MPs in any of our meconium samples. This result was attributed to several reasons. Firstly, we focused on MPs with diameter >10 μm and the placenta barrier prevents most of these macromolecular substances from entering the fetus [37]. In the most recent study of MPs in the placenta, only 6 MPs were found ranging from 7.3 to 27.6 μm in 4 out of 30 participants in normal pregnancies [10]. Furthermore, a recent study reported only 12 MPs in 4 human placentas [11]. These results indicated that human placental MP exposure levels are miniscule. Therefore, low MP concentrations could be the major reason for our result.
The limit of FTIR could be another reason. FTIR has been used to detect contaminants in many environmental samples [44,45,46]. It also has been used to detect MPs from stool [47]. However, FTIR can only accurately detect irregular particles with diameter > 50 μm [48]. It is unable to detect those irregular MPs with diameter ranging from 10–50 μm in the meconium samples. A recent study demonstrates that the majority of detected MPs (64%) are smaller than 10 μm, and the shape of those ranging from 10 to 34.5 μm is irregular (fragment, film, pellet, fiber) in the placenta [10]. A previous study also revealed that MPs with diameter < 10 μm were able to penetrate the placenta because MPs with diameter ranging 5–10 μm were detected in the placenta [11]. These results suggest that most MPs in the human placenta are smaller than 10 μm, and as for MPs ranging from 10–50 μm in the placenta, they all have irregular shapes. Even though two studies have shown MPs with diameter > 50 μm in the placenta and in the meconium [24,25], the authors suspect that the negative controls may have been contaminated by MPs, thus weakening the results’ credibility. PS beads with a diameter up to 240 nm are taken up by the placenta and can penetrate the placental barrier in ex vivo dual recirculating human placental perfusion model [49]. Several studies have also confirmed that nano-sized MPs can infiltrate the fetus [12,15,50]. Besides, nano-sized particles could pass through the human placenta barrier and appear in meconium. For example, transmission electron microscope analysis has shown TiO2 particles ranging from 10 to 225 nm in diameter in meconium [23]. In sum, we found no MPs in meconium, and this may indicate low-level MPs, irregularly shaped MPs ranging from 10–50 μm, or MPs with diameter < 10 μm in meconium.
Although we observed no MPs in meconium, we found muscovite, octanoic hydrazide, and palmitic acid in the meconium samples (Figure 5). Muscovite, also called white mica, is a major component of traditional Chinese medicine, which has been utilized to treat bleeding, dysentery, and inflammation [51]. Muscovite has been developed and marketed in China for the treatment of gastric disease [52,53]. Considering that women often use traditional Chinese medicine during pregnancy [54], it was not surprising that we observed muscovite in the meconium. This reminded us of the potential for inorganic particle exposure in human fetuses. Palmitic acid is the most abundant saturated fatty acid in the blood [55], and its concentration in amniotic fluid is considered the most reliable method for assessing fetal lung maturity [56]. The presence of palmitic acid in meconium indicated that meconium’s grease had not been eliminated. In order to remove grease in the meconium samples in our study protocol, we used a mixed solution composed of petroleum ether and alcohol (v/v, 4:1). Additionally, we used hot water to dissolve as much grease as possible. Indeed, we only found palmitic acid in one meconium sample, and the presence of palmitic acid did not affect MP detection. The present study has several limitations. Firstly, we did not make the connection between our results and the mothers’ exposure. Secondly, in our study, we only focused on MPs with diameter > 10 μm. However, nano-sized MPs deserve attention because they are more prone to penetrating the human body due to their small diameter. To detect nano-sized MPs, further study should employ higher spatial resolution instruments such as surface-enhanced Raman spectroscopy, mass spectrometry, and combinations of various detection methods [57]. Thirdly, we selected PS standard as representative MPs in the recovery experiment, similar to how PS has been found in existing meconium MP studies [24,25]. It should also be mentioned that MPs’ response to the digestion method varies with different materials [32]. Lastly, although our pretreatment methods showed good recovery, MPs in meconium may be lost during sample preparation due to the extraction conditions (HNO3 and heating to 80 °C) [58]. Increasing evidence of MPs in human bio-samples has aroused public attention and concern. This has alerted the scientific community of MP exposure-risk in humans, as well as the need to promote plastic management.

5. Conclusions

We developed an effective pretreatment method to separate microplastics from meconium. Using our new pretreatment method, we detected no MPs (>10 μm) in meconium by comparing with Omnic and Bruker reference spectra databases. This suggested low fetal MP exposure levels in newborns. Further studies should focus on fetal nanoplastics exposure. In addition, the existence of NPs in the fetal body and their related metabolic pathway also warrants further study. However, we should not overlook the limitations of the human data presented in the previous studies when we conduct risk assessment on human microplastics exposure.

Supplementary Materials

The following supporting information can be downloaded at: https://www.mdpi.com/article/10.3390/toxics11040310/s1, Table S1: The information of protocols and samples used in the initial pretreatments; Figure S1: The composition of diaper control. (A) Photograph of Fourier transform infrared microspectroscopy (200 × magnification); (B) FTIR spectrum of diaper. The red dot in A indicates the position for detected; Figure S2: FTIR spectra of other potential MPs in the meconium samples from (A) No. 1, (B) No. 9, (C) No.10, (D) No. 15, (E) No. 17, (F,G) No. 32, (H) No. 37.

Author Contributions

Conceptualization, Z.H., Z.L., J.W. (Jiamin Wang) and X.G.; methodology, Z.L., J.W. (Jiamin Wang) and X.G.; formal analysis, Z.L., J.W. (Jiamin Wang) and X.G.; resources, Z.H., H.S. and X.Y.; data curation, J.D., J.W. (Jieling Wu), Y.Z., B.L., Y.H., R.Y. and Y.D.; writing—Original draft preparation, Z.L., J.W. (Jiamin Wang) and X.G.; writing—Review and editing, Z.H.; visualization, Z.L., J.W. (Jiamin Wang), X.G., J.D., J.W. (Jieling Wu), Y.Z., B.L., Y.H., R.Y. and Y.D.; project administration, Z.H.; funding acquisition, Z.H., H.S. and X.Y. All authors have read and agreed to the published version of the manuscript.

Funding

This work was supported by grants from the National Natural Science Foundation of China (Grant No. 82273656, 82073519, 81872601), the Science and Technology Project of Guangdong Province, China (Grant No. 2022A0505050035), the Guangdong Basic Applied Basic Research Foundation (Grant No. 2022A1515010610, the Guangdong–Dongguan Joint grant No.2022A1515111098), the Chinese Postdoctoral Science Foundation (Grant No.2022M721486), the National Key R&D Program of China Ministry of Science and Technology of China (Grant No. 2018YFC1602103), the Guangdong Key R&D Program Ministry of Science and Technology of Guangdong Province (Grant No. 2019B020210002), the National Training Program of Innovation and Entrepreneurship for Undergraduates (Grant No. S202212121034, S202112121113, S202112121115), the Guangdong Provincial Key Laboratory of Tropical Disease Research (Grant No. 2017B030314035), and the NMPA Key Laboratory for Safety Evaluation of Cosmetics.

Institutional Review Board Statement

The study was conducted in accordance with the Declaration of Helsinki and approved by the Guangdong Women and Children Hospital Scientific Research Committee on Ethics in the Care and Use of Human Samples (Permit No. 201801057).

Informed Consent Statement

Informed consent was obtained from all subjects involved in this study.

Data Availability Statement

The data presented in this study are available on request from the corresponding author.

Conflicts of Interest

The authors declare no conflict of interest.

References

  1. Okoffo, E.D.; Donner, E.; McGrath, S.P.; Tscharke, B.J.; O’Brien, J.W.; O’Brien, S.; Ribeiro, F.; Burrows, S.D.; Toapanta, T.; Rauert, C.; et al. Plastics in biosolids from 1950 to 2016: A function of global plastic production and consumption. Water Res. 2021, 201, 117367. [Google Scholar] [CrossRef] [PubMed]
  2. Prata, J.C.; Silva, A.L.P.; da Costa, J.P.; Mouneyrac, C.; Walker, T.R.; Duarte, A.C.; Rocha-Santos, T. Solutions and Integrated Strategies for the Control and Mitigation of Plastic and Microplastic Pollution. Int. J. Environ. Res. Public Health 2019, 16, 2411. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  3. Geyer, R.; Jambeck, J.R.; Law, K.L. Production, use, and fate of all plastics ever made. Sci. Adv. 2017, 3, e1700782. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  4. Liang, B.; Zhong, Y.; Huang, Y.; Lin, X.; Liu, J.; Lin, L.; Hu, M.; Jiang, J.; Dai, M.; Wang, B.; et al. Underestimated health risks: Polystyrene micro- and nanoplastics jointly induce intestinal barrier dysfunction by ROS-mediated epithelial cell apoptosis. Part. Fibre Toxicol. 2021, 18, 20. [Google Scholar] [CrossRef] [PubMed]
  5. Galloway, T.S.; Cole, M.; Lewis, C. Interactions of microplastic debris throughout the marine ecosystem. Nat. Ecol. Evol. 2017, 1, 116. [Google Scholar] [CrossRef]
  6. Praveena, S.M.; Shaifuddin, S.N.M.; Akizuki, S. Exploration of microplastics from personal care and cosmetic products and its estimated emissions to marine environment: An evidence from Malaysia. Mar. Pollut. Bull. 2018, 136, 135–140. [Google Scholar] [CrossRef]
  7. Zhang, N.; Li, Y.B.; He, H.R.; Zhang, J.F.; Ma, G.S. You are what you eat: Microplastics in the feces of young men living in Beijing. Sci. Total Environ. 2021, 767, 144345. [Google Scholar] [CrossRef]
  8. Leslie, H.A.; van Velzen, M.J.M.; Brandsma, S.H.; Vethaak, D.; Garcia-Vallejo, J.J.; Lamoree, M.H. Discovery and quantification of plastic particle pollution in human blood. Environ. Int. 2022, 163, 107199. [Google Scholar] [CrossRef]
  9. Amato-Lourenco, L.F.; Carvalho-Oliveira, R.; Junior, G.R.; Dos Santos Galvao, L.; Ando, R.A.; Mauad, T. Presence of airborne microplastics in human lung tissue. J. Hazard. Mater. 2021, 416, 126124. [Google Scholar] [CrossRef]
  10. Amereh, F.; Amjadi, N.; Mohseni-Bandpei, A.; Isazadeh, S.; Mehrabi, Y.; Eslami, A.; Naeiji, Z.; Rafiee, M. Placental plastics in young women from general population correlate with reduced foetal growth in IUGR pregnancies. Environ. Pollut. 2022, 314, 120174. [Google Scholar] [CrossRef]
  11. Ragusa, A.; Svelato, A.; Santacroce, C.; Catalano, P.; Notarstefano, V.; Carnevali, O.; Papa, F.; Rongioletti, M.C.A.; Baiocco, F.; Draghi, S.; et al. Plasticenta: First evidence of microplastics in human placenta. Environ. Int. 2021, 146, 106274. [Google Scholar] [CrossRef]
  12. Huang, T.; Zhang, W.; Lin, T.; Liu, S.; Sun, Z.; Liu, F.; Yuan, Y.; Xiang, X.; Kuang, H.; Yang, B.; et al. Maternal exposure to polystyrene nanoplastics during gestation and lactation induces hepatic and testicular toxicity in male mouse offspring. Food Chem. Toxicol. 2022, 160, 112803. [Google Scholar] [CrossRef]
  13. Jeong, B.; Baek, J.Y.; Koo, J.; Park, S.; Ryu, Y.K.; Kim, K.S.; Zhang, S.; Chung, C.; Dogan, R.; Choi, H.S.; et al. Maternal exposure to polystyrene nanoplastics causes brain abnormalities in progeny. J. Hazard. Mater. 2022, 426, 127815. [Google Scholar] [CrossRef]
  14. Lu, K.; Lai, K.P.; Stoeger, T.; Ji, S.; Lin, Z.; Lin, X.; Chan, T.F.; Fang, J.K.-H.; Lo, M.; Gao, L.; et al. Detrimental effects of microplastic exposure on normal and asthmatic pulmonary physiology. J. Hazard. Mater. 2021, 416, 126069. [Google Scholar] [CrossRef] [PubMed]
  15. Nie, J.H.; Shen, Y.; Roshdy, M.; Cheng, X.; Wang, G.; Yang, X. Polystyrene nanoplastics exposure caused defective neural tube morphogenesis through caveolae-mediated endocytosis and faulty apoptosis. Nanotoxicology 2021, 15, 885–904. [Google Scholar] [CrossRef]
  16. Zaheer, J.; Kim, H.; Ko, I.O.; Jo, E.K.; Choi, E.J.; Lee, H.J.; Shim, I.; Woo, H.J.; Choi, J.; Kim, G.H.; et al. Pre/post-natal exposure to microplastic as a potential risk factor for autism spectrum disorder. Environ. Int. 2022, 161, 107121. [Google Scholar] [CrossRef]
  17. Vizcaino, E.; Grimalt, J.O.; Glomstad, B.; Fernández-Somoano, A.; Tardón, A. Gestational weight gain and exposure of newborns to persistent organic pollutants. Environ. Health Perspect. 2014, 122, 873–879. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  18. Yong, H.E.J.; Chan, S.Y.; Chakraborty, A.; Rajaraman, G.; Ricardo, S.; Benharouga, M.; Alfaidy, N.; Staud, F.; Murthi, P. Significance of the placental barrier in antenatal viral infections. Biochim. Biophys. Acta Mol. Basis Dis. 2021, 1867, 166244. [Google Scholar] [CrossRef]
  19. Concheiro, M.; Huestis, M.A. Drug exposure during pregnancy: Analytical methods and toxicological findings. Bioanalysis 2018, 10, 587–606. [Google Scholar] [CrossRef] [PubMed]
  20. Bearer, C.F. Meconium as a biological marker of prenatal exposure. Ambul. Pediatr. 2003, 3, 40–43. [Google Scholar] [CrossRef] [PubMed]
  21. Bakdash, A.; Burger, P.; Goecke, T.W.; Fasching, P.A.; Reulbach, U.; Bleich, S.; Hastedt, M.; Rothe, M.; Beckmann, M.W.; Pragst, F.; et al. Quantification of fatty acid ethyl esters (FAEE) and ethyl glucuronide (EtG) in meconium from newborns for detection of alcohol abuse in a maternal health evaluation study. Anal. Bioanal. Chem. 2010, 396, 2469–2477. [Google Scholar] [CrossRef]
  22. Ostrea, E.M.; Bielawski, D.M.; Posecion, N.C. Meconium analysis to detect fetal exposure to neurotoxicants. Arch. Dis. Child. 2006, 91, 628–629. [Google Scholar] [CrossRef]
  23. Guillard, A.; Gaultier, E.; Cartier, C.; Devoille, L.; Noireaux, J.; Chevalier, L.; Morin, M.; Grandin, F.; Lacroix, M.Z.; Coméra, C.; et al. Basal Ti level in the human placenta and meconium and evidence of a materno-foetal transfer of food-grade TiO nanoparticles in an ex vivo placental perfusion model. Part. Fibre Toxicol. 2020, 17, 51. [Google Scholar] [CrossRef]
  24. Braun, T.; Ehrlich, L.; Henrich, W.; Koeppel, S.; Lomako, I.; Schwabl, P.; Liebmann, B. Detection of Microplastic in Human Placenta and Meconium in a Clinical Setting. Pharmaceutics 2021, 13, 921. [Google Scholar] [CrossRef] [PubMed]
  25. Liu, S.; Lin, G.; Liu, X.; Yang, R.; Wang, H.; Sun, Y.; Chen, B.; Dong, R. Detection of various microplastics in placentas, meconium, infant feces, breastmilk and infant formula: A pilot prospective study. Sci. Total Environ. 2022, 854, 158699. [Google Scholar] [CrossRef] [PubMed]
  26. Liu, S.; Liu, X.; Guo, J.; Yang, R.; Wang, H.; Sun, Y.; Chen, B.; Dong, R. The Association Between Microplastics and Microbiota in Placentas and Meconium: The First Evidence in Humans. Environ. Sci. Technol. 2022; online ahead of print. [Google Scholar]
  27. Kutralam-Muniasamy, G.; Shruti, V.C.; Pérez-Guevara, F.; Roy, P.D. Microplastic diagnostics in humans: “The 3Ps” Progress, problems, and prospects. Sci. Total Environ. 2023, 856, 159164. [Google Scholar] [CrossRef] [PubMed]
  28. Kuhlman, R.L. Letter to the editor, discovery and quantification of plastic particle pollution in human blood. Environ. Int. 2022, 167, 107400. [Google Scholar] [CrossRef]
  29. Yan, Z.; Zhao, H.; Zhao, Y.; Zhu, Q.; Qiao, R.; Ren, H.; Zhang, Y. An efficient method for extracting microplastics from feces of different species. J. Hazard. Mater. 2020, 384, 121489. [Google Scholar] [CrossRef]
  30. Schwabl, P.; Köppel, S.; Königshofer, P.; Bucsics, T.; Trauner, M.; Reiberger, T.; Liebmann, B. Detection of Various Microplastics in Human Stool: A Prospective Case Series. Ann. Intern. Med. 2019, 171, 453–457. [Google Scholar] [CrossRef]
  31. Zhao, S.; Ward, J.E.; Danley, M.; Mincer, T.J. Field-Based Evidence for Microplastic in Marine Aggregates and Mussels: Implications for Trophic Transfer. Environ. Sci. Technol. 2018, 52, 11038–11048. [Google Scholar] [CrossRef]
  32. Aung, T.; Batish, I.; Ovissipour, R. Prevalence of Microplastics in the Eastern Oyster Crassostrea virginica in the Chesapeake Bay: The Impact of Different Digestion Methods on Microplastic Properties. Toxics 2022, 10, 29. [Google Scholar] [CrossRef]
  33. Davidson, K.; Dudas, S.E. Microplastic Ingestion by Wild and Cultured Manila Clams (Venerupis philippinarum) from Baynes Sound, British Columbia. Arch. Environ. Contam. Toxicol. 2016, 71, 147–156. [Google Scholar] [CrossRef]
  34. Smith, M.; Love, D.C.; Rochman, C.M.; Neff, R.A. Microplastics in Seafood and the Implications for Human Health. Curr. Environ. Health Rep. 2018, 5, 375–386. [Google Scholar] [CrossRef] [Green Version]
  35. Lam, T.W.L.; Fok, L.; Lin, L.; Xie, Q.; Li, H.X.; Xu, X.R.; Yeung, L.C. Spatial variation of floatable plastic debris and microplastics in the Pearl River Estuary, South China. Mar. Pollut. Bull. 2020, 158, 111383. [Google Scholar] [CrossRef]
  36. Yan, M.; Nie, H.; Xu, K.; He, Y.; Hu, Y.; Huang, Y.; Wang, J. Microplastic abundance, distribution and composition in the Pearl River along Guangzhou city and Pearl River estuary, China. Chemosphere 2019, 217, 879–886. [Google Scholar] [CrossRef] [PubMed]
  37. Burton, G.J.; Fowden, A.L. The placenta: A multifaceted, transient organ. Philos. Trans. R. Soc. Lond. B Biol. Sci. 2015, 370, 20140066. [Google Scholar] [CrossRef] [Green Version]
  38. Hu, J.; Qin, X.; Zhang, J.; Zhu, Y.; Zeng, W.; Lin, Y.; Liu, X. Polystyrene microplastics disturb maternal-fetal immune balance and cause reproductive toxicity in pregnant mice. Reprod. Toxicol. 2021, 106, 42–50. [Google Scholar] [CrossRef] [PubMed]
  39. Tossetta, G.; Paolinelli, F.; Avellini, C.; Salvolini, E.; Ciarmela, P.; Lorenzi, T.; Emanuelli, M.; Toti, P.; Giuliante, R.; Gesuita, R.; et al. IL-1β and TGF-β weaken the placental barrier through destruction of tight junctions: An in vivo and in vitro study. Placenta 2014, 35, 509–516. [Google Scholar] [CrossRef] [PubMed]
  40. Beall, M.H.; van den Wijngaard, J.P.; van Gemert, M.J.; Ross, M.G. Amniotic fluid water dynamics. Placenta 2007, 28, 816–823. [Google Scholar] [CrossRef] [PubMed]
  41. Pritchard, J.A. Fetal swallowing and amniotic fluid volume. Obstet. Gynecol. 1966, 28, 606–610. [Google Scholar] [PubMed]
  42. Prata, J.C.; da Costa, J.P.; Girao, A.V.; Lopes, I.; Duarte, A.C.; Rocha-Santos, T. Identifying a quick and efficient method of removing organic matter without damaging microplastic samples. Sci. Total Environ. 2019, 686, 131–139. [Google Scholar] [CrossRef] [PubMed]
  43. Kennedy, K.M.; Gerlach, M.J.; Adam, T.; Heimesaat, M.M.; Rossi, L.; Surette, M.G.; Sloboda, D.M.; Braun, T. Fetal meconium does not have a detectable microbiota before birth. Nat. Microbiol. 2021, 6, 865–873. [Google Scholar] [CrossRef] [PubMed]
  44. Soltani, N.S.; Taylor, M.P.; Wilson, S.P. Quantification and exposure assessment of microplastics in Australian indoor house dust. Environ. Pollut. 2021, 283, 117064. [Google Scholar] [CrossRef]
  45. Zhao, S.; Wang, T.; Zhu, L.; Xu, P.; Wang, X.; Gao, L.; Li, D. Analysis of suspended microplastics in the Changjiang Estuary: Implications for riverine plastic load to the ocean. Water Res. 2019, 161, 560–569. [Google Scholar] [CrossRef]
  46. Zhou, B.; Wang, J.; Zhang, H.; Shi, H.; Fei, Y.; Huang, S.; Tong, Y.; Wen, D.; Luo, Y.; Barceló, D. Microplastics in agricultural soils on the coastal plain of Hangzhou Bay, east China: Multiple sources other than plastic mulching film. J. Hazard. Mater. 2020, 388, 121814. [Google Scholar] [CrossRef] [PubMed]
  47. Perez-Guevara, F.; Kutralam-Muniasamy, G.; Shruti, V.C. Critical review on microplastics in fecal matter: Research progress, analytical methods and future outlook. Sci. Total Environ. 2021, 778, 146395. [Google Scholar] [CrossRef]
  48. Kazarian, S.G.; Chan, K.L.A. ATR-FTIR spectroscopic imaging: Recent advances and applications to biological systems. Analyst 2013, 138, 1940–1951. [Google Scholar] [CrossRef] [PubMed]
  49. Wick, P.; Malek, A.; Manser, P.; Meili, D.; Maeder-Althaus, X.; Diener, L.; Diener, P.A.; Zisch, A.; Krug, H.F.; von Mandach, U. Barrier capacity of human placenta for nanosized materials. Environ. Health Perspect. 2010, 118, 432–436. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  50. Fournier, S.B.; D’Errico, J.N.; Adler, D.S.; Kollontzi, S.; Goedken, M.J.; Fabris, L.; Yurkow, E.J.; Stapleton, P.A. Nanopolystyrene translocation and fetal deposition after acute lung exposure during late-stage pregnancy. Part. Fibre Toxicol. 2020, 17, 55. [Google Scholar] [CrossRef]
  51. Xia, T.; Lei, C.; Xu, C.; Peng, N.; Li, Y.; Yang, X.Y.; Cheng, Z.Z.; Gauthier, M.; Gu, H.Z.; Zou, T. Preparation and Antitumor Study of Two-Dimensional Muscovite Nanosheets. Langmuir 2020, 36, 14268–14275. [Google Scholar] [CrossRef]
  52. Qian, Y.; Si, J.M.; Wang, L.J.; Chen, S.J.; Zhu, Y.F. Mechanisms of muscovite on gastric mucosal protective effect. Zhongguo Zhong Yao Za Zhi 2004, 29, 781–785. [Google Scholar]
  53. Si, J.M.; Qian, Y.; Wu, J.G. The effect of muscovite on the quality of gastric ulcer healing. Zhongguo Zhong Yao Za Zhi 2005, 30, 1536–1541. [Google Scholar]
  54. Chen, H.Q.; Zou, S.H.; Yang, J.B.; Cai, J.; Zhang, Y.; Wang, Z.L. A survey and analysis of using traditional Chinese medicine during pregnancy. Int. J. Clin. Exp. Med. 2015, 8, 19496–19500. [Google Scholar]
  55. Amine, H.; Benomar, Y.; Taouis, M. Palmitic acid promotes resistin-induced insulin resistance and inflammation in SH-SY5Y human neuroblastoma. Sci. Rep. 2021, 11, 5427. [Google Scholar] [CrossRef] [PubMed]
  56. Bichler, A.; Daxenbichler, G.; Geir, W. Determination of amniotic fluid palmitic acid concentration for the estimation of fetal lung maturity. Clin. Chim. Acta 1977, 74, 133–138. [Google Scholar] [CrossRef] [PubMed]
  57. Saliu, F.; Biale, G.; Raguso, C.; La Nasa, J.; Degano, I.; Seveso, D.; Galli, P.; Lasagni, M.; Modugno, F. Detection of plastic particles in marine sponges by a combined infrared micro-spectroscopy and pyrolysis-gas chromatography-mass spectrometry approach. Sci. Total Environ. 2022, 819, 152965. [Google Scholar] [CrossRef] [PubMed]
  58. Nguyen, B.; Claveau-Mallet, D.; Hernandez, L.M.; Xu, E.G.; Farner, J.M.; Tufenkji, N. Separation and Analysis of Microplastics and Nanoplastics in Complex Environmental Samples. Acc. Chem. Res. 2019, 52, 858–866. [Google Scholar] [CrossRef] [PubMed] [Green Version]
Toxics 11 00310 g001 550
Figure 1. Study overview. Mix: Petroleum ether and alcohol (4:1, v/v), HNO3: Nitric acid, H2O2: Hydrogen peroxide. The numbers 1–3 represent the order in which the reagents were added.
Figure 1. Study overview. Mix: Petroleum ether and alcohol (4:1, v/v), HNO3: Nitric acid, H2O2: Hydrogen peroxide. The numbers 1–3 represent the order in which the reagents were added.
Toxics 11 00310 g001
Toxics 11 00310 g002 550
Figure 2. Different effects of various digestion methods. (A) After digestion with H2O2 for nine months; (B) After HNO3 digestion; (C) After digestion by a combination of Fenton’s reagent and HNO3; and (D) The process of our established pretreatment methods. The red boxes in (A–C) indicate incomplete digestion.
Figure 2. Different effects of various digestion methods. (A) After digestion with H2O2 for nine months; (B) After HNO3 digestion; (C) After digestion by a combination of Fenton’s reagent and HNO3; and (D) The process of our established pretreatment methods. The red boxes in (A–C) indicate incomplete digestion.
Toxics 11 00310 g002
Toxics 11 00310 g003 550
Figure 3. PS standard before/after digestion. (A,B) Before digestion, 50 μm and 200 μm, respectively; and (C,D) After digestion, 50 μm and 200 μm, respectively.
Figure 3. PS standard before/after digestion. (A,B) Before digestion, 50 μm and 200 μm, respectively; and (C,D) After digestion, 50 μm and 200 μm, respectively.
Toxics 11 00310 g003
Toxics 11 00310 g004 550
Figure 4. Microscope with field image super depth (200× magnification). (A) Procedure control and (B–I) Representative samples. Red circles mark potential MPs.
Figure 4. Microscope with field image super depth (200× magnification). (A) Procedure control and (B–I) Representative samples. Red circles mark potential MPs.
Toxics 11 00310 g004
Toxics 11 00310 g005 550
Figure 5. The acquired FTIR spectrum. (A) Muscovite, (B) Octanoic hydrazide, and (C) Palmitic acid.
Figure 5. The acquired FTIR spectrum. (A) Muscovite, (B) Octanoic hydrazide, and (C) Palmitic acid.
Toxics 11 00310 g005
Table
Table 1. The comparison of different chemical digestion methods.
Table 1. The comparison of different chemical digestion methods.
ChemicalHydrogen Peroxide (H2O2)Nitric Acid (HNO3)Fenton’s Reagent + HNO3Petroleum Ether and Alcohol + HNO3 + H2O2
SampleFeces [7,30,31]
Meconium [24]		Meconium [25]
Oyster [32] and clam tissue [33]		Feces [29]Meconium
Present study
Method summary25 mL 30% H2O2 with 3 g human fecal samples for 20 days [7].
30% H2O2 at 25 °C for two weeks [30].
30% H2O2 and samples were mixed in a 1:1 v/v ratio, incubated in a sand bath (~75 °C) for 24 h and then at room temperature for 36 to 48 h [31].
H2O2 for 5 weeks to completely eliminate the organic matter [24].		HNO3 is added to the samples, allowing to stand for 48 h, and then heat at 95 °C for at least 3 h [25].
HNO3 is added to the samples and incubate at 60 °C for 24 h [32].
Clam tissue digested in 40 mL of 69–71% HNO3 for 4 h in a hot
water bath (~90 °C) [33]. 		Phase 1: 140–700 mL Fenton’s reagent (H2O2: iron catalyst solution = 2.5:1) with human, chicken, and zebrafish feces, lasting less than 5 h below 40 °C.
Phase 2: 65% HNO3 is added and incubated in 50 °C water bath for 30 min.		Phase 1: Petroleum ether and alcohol (4:1, v/v) remove lipids.
Phase 2: HNO3 (5 mL/g meconium) is added and incubated in cold water bath overnight, followed by digestion for 4 h at 80 °C.
Phase 3: 5 mL H2O2 is added for 30 min at 80 °C, followed by filtering the digestion solution.
AdvantageEasy to operate; extract MPs with no damage.Efficient and feasible way for meconium digestion; time-saving.Easy to operate; time-savingCompletely digest our meconium samples; easy to operate; time-saving.
DisadvantageCould not completely digest our meconium samples; time-consumingCould not completely digested our meconium samples; potentially damage MPs.Could not completely digest our meconium samples.Potentially damage MPs
Table
Table 2. The recovery rate of 50 μm and 200 μm PS standard in the test.
Table 2. The recovery rate of 50 μm and 200 μm PS standard in the test.
GroupAdded Targets/ItemRecovery Targets/ItemRecovery Rate (%)
50 μm200 μm50 μm200 μm50 μm200 μm
1293872586588.0574.71
2255631813170.9849.21
3726346902695.0476.47
Average recovery rate (%)----84.69 ± 12.3866.80 ± 15.26
“-“: Not available.
Table
Table 3. Summary of sample information and results of MP detection.
Table 3. Summary of sample information and results of MP detection.
Sample DescriptionDry Weight/gResults
Procedure blank control 1-Negative
Procedure blank control 2-Negative
Procedure blank control 3-Negative
Meconium No. 11.8600Negative
Meconium No. 2 0.8013Negative
Meconium No. 3 2.1695Negative
Meconium No. 9 2.5295Negative
Meconium No. 102.8588Negative
Meconium No. 124.3440Negative
Meconium No. 143.0063Negative
Meconium No. 150.4038Negative
Meconium No. 160.9895Negative
Meconium No. 174.6835Negative
Meconium No. 18 1.4887Negative
Meconium No. 191.4463Negative
Meconium No. 292.1207Negative
Meconium No. 311.7712Negative
Meconium No. 320.7137Negative
Meconium No. 372.1840Negative
“-“: Not available.
Disclaimer/Publisher’s Note: The statements, opinions and data contained in all publications are solely those of the individual author(s) and contributor(s) and not of MDPI and/or the editor(s). MDPI and/or the editor(s) disclaim responsibility for any injury to people or property resulting from any ideas, methods, instructions or products referred to in the content.

Share and Cite

MDPI and ACS Style

Li, Z.; Wang, J.; Gao, X.; Du, J.; Sui, H.; Wu, J.; Zhong, Y.; Liang, B.; Huang, Y.; Ye, R.; et al. Investigation of Microplastics (≥10 μm) in Meconium by Fourier Transform Infrared Microspectroscopy. Toxics 2023, 11, 310. https://doi.org/10.3390/toxics11040310

AMA Style

Li Z, Wang J, Gao X, Du J, Sui H, Wu J, Zhong Y, Liang B, Huang Y, Ye R, et al. Investigation of Microplastics (≥10 μm) in Meconium by Fourier Transform Infrared Microspectroscopy. Toxics. 2023; 11(4):310. https://doi.org/10.3390/toxics11040310

Chicago/Turabian Style

Li, Zhiming, Jiamin Wang, Xia Gao, Jiaxin Du, Haixia Sui, Jieling Wu, Yizhou Zhong, Boxuan Liang, Yuji Huang, Rongyi Ye, and et al. 2023. "Investigation of Microplastics (≥10 μm) in Meconium by Fourier Transform Infrared Microspectroscopy" Toxics 11, no. 4: 310. https://doi.org/10.3390/toxics11040310

Note that from the first issue of 2016, this journal uses article numbers instead of page numbers. See further details here.

Article Metrics

Back to TopTop