| Home | E-Submission | Sitemap | Contact Us |  
Environ Anal Health Toxicol > Volume 37:2022 > Article
Ilechukwu, Ehigiator, Ben, Okonkwo, Olorunfemi, Modo, Ilechukwu, and Ohagwa: Chronic toxic effects of polystyrene microplastics on reproductive parameters of male rats


Microplastics have become a significant environmental concern. However, information on toxicity of microplastics in terrestrial organisms is limited. In this study, the chronic toxic effects of polystyrene microplastics (PS-MPs) on the reproductive system and serum antioxidants of male albino Wistar rats fed for 90 days with standard rat feed containing 1–10% granules of crushed polystyrene disposable plates were evaluated. Significant reductions in volume, motility, epididymal sperm count and serum testosterone level were observed. Histological examination of testicular architecture showed distorted testes with vacuolated seminiferous tubules at the highest percentage, together with increased catalase and decreased superoxide dismutase activities. This study showed that ingestion of PS-MPs caused reproductive dysfunction in male rats and contributes to understanding the potential toxicity of microplastics in terrestrial animals.


Microplastic pollution has gained global attention in recent times due to its environmental ubiquity. They are plastic particles of less than 5 mm in any one dimension [1,2]. Microplastics are of two main types; primary microplastics which are manufactured as such, and secondary microplastics which are degradation fragments of larger pieces [3]. They arise from littering, storm water overflow, wastewater treatment plants, biosolid application, atmospheric deposition, release from industries, and poor waste disposal [46].
Microplastics occur in different environmental compartments [710]. As mixtures of various chemicals and materials, microplastics may cause a multitude of harmful effects [11], such as physical blockage of the digestive tract, leakage of plastic additives, and release of adsorbed contaminants [12,13]. Organisms ranging from aquatic invertebrates to mammals may ingest microplastics [1417]. Accumulation of microplastics in the digestive system and transfer to other tissues through the circulatory system in mice as well as the trophic transfer of microplastics from aquatic to terrestrial mammals has been reported [18,19]. Adverse effects of exposure include disturbance of lipid metabolism, oxidative stress, decreased reproductive output, immobilization and triggered molting in copepod [2023]. Polystyrene is a major constituent of microplastics reported in the environment [1,8,9], due to its mass production and widespread use for insulation [24]. Polystyrene absorbs persistent organic pollutants and polycyclic aromatic hydrocarbons more extensively than other plastic polymers [25]. When used as plates, cups, and food packaging materials, food contact chemicals may transfer into food and be ingested by humans [26,27], and they are prone to weathering and resistant to biodegradation [24,28]. Currently, there are few studies on the adverse effects of microplastics on terrestrial mammals, as most studies are focused on aquatic organisms despite the ubiquitous presence of microplastics in the terrestrial environment [29,30]. Further, the majority of toxicological studies have been conducted with virgin or pristine microplastic particles. In this study, granules from disposable polystyrene plates were evaluated regarding their effects on the reproductive and antioxidant system of male Wistar rats.

Materials and Methods

Microplastic feed preparation

Packs of polystyrene disposable plates purchased from a local store were thoroughly washed with distilled and deionized water and dried at room temperature for 48 hours. The plates were crushed with a manual blender and particles that passed through a 2 mm mesh sieve were mixed into standard rat feed (Ladokun Feeds, Ibadan, Nigeria) in a stainless-steel mixing bowls at 1%, (10 g polystyrene particles in 1 kg of feed), 5% (50 g polystyrene particles in 1 kg of feed), and 10% (100 g polystyrene particles in 1 kg of feed).

Animal handling and experimental design

Twenty-four male albino rats obtained from the animal house of the University of Benin, Nigeria, weighing between 106–125 g were acclimatized for two weeks under standard laboratory conditions and distributed into four groups of six rats each in metal cages (56×30×22 cm). Group 1 served as control and received water and normal feed ad libitum. Groups 2, 3 and 4 received feed containing crushed polystyrene at 1%, 5%, and 10% respectively, which were constituted in 150 g of feed and fed to treated rats daily in the first 30 days. It was increased to 300 g daily for the next 60 days. Treatment was done such that the animals were fasted overnight after which the rats in the treatment groups were made to first eat all the polystyrene treated feeds before the normal feed. On day 90, the animals were sacrificed after anesthesia using chloroform before collection of seminal fluid. Blood collected from each animal via cardiac puncture with a 5 mL syringe was transferred into centrifuge tubes and centrifuged at 3000 rpm for 15 minutes. The serum obtained was used for determination of testosterone, glutathione (GSH), and malondialdehyde (MDA), as well as the activities of superoxide dismutase (SOD), catalase (CAT) and glutathione peroxidase (GSH-Px).

Organ collection and histology

The rats were dissected immediately after sacrifice and the testes were removed, cleared of adherent tissues and weighed on an electronic scale. The organs were fixed in Bouin’s solution for six hours before transfer to 10% formalin for 24 hours. Testes samples were processed routinely and embedded in paraffin blocks. Slides were prepared, stained with hematoxylin and eosin for histological evaluation under a light microscope. Microphotographs of the slides were also taken.

Serum analyses

Total serum testosterone was determined using an ELISA kit following the manufacturer’s protocol (Diametra, Perugia, Italy). Standard methods were used to determine the serum concentrations of GSH [31], MDA [32] and the activities of CAT [33], GSH-Px [34] and SOD [35]. Briefly GSH was measured by analyzing the thiol complexes reduction of DTNB (5, 5′-dithiobis (2-nitrobenzoic acid)) and absorbance read at 412 nm. Trichloroacetic acid (2.5%) was used to remove interfering proteins. Thiobarbituric acid method was used for the determination of MDA. Decrease in absorbance from the degradation of H2O2 by CAT enzyme in the presence of phosphate buffer was measured to determine CAT activity. Extinction coefficient of 39.4 mM−1 cm−1 was used for the calculation of H2O2 decomposition. One unit of activity is equivalent to 1 mM of H2O2 degraded per minute. GPx activity was determined by oxidation of NADPH to NADP+. The decrease in absorbance which is proportional to the GPx activity was measured at 340 nm. SOD was determined by inhibition of nitro blue tetrazolium (NBT) reduction. The amount of enzyme that leads to 50% inhibition of NBT reduction expresses one unit of enzyme activity. NBT reduction was measured at 600 nm.

Sperm motility and count assay

Sperm motility was determined according to Zemjanis [36]. The microscopic fields were viewed under a light microscope to determine motile and non-motile spermatozoa. Sperms were counted according to Pant and Srivastava [37], employing the improved Neubauer hemocytometer (depth 0.1 mm, LABART, Waldbüttelbrunn, Germany).

Morphology and viability assay

Morphology and viability were determined from 400 spermatozoa counted in smears stained according to Wells and Awa [38], stains (0.2 g eosin and 0.6 g fast green dissolved in distilled water and ethanol in 2:1 ratio) [39].

Statistical analysis

All data were analyzed using IBM SPSS Statistics version 21 and presented as mean±standard error of mean and analyzed by one-way analysis of variance followed by multiple comparison test. Significance of the mean differences was considered at p<0.05.

Results and Discussion

There was a decrease in the body weight of the treated groups which was significant (p<0.05) for Groups 3 and 4 (Table 1). Significant decrease in body weight of mice after six weeks exposure to polystyrene microplastics has been reported by Xie et al. [40]. Similar reduction also observed in this research may be due to the difficulty in expelling larger sized MPs from the body, resulting to heavy burden on gastro-intestinal tract which may reduce food absorption and cause decreased body weight [41].

Reproductive parameters

The sperm of all rats was milky in appearance while the viscosity and pH were normal and 8.0 respectively. The effects of the polystyrene microparticles on the sperm quality and testosterone levels of the male Wistar rats are shown in Table 2. There was a non-significant reduction in viability and morphology of the sperm cells and a non-significant increase in abnormal morphology and dead cells. The semen volume of the exposed group also decreased but significant only for Group 4 that received the highest proportion of microplastics. Sperm motility also decreased across the treated groups, significant (p<0.05) for Groups 3 and 4. The sperm cell count showed a significant decrease (p<0.05) for all treated groups. Testosterone also significantly decreased for Groups 3 and 4. This result indicates that polystyrene granules from polystyrene plates have adverse effects on the reproductive capabilities of male Wistar rats. It also agrees with other studies which found that polystyrene microplastics adversely affected the reproductive capacity of oysters and marine medaka [4042].


The histology of the testes (Figure 1) showed marked difference between the control group and the treated group. Photomicrograph of the control group (GP 1) shows seminiferous tubules containing spermatogenic cells, spermatozoa, and Sertoli cells, while the photomicrograph of the groups that received polystyrene (GP 2–4) shows morphological abnormalities in progressive distortion of testes that became prominent with vacuolation of the seminiferous tubules and reduced sperm cell levels in the group that received the highest proportion of microplastics (GP 4). Spermatogenic cells became loosely arranged in the treated groups with blank cavities appearing on the tissues with increasing PS-MPs [40].

Antioxidant assay

Both GSH-Px and GSH biomarkers showed no particular trend in their response to the exposure to polystyrene microplastics (Table 3). MDA increased marginally in the group that received the polystyrene microplastics but not proportionally dependent. The increase was not significant (p<0.05) except for the group that received 5% microplastics (Group 3), in contrast to the significant increase in MDA upon exposure to polystyrene microplastics in marine medaka [42,43]. CAT increased with the proportion of microplastics in the feed, but significantly (p<0.05) only for the group receiving the highest proportion (Group 4). SOD facilitates the breakdown of superoxide radical into molecular oxygen or hydrogen peroxide [44]. There was a significant decrease (p<0.05) in the SOD activity of the exposed groups except for the group receiving 1% microplastics. Similar trend for CAT and SOD activity in earthworms exposed to soil treated with microplastics has been reported [17].
These antioxidant enzymes are markers to assess early oxidative damages caused by xenobiotics. Increased GSH-Px, SOD, and decreased CAT activity were observed in mice exposed to microplastics [19]. Disturbed antioxidant system in aquatic organisms after exposure to microplastics has also been reported [40,45,46]. These results indicate that exposure of Wistar rats to polystyrene microplastics induced responses that caused imbalance in their antioxidant defense system.
In examining the factors that contribute to microplastic-induced toxicity, Choi et al. [47] reported that smaller microplastic size and long exposure time increased intracellular levels of reactive oxygen species. Smaller particles have been reported to induce more response due to large surface area that enhances their bioavailability [4850]. These two factors; chronic exposure and the smaller components of the polystyrene microplastics may have contributed significantly to the adverse effects observed in this study.


Findings of this study suggest that under environmentally relevant conditions, polystyrene microplastics may cause adverse effect on the reproductive and antioxidant system of male Wistar rats. Knowledge gained from this study can be applied to the study of effects of microplastics in terrestrial animals.

Conflict of interest

Authors declare no conflict of interest.


CRediT author statement
II: Conceptualization, Investigation, Supervision, Writing-Original draft preparation; BEE: Investigation, Supervision, Formal analysis, Writing-Reviewing and Editing; IOB: Investigation, Writing-Reviewing and Editing; CJO: Methodology, Validation; OSO: Investigation, Methodology, Resources; UEM: Methodology, Writing-Reviewing and Editing; CEI: Conception, Methodology, Writing-Reviewing and Editing; NJO: Methodology, Writing-Reviewing and Editing, Validation.


1. Tsang YY, Mak CW, Liebich C, Lam SW, Sze ET, Chan KM. Microplastic pollution in the marine waters and sediments of Hong Kong. Marine Pollution Bulletin 2017;115(1–2):20-28 https://doi.org/10.1016/j.marpolbul.2016.11.003 .
crossref pmid
2. Lambert S, Wagner M. Microplastics are contaminants of emerging concern in freshwater environments: an overview. Freshwater Microplastics 2018;58: 1-23 https://doi.org/10.1007/978-3-319-61615-5_1 .
3. Andrady AL. Microplastics in the marine environment. Mar Pollut Bull 2011;62: 1596-1605 https://doi.org/10.1016/j.marpolbul.2011.05.030 .
crossref pmid
4. Lambert S, Sinclair CJ, Boxall ABA. Occurrence, degradation and effects of polymer-based materials in the environment. Rev Environ Contam Toxicol 2014;227: 1-53 https://doi.org/10.1007/978-3-319-01327-5_1 .
crossref pmid
5. Okoffo ED, O’Brien S, O’Brien JW, Tscharke BJ, Thomas KV. Wastewater treatment plants as a source of plastics in the environment: a review of occurrence, methods for identification, quantification and fate. Environmental Science: Water Research & Technology 2019;5(11):1908-1931 https://doi.org/10.1039/C9EW00428A .
6. Crossman J, Hurley RR, Futter M, Nizzetto L. Transfer and transport of microplastics from biosolids to agricultural soils and the wider environment. Science of The Total Environment 2020;724: 138334 https://doi.org/10.1016/j.scitotenv.2020.138334 .
crossref pmid
7. Jambeck JR, Geyer R, Wilcox C, Siegler TR, Perryman M, Andrady A, et al. Plastic waste inputs from land into the ocean. Science 2015;347(6223):768-771 https://doi.org/10.1126/science.1260352 .
crossref pmid
8. Ilechukwu I, Ndukwe GI, Mgbemena NM, Akandu AU. Occurrence of microplastics in surface sediments of beaches in Lagos, Nigeria. European Chemical Bulletin 2019;8(11):371-375 http://dx.doi.org/10.17628/ecb.2019.8.371-375 .
9. Napper IE, Davies BF, Clifford H, Elvin S, Koldewey HJ, Mayewski PA, et al. Reaching new heights in plastic pollution-preliminary findings of microplastics on Mount Everest. One Earth 2020;3(5):621-630 https://doi.org/10.1016/j.oneear.2020.10.020 .
10. Bergmann M, Mützel S, Primpke S, Tekman MB, Trachsel J, Gerdts G. White and wonderful? Microplastics prevail in snow from the Alps to the Arctic. Science Advances; 2019. 5(8):eaax1157 https://doi.org/10.1126/sciadv.aax1157 .
crossref pmid pmc
11. Rochman CM, Brookson C, Bikker J, Djuric N, Earn A, Bucci K, et al. Rethinking microplastics as a diverse contaminant suite. Environmental Toxicology and Chemistry 2019;38(4):703-711 https://doi.org/10.1002/etc.4371 .
crossref pmid
12. Ma P, Wei Wang M, Liu H, Feng Chen Y, Xia J. Research on ecotoxicology of microplastics on freshwater aquatic organisms. Environmental Pollutants and Bioavailability 2019;31(1):131-137 https://doi.org/10.1080/26395940.2019.1580151 .
13. Galloway TS. Micro-and nano-plastics and human health In Marine anthropogenic litter; Springer; Cham: 2015. 343-366 https://doi.org/10.1007/978-3-319-16510-3_13 .

14. Ilechukwu I, Ndukwe GI, Ehigiator BE, Ezeh CS, Asogwa SL. Microplastics in silver catfish (Chrysichthys nigrodigitatus) from new Calabar River in Niger Delta, Nigeria. Ghana Journal of Science 2021;62(2):16-24 https://dx.doi.org/10.4314/gjs.v62i2.2 .
crossref pdf
15. Courtene-Jones W, Quinn B, Ewins C, Gary SF, Narayanaswamy BE. Consistent microplastic ingestion by deep-sea invertebrates over the last four decades (1976–2015), a study from the North East Atlantic. Environmental Pollution 2019;244: 503-512 https://doi.org/10.1016/j.envpol.2018.10.090 .
crossref pmid
16. Cong Y, Jin F, Tian M, Wang J, Shi H, Wang Y, et al. Ingestion, egestion and post-exposure effects of polystyrene microspheres on marine medaka (Oryzias melastigma). Chemosphere 2019;228: 93-100 https://doi.org/10.1016/j.chemosphere.2019.04.098 .
crossref pmid
17. Wang J, Coffin S, Sun C, Schlenk D, Gan J. Negligible effects of microplastics on animal fitness and HOC bioaccumulation in earthworm Eisenia fetida in soil. Environmental Pollution 2019;249: 776-784 https://doi.org/10.1016/j.envpol.2019.03.102 .
crossref pmid
18. da Costa Araujo AP, Malafaia G. Microplastic ingestion induces behavioral disorders in mice: a preliminary study on the trophic transfer effects via tadpoles and fish. Journal of Hazardous Materials 2021;401: 123263 https://doi.org/10.1016/j.jhazmat.2020.123263 .
crossref pmid
19. Deng Y, Zhang Y, Lemos B, Ren H. Tissue accumulation of microplastics in mice and biomarker responses suggest widespread health risks of exposure. Scientific Reports 2017;7(1):1-10 https://doi.org/10.1038/srep46687 .
crossref pmid pmc
20. Trestrail C, Nugegoda D, Shimeta J. Invertebrate responses to microplastic ingestion: Reviewing the role of the antioxidant system. Science of The Total Environment 2020;734: 138559 https://doi.org/10.1016/j.scitotenv.2020.138559 .
crossref pmid
21. Amereh F, Babaei M, Eslami A, Fazelipour S, Rafiee M. The emerging risk of exposure to nano (micro) plastics on endocrine disturbance and reproductive toxicity: from a hypothetical scenario to a global public health challenge. Environmental Pollution 2020;261: 114158 https://doi.org/10.1016/j.envpol.2020.114158 .
crossref pmid
22. Mak CW, Yeung KCF, Chan KM. Acute toxic effects of polyethylene microplastic on adult zebrafish. Ecotoxicology and environmental safety 2019;182: 109442 https://doi.org/10.1016/j.ecoenv.2019.109442 .
crossref pmid
23. Ziajahromi S, Kumar A, Neale PA, Leusch FD. Impact of microplastic beads and fibers on water flea (Ceriodaphnia dubia) survival, growth, and reproduction: implications of single and mixture exposures. Environmental Science & Technology 2017;51(22):13397-13406 https://doi.org/10.1021/acs.est.7b03574 .
crossref pmid
24. Bond T, Ferrandiz-Mas V, Felipe-Sotelo M, Van Sebille E. The occurrence and degradation of aquatic plastic litter based on polymer physicochemical properties: A review. Critical Reviews in Environmental Science and Technology 2018;48(7–9):685-722 https://doi.org/10.1080/10643389.2018.1483155 .
25. Rochman CM, Manzano C, Hentschel BT, Simonich SLM, Hoh E. Polystyrene plastic: a source and sink for polycyclic aromatic hydrocarbons in the marine environment. Environmental Science & Technology 2013;47(24):13976-13984 https://doi.org/10.1021/es403605f .
crossref pmid pmc
26. Fadare OO, Wan B, Guo LH, Zhao L. Microplastics from consumer plastic food containers: Are we consuming it? Chemosphere 2020;253: 126787 https://doi.org/10.1016/j.chemosphere.2020.126787 .
crossref pmid
27. Muncke J, Andersson AM, Backhaus T, Boucher JM, Carney Almroth B, Castillo Castillo A, et al. Impacts of food contact chemicals on human health: a consensus statement. Environmental Health 2020;19(1):1-12 https://doi.org/10.1186/s12940-020-0572-5 .
crossref pmid pmc
28. Gewert B, Plassmann MM, MacLeod M. Pathways for degradation of plastic polymers floating in the marine environment. Environmental science: processes & impacts 2015;17(9):1513-1521 https://doi.org/10.1039/C5EM00207A .
crossref pmid
29. de Souza Machado AA, Lau CW, Till J, Kloas W, Lehmann A, Becker R, et al. Impacts of microplastics on the soil biophysical environment. Environmental Science & Technology 2018;52(17):9656-9665 https://doi.org/10.1021/acs.est.8b02212 .
crossref pmid pmc
30. Qi Y, Yang X, Pelaez AM, Lwanga EH, Beriot N, Gertsen H, et al. Macro-and micro-plastics in soil-plant system: effects of plastic mulch film residues on wheat (Triticum aestivum) growth. Science of the Total Environment 2018;645: 1048-1056 https://doi.org/10.1016/j.scitotenv.2018.07.229 .
crossref pmid
31. Ellman GL. A colorimetric method for determining low concentrations of mercaptans. Archives of Biochemistry and Biophysics 1958;74(2):443-450 https://doi.org/10.1016/0003-9861(58)90014-6 .
crossref pmid
32. Uchiyama M, Mihara M. Determination of malonaldehyde precursor in tissues by thiobarbituric acid test. Analytical Biochemistry 1978;86(1):271-278 https://doi.org/10.1016/0003-2697(78)90342-1 .
crossref pmid
33. Aebi H. Catalase in Vitro. In: Packer L, editor. Oxygen Radicals in Biological Systems, Methods in Enzymology. 1984. 105: p. 121-126 https://doi.org/10.1016/S0076-6879(84)05016-3 .
34. Flohé L, Günzler WA. Assays of glutathione peroxidase. Methods in Enzymology 1984;105: 114-120 https://doi.org/10.1016/S0076-6879(84)05015-1 .
crossref pmid
35. Misra HP, Fridovich I. The role of superoxide anion in the autoxidation of epinephrine and a simple assay for superoxide dismutase. Journal of Biological Chemistry 1972;247(10):3170-3175 https://doi.org/10.1016/S0021-9258(19)45228-9 .
crossref pmid
36. Zemjanis R. Collection and Evaluation of Semen. Diagnostic and Therapeutic Techniques in Animal Reproduction. 2nd edition. Williams and Wilson; Baltimore: 1970. p. 139-156.

37. Pant N, Srivastava SP. Testicular and spermatotoxic effects of quinalphos in rats. Journal of Applied Toxicology: An International Journal 2003;23(4):271-274 https://doi.org/10.1002/jat.919 .
crossref pmid
38. Wells ME, Awa OA. New technique for assessing acrosomal characteristics of spermatozoa. Journal of Dairy Science 1970;53(2):227-232 https://doi.org/10.3168/jds.S0022-0302(70)86184-7 .
crossref pmid
39. Adedara IA, Alake SE, Adeyemo MO, Olajide LO, Ajibade TO, Farombi EO. Taurine enhances spermatogenic function and antioxidant defense mechanisms in testes and epididymis of L-NAME-induced hypertensive rats. Biomedicine & Pharmacotherapy 2018;97: 181-189 https://doi.org/10.1016/j.biopha.2017.10.095 .
crossref pmid
40. Xie X, Deng T, Duan J, Xie J, Yuan J, Chen M. Exposure to polystyrene microplastics causes reproductive toxicity through oxidative stress and activation of the p38 MAPK signaling pathway. Ecotoxicology and Environmental Safety 2020;190: 110133 https://doi.org/10.1016/j.ecoenv.2019.110133 .
crossref pmid
41. Jin H, Ma T, Sha X, Liu Z, Zhou Y, Meng X, et al. Polystyrene microplastics induced male reproductive toxicity in mice. Journal of Hazardous Materials 2021;401: 123430 https://doi.org/10.1016/j.jhazmat.2020.123430 .
crossref pmid
42. Wang J, Li Y, Lu L, Zheng M, Zhang X, Tian H, et al. Polystyrene microplastics cause tissue damages, sex-specific reproductive disruption and transgenerational effects in marine medaka (Oryzias melastigma). Environmental Pollution 2019;254: 113024 https://doi.org/10.1016/j.envpol.2019.113024 .
crossref pmid
43. Sussarellu R, Suquet M, Thomas Y, Lambert C, Fabioux C, Pernet MEJ, et al. Oyster reproduction is affected by exposure to polystyrene microplastics. Proceedings of the National Academy of Sciences 2016;113(9):2430-2435 https://doi.org/10.1073/pnas.1519019113 .
crossref pmid pmc
44. Mittler R. Oxidative stress, antioxidants and stress tolerance. Trends in Plant Science 2002;7(9):405-410 https://doi.org/10.1016/s1360-1385(02)02312-9 .
crossref pmid
45. Barboza LGA, Vieira LR, Branco V, Figueiredo N, Carvalho F, Carvalho C, et al. Microplastics cause neurotoxicity, oxidative damage and energy-related changes and interact with the bioaccumulation of mercury in the European seabass, Dicentrarchus labrax (Linnaeus, 1758). Aquatic toxicology 2018;195: 49-57 https://doi.org/10.1016/j.aquatox.2017.12.008 .
crossref pmid
46. Jeong CB, Won EJ, Kang HM, Lee MC, Hwang DS, Hwang UK, et al. Microplastic size-dependent toxicity, oxidative stress induction, and p-JNK and p-p38 activation in the Monogonot Rotifer (Brachionus koreanus). Environ Sci Technol 2016;50(16):8849-8857 https://doi.org/10.1021/acs.est.6b01441 .
crossref pmid
47. Choi JS, Hong SH, Park JW. Evaluation of microplastic toxicity in accordance with different sizes and exposure times in the marine copepod Tigriopus japonicus . Marine Environmental Research 2020;153: 104838 https://doi.org/10.1016/j.marenvres.2019.104838 .
crossref pmid
48. Wu D, Wang T, Wang J, Jiang L, Yin Y, Guo H. Size-dependent toxic effects of polystyrene microplastic exposure on Microcystis aeruginosa growth and microcystin production. Science of The Total Environment 2021;761: 143265 https://doi.org/10.1016/j.scitotenv.2020.143265 .
crossref pmid
49. Bucci K, Rochman CM. Microplastics: a multidimensional contaminant requires a multidimensional framework for assessing risk. Microplastics and Nanoplastics 2022;2(1):1-9 https://doi.org/10.1186/s43591-022-00028-0 .
50. Wieland S, Balmes A, Bender J, Kitzinger J, Meyer F, Ramsperger AF, et al. From properties to toxicity: comparing microplastics to other airborne microparticles. Journal of Hazardous Materials 2022;428: 128151 https://doi.org/10.1016/j.jhazmat.2021.128151 .
crossref pmid

Figure 1
H&E stain of the of the testicular tissue. A–D; A: Control group, B: 1 % PS-MPS, C: 5 % PS-MPS, D: 10 % PS-MPS. Black arrow (GP D) indicates blank cavities and lines (GP A) show normal cavities.
Table 1
Weight of the animals before and after treatment.
Groups Initial body weight (g) Final body weight (g)
Control (Group 1) 123.3±8.0a 237.8±7.5a
Group 2 111.0±3.1a 221.5±5.7a
Group 3 112.5±2.2a 198.3±16.3b
Group 4 118.8±4.6a 213.3±5.1b
Table 2
Effect of polystyrene microparticles on the sperm quality and testosterone levels of male Wistar rat.
Parameter Viability (%) Volume (mL) Normal morphology (%) Abnormal morphology (%) Motility (%) Sluggish (%) Dead (%) Sperm cell count (x 106 sperm/mL) Testosterone (ng/mL)
Group 1 86.3±2.4a 0.25±0.03a 85.0±2.0a 15.0±2.0a 81.3±1.3a 8.8±1.3a 11.3±1.3a 825±52a 4.34±0.2a
Group 2 83.8±2.4a 0.15±0.03a 78.8±3.2a 21.3±3.2a 75.0±2.0a 10.0±0.0a 15.0±2.0a 538±24b 3.53±0.6a
Group 3 73.8±2.4 a 0.15±0.02a 71.3±2.4a 28.8±2.4a 66.3±2.4b 11.3±1.3a 22.5±3.2a 513±43b 1.68±0.2b
Group 4 78.8±4.3 a 0.09±0.04b 75.0±5.4a 25.0±5.4a 66.3±5.5b 11.3±1.3a 22.5±4.8a 375±85b 1.52±0.2b

Values are means±standard error of mean. n=4. Values with different superscript are statistically significant at (p<0.05).

Table 3
Effect of polystyrene microparticles on the oxidative stress/antioxidant status of male Wistar rats.
Groups GSH (μmol/mL) GSH-Px (μmol/mL) CAT(U/mL) SOD (U/mL) MDA (μmol/mL)
Control (Group 1) 2.2±0.3a 0.12±0.01 a 3.5±0.4 a 0.20±0.04 a 0.61±0.04 a
Group 2 2.5±0.4 a 0.11±0.01 a 3.7±0.9 a 0.18±0.08 a 0.62±0.10 a
Group 3 2.1±0.04 a 0.12±0.00 a 3.9±1.1 a 0.12±0.02 b 0.72±0.05 b
Group 4 2.4±0.04 a 0.11±0.02 a 5.8±2.3 b 0.12±0.05 b 0.71±0.08 a

Values are means±standard error of mean. n=4. Values with different superscript are statistically significant at (p<0.05).

Editorial Office
Division of Environmental Science and Ecological Engineering, Korea University
145 Anam-ro, Seongbuk-gu, Seoul 02841, Korea
Tel : +82-32-560-7520   E-mail: envitoxic@gmail.com
About |  Browse Articles |  Current Issue |  For Authors and Reviewers
Copyright © 2024 by The Korean Society of Environmental Health and Toxicology & Korea Society for Environmental Analysis.     Developed in M2PI