Recently, the concerns about micro- and nano-plastics (NPs) toxicity have been increasing constantly, however the investigations are quiet meager. The present study provides evidences on the toxicological prospectives of virgin-, coronated- and isolated-NPs on human blood cells and Allium cepa root tip, respectively. Several plasma proteins displayed strong affinity towards NPs and produced multi-layered corona of 13 nm to 600 nm size. The coronated-NPs often attracted each other via non-specific protein-protein attraction which subsequently induced protein-induced coalescence in NPs. In the protein point of view, the interaction caused conformational changes and denaturation of protein thereby turned it as bio-incompatible. The coronated-NPs with increased protein confirmation changes caused higher genotoxic and cytotoxic effect in human blood cells than the virgin-NPs. On the other hand, virgin-NPs and the NPs isolated from facial scrubs hindered the root growth and caused chromosome aberration (ring formation, C-mitotic and chromosomal breaks, etc.) in root of Allium cepa. At the outset, the present study highlights the urgent need of scrutinization and regulation of NPs use in medical applications and pre-requisition of additional studies for assessing the bio-accumulation and bio-magnification of NPs.
Because of modern consumption culture, plastic usage has deep routed in our daily life, thereby the global virgin plastic production escalated to a total of 8300 million metric tons (Mt) in 2015, of which around 4977 Mt waste had been generated and accumulated in natural environment1. Owing to the sustainability, flexibility, durability, stability, long-lasting ability, viscosity and bioavailability, the cosmetics, personal care, textile and food packaging industries incorporates plastic materials in wide range of products2,3,4. For instance, facial masks, lipstick, mascara, eye shadow, anti-wrinkle creams, soap, shampoo, conditioner, moisturizers, shower gel, hair spray, hair coloring, scrubs, toothpaste, deodorant, shaving cream, sunscreen, insect repellent, yoga pants, t-shirts, jeans, fleece, socks, running shorts, acrylic onesies, microfiber cleaning cloths, unbending plate and holders, expendable eating utensils, frothed mugs, plates, bowls2,5,6 and many other products ubiquitously composed of 1 to 90% of plastic. From these products as well as from indiscriminately discharged plastic polymer debris, including polyvinylchloride, polylactic acid, nylon, polypropylene, polyethylene and polystyrene, small plastic fragments called micro-plastics (cannot be decomposed or collected for recycling) are derived, enters water ways through drains and reaches aquatic environment. As a result, micro-plastics (MPs) are now pervasive in the environment and found worldwide7. In the environment these MPs are progressively broken into nano-plastics (NPs) due to physical, chemical and biological processes8.
Over the past few decades, polystyrenes a prevalent MPs and NPs being used in various day-to-day life products. These plastics can easily enter in to the cells through clathrin-coated vesicles9, macro pinocytosis10 and phagocytosis2 and interacts with various bio-molecules due to their expansive surface to mass proportion and smaller size. Particularly, the interaction with proteins produce polystyrene-protein complex and upon complexation, a protein coat is formed commonly alludes as corona11. Formation of biomolecular corona on MPs/NPs subsequently provides them a new biological identity; to escape from immune system, prolonged persistence in circulation and interfere cellular and molecular processes. Studies reported that protein corona reduces the RBC agglutination compare to the virgin-NPs12, successively translocate the NPs to all organs and accumulates/aggregates in liver, kidney and gut13,14. This uninterrupted entry of coronated-NPs in biological system could pave the way to unanticipated effects and eventually promotes them as a potential health hazard.
Recently, studies on MPs and NPs have grown exponentially revealing the discharges from the cosmetics and personal care products have potential harmful consequences towards wide range of animals and environment. For instance, the pseudocoelomate animal Brachionus koreanus (rotifer)15 and the crustaceans Tigriopus japonicas (copepod)16 showed significant reduction in growth rate and retardation, respectively upon exposure to MPs. Further, MPs displayed significant histological changes in the tissue and cellular level of blue mussel (Mytilus edulis L.)17, sea bass (Dicentrarchus labrax)18 and reduction in feeding activity in lugworm Arenicola marina19. In Eisenia andrei (earthworms), fibrosis, congestion and inflammatory infiltrates were observed20, and in microalgae namely, Chlorella sp. and Scenedesmus sp., the physical adsorption of polystyrene micro-beads inhibited the photosynthesis process21. Though there are indisputable evidences on the significant deformity at the cellular level and accumulation of NPs in the vital organs, the effect magnitude and the fate of micro-plastics is still uncertain. Therefore, the present study intended to assess (i) the physical changes in virgin-NPs during protein interaction, (ii) adverse effects of plasma coronated-NPs on human blood cells, (iii) toxicological impacts of virgin-NPs and the NPs isolated from cosmetics against human blood cells and Allium cepa root cells.
Result and Discussion
Though MPs and NPs have constantly been released and persisted in the environment for more than 50 years, only very recently they were identified and acquainted. Since then few studies have demonstrated their adverse effects in human and environmental health. Privation of fundamental knowledge that links the physical changes of MP/NP’s to the biological macro-molecular interactions, thus triggered molecular alterations and cell toxicity is the break down to understand and evaluate the harmfulness of plastics to humans22,23,24. Therefore, in the present study, we first investigated the interactive prospectives of virgin-NPs with HSA and with human plasma followed by physical changes in NPs and proteins, secondly, tested the adverse effects of plasma coronated- and virgin-NPs on human blood cells, and finally, evaluated the cytotoxic and genotoxic effect of NPs isolated from commercial face scrubs on the human blood cells as well as A. cepa root tips.
Protein corona formation on Virgin-NPs
Interaction of virgin-NPs with HSA demonstrated three significant manifestations, such as protein corona formation, protein-induced coalescence of NPs, and secondary and tertiary structural changes in HSA. At the initial stages of the interaction, the polymeric property of NPs (Fig. 1) was disoriented and separated from each other upon HSA addition. As soon as HSA interacts with NPs, a primary cluster of HSA forms around the NPs and stabilizes by means of crowding effect25. This process can be repeated until the entire surface filled with HSA, resulted as protein corona (Fig. 2). In the beginning, the abundance of free HSA forms weak and dynamic interactions with NPs to set equilibrium amongst free and bound HSA. Over time, the equilibrium moves to the HSA adsorbed with higher affinity, which modifies the initial corona arrangements, thermodynamically stabilizes and brings it to an irreversible minimum energy state. The former known as soft corona consisting of loosely bound HSA due to low affinity and the latter is hard corona comprises tightly bound HSA26. The thickness of the corona can be determined by the secondary binders that are associated with the primary binders (HSA bound on NPs) via protein – protein interaction. Layer by layer association of secondary binders produces multi-layered corona with the size ranging from 13 nm (Fig. 2a) to 135 nm (Fig. 2f). Variation in corona size could be due to the bonding sites paucity or free protein scarcity in the solution.
Although, the binding mechanism of protein with NPs is not fully understood, it is believed that the biomolecules can binds on the NPs surfaces via non-specific attraction forces especially, Van der Waals forces or by the electric polarity alteration of approaching molecules leads to the establishment of strong bond (hydrophobic) between them or by simple dipole against dipole bonding particularly, hydrogen bond via hydrophilic chemical groups (─OH, ═O, ─NH, ═NH, ≡N)27 or by the spontaneous adsorption depending on the amino acid content, where the imidazole ring of histidine (His), side chains of phenylalanine (Phe) and tyrosine (Tyr), pyrrole ring proline (Pro) and isopropyl group of valine (Val) could possibly establish strong interaction with the benzene ring of polystyrene NPs28. Apart from these residues, aspartic acid (Asp), arginine (Arg), histidine (His), tryptophan (Trp) and glutamine (Gln) may institute the electrostatic adsorption with polystyrene NPs29. Considering HSA, the most abundant protein in serum composed of 18 Tyr, 31 Phe and 1 Trp, and 34 disulfide bonds that could provide rapid binding (within seconds to minutes) towards NPs and therefore, found as the major proportion of corona in the serum interaction studies30,31.
Protein induced NPs coalescence
Up till now, majority of investigation focused only on the protein confirmation and its functional properties, herein we provide first evidence on the diffusion and coalescence of NPs directed by the protein corona. Figure 3, demonstrates the approach of two coronated-NPs by means of non-specific protein-protein attraction where a thread like structure that connecting two NPs was observed (Fig. 3c), followed by corona reorientation that produces neck like bridge between two NPs (Fig. 3d,e), widening of bridge for the diffusion of NP to coalesce with other (Fig. 3f), and finally, coalesced NPs inclined to a round shape with multi-layered HSA corona (Fig. 3i). Because of the coalescence effect, there is a significant grain growth by means of successive coalescence (Fig. 3g,h) was observed in NPs. This observation clearly proves the remarkable coalescence effect of NPs upon interaction with protein (Fig. 4) that has been documented as aggregation in previous studies13,32. So far, many phenomenon namely, Brownian coalescence wherein collision occurs between particulates due to Brownian motion, Ostwald ripening where the particulates turns in to large ones through molecular diffusion across the intervening continuous phase, hydrodynamic coarsening via particulates interfacial velocity, coalescence-induced coalescence and diffusion-induced coalescence have been proposed for particulate coarsening effect33. Herein, we observed the protein-induced coalescence of NPs, where the NPs possibly dissolves during strong surface pressure produced by corona while approaching to larger coronated-NPs, diffuses across the neck like protein-bridge and coalesces with the other NPs. The TEM observations of coalescence effect revealed that three to four coronated-NPs coalesced to produce 500 nm size particles (Fig. 3g–i). Depending on the time, particle quantity and HSA concentration, the particle size can increase several fold (Fig. S3c,d).
Protein conformation changes
On the other hand, conformational change in the protein structure was elucidated by spectroscopic and electrophoretic studies. Upon stable and continuous interaction with NPs, HSA produce hyper-chromatic effect reflecting the ground state complex formation in the micro-environment. Under UV spectrophotometry, HSA exhibited absorbance maxima ~280 nm due to π → π* transition of the tryptophan or tyrosine residues34. Whereas, the absorption spectra of HSA-NPs complex derived from NPs concentration 10, 25, 50, 75, & 100 μg/mL, showed gradual increase in the peak intensity at 276 nm (Fig. 5a) while at constant protein concentration, which could be due to the complexation of HSA with NP as well as secondary structure changes owing to hyper affinity. Further, there was no significant shift in the λmax observed. On contrary, the fluorescence emission property of tyrosin and/or tryptophan and/or phenylalanine residues of HSA was interfered during NPs complexation which caused variation in the intrinsic fluorescence signifying the structural changes. The λem of native HSA at 340 nm was blue shifted to 335 nm with significant quenching effect upon interaction with increasing concentration of NPs (Fig. 5a). Generally, the blue shifting of λem of protein indicates the alteration in the aromatic micro-environment and interaction of Trp residues35,36 with other molecules, whereas the quenching could be due to the collision of quencher molecules with the excited fluorescent residues that leads to the blocking of proton emission (collisional or dynamic quenching) or by the complex formation between the quencher and fluorophore at the ground state (static quenching)37,38. Apart from the excited or ground state reaction, the spectral variations can also be produced by the molecular rearrangements, energy transfer, protein conformational changes, substrate binding, subunit association and denaturation39. Herein, the hyper-chromatic and quenching effect of HSA upon interaction with NPs reveals the existence of static quenching as well as conformational changes in the HSA40. The binding parameters for HSA and NPs were assessed by Stern–Volmer (F0/F vs. [NP]) and double logarithmic plot (log (F0 − F/F) vs. log[NP]) at 290, 300, & 310 K.
Wherein, F0 and F are the fluorescence intensity of HSA of pre- and post-NP interaction, Ksv is Stern-Volmer constant, Kq is dynamic quenching rate constant, τ0 is the life time of HSA without quencher, K is binding constant of HSA, n is number of binding sites and NP is nano-plastics in different concentration. The Stern-Volmer quenching plot presented in Fig. 5b and the Kq was found to be 0.008 × 1013, 0.0096 × 1013, and 0.0055 × 1013 (L mol−1) for 290, 300, and 310 K, respectively. From the double logarithmic eq., the K values for respective temperature were determined as 3.801, 5.726 and 1.341 L mol−1 and the n value was found close to be 1 denoting single binding site.
Under CD spectroscopy, the quantitative secondary and tertiary structure of HSA pre- and post-NPs complex was investigated. In which the native HSA produced two minima at 208 and 221 nm and a maxima at 215 nm corresponding to π − π* transition as well as α helix, π − π* transition for both α helix and random coiling, and β sheet, respectively41. Figure 5c shows the CD spectra of HSA-NP complexation, wherein a notable increase in the ellipticity at 208 and 221 nm and spectral shape changes was observed upon complexation denoting the intra-molecular H-bonding rearrangements. Complexation of HSA with different concentration of NPs showed increase in the percentage of α helix structure and reduction in β sheet percentage evidencing the additional stabilization of HSA secondary structure42 induced by NPs. Further, the reduction in β sheet percentage suggests the amino acid residues of polypeptide chain binding with NPs, which cause partial unfolding. Since the protein structure controls its function and drives them either as beneficial or harmful, the conformational changes in the HSA structure could eventually change their function. In order to compare the secondary structure of native and adsorbed HSA, FT-IR spectroscopy was employed. The infrared spectra (Fig. 5d) of HSA-NP complexation showed slight peak shift and drastic increase in intensity of the protein amide I band at 1651 cm−1 and amide II band at 1545 cm−1 corresponding to C═O stretch and C─N stretching coupled with N─H bending, respectively indicating the structural changes in intra-molecular bonding. Further, the strong interaction of NPs with HSA’s C─N groups was evident from the high frequency shifting of N─H stretching of amide A band at 3296 cm−1 43 towards 3372 cm−1. In addition, the C─O stretching at 1072 cm−1 shifted to 1076 cm−1 upon complexation. The alterations and increase in the band intensity of amide I and II bands of HSA confirms the continuous interaction/adsorption of HSA with NPs as well as the significant alterations in HSA confirmation42. Subsequently, the HSA conformation changes exhibited difference in band density among HSA of pre- and post-NPs interaction in relation to NPs concentration under SDS-PAGE (Fig. 6a). While increasing the NPs concentration, significant decrease in the band density at 67 kDa was recorded (Fig. 6b). The electrophoretic and spectral data strongly suggests that the NPs sturdily cause alterations in the HSA conformation.
Interaction of NPs with blood plasma
In order to delve into the corona formation, NPs coalescence, and protein conformation effects in human body, different concentrations of virgin-NPs were introduced to human plasma. As expected, multilayered protein corona with size range of 100 to 600 nm was observed (Fig. 7). As mentioned above, increase in the corona size can possibly accomplished by the protein concentration in the medium. Since, plasma is the protein reserve of human body containing albumins as main protein mass, the corona formation could be mainly influenced by albumins followed by other plasma proteins that could probably serve as secondary binders (Fig. S4)11,30,31,44. During corona formation in protein mixture, protein displacement from corona due to affinity competition between proteins could occur, where the weak affinity proteins can be replaced with strong affinity proteins, called Vroman effect, which produce hard corona45,46. However, final protein composition in the corona can be primarily influenced by material type, size, and surface properties, as well as the protein medium composition and experimental conditions11,47,48.
Formation of several 100 nm size corona could comfort the cellular uptake, distribution, excretion and related toxicity of NPs inside the body. As seen in the HSA-NPs interaction, a significant increase in the grain size of NPs (upto 1 μm) was observed during plasma interaction as well (Fig. 7b,c). Such grain growth could be achieved via plasma protein-induced coalescence of multiple coronated-NPs as displayed in Fig. 7f–i. Further, these coronated-NPs were subjected to SDS-PAGE, which confirms several plasma proteins especially, albumins, globulins, fibrinogens and other proteins are adsorbed to the NPs surface49 and these proteins play significant roles including, maintaining osmatic pressure, molecule transport, immune response, enzyme activity and blood coagulation, respectively. SDS-PAGE analysis also demonstrated that upon increasing the NPs concentration there is a gradual decrease in the overall protein band intensity and appearance and disappearance of protein bands (Fig. S4). It appears at 50 μg/mL NPs concentration, the plasma protein interaction encounters the equilibrium amongst free and bound proteins and thus there is notable difference in the protein bands (Fig. S4) suggesting the possibility of increased proteins conformational changes.
Human and environmental toxicity of NPs
Physico-chemical properties such as, size, shape and surface properties, and additives as well as sorbed material can influence NPs/MPs biological ramifications. Studies on fluorescence polystyrene NPs revealed that the toxicity, persistence and excretion of NPs in organisms are size dependent process. For example, in rotifers, larger NPs (>100 nm) were accumulated in gut and excreted simultaneously, whereas small NPs (<50 nm) apparently pass through the intestinal wall, entered tissues and organs through circulation, and reached extruded eggs50. Numerous controlled laboratory studies on MPs/NPs displayed size dependent milder to chronic conditions in various ecological targets ranging from planktonic species to filter-feeders and bottom grazers and from earthworms (Lumbricus terrestris) to terrestrial birds. The conditions includes, compromised immune responses in fathead minnows (Pimephales promelas)32, induced liver lesions in zebrafish (Danio rerio)51, reduced reproduction, feeding, growth rate in rotifers50 and Lumbricus terrestris52, embryotoxicity in sea urchin53 and mortality and multiple molting in brine shrimp54 and blockage of intestinal tract and compromised the feeding and digestion in Mediterranean seabirds55. Although several studies demonstrated, the accumulation and persistence of NPs in terrestrial birds, earthworms, rotifers and other organisms56,57,58, the exact damage caused by NPs or its mechanism of action were not identified, however negative effects are inevitable due to the carcinogenic plastics additives especially, phthalates, bisphenol A, brominated flame retardants, triclosan, bisphenone and organotins59 and sorbed pollutants60 that leach into cells. At the outset, it is assumed that in any organism, ingested nano-plastics will typically reach the intestine via peristaltic action, where it can be (i) incorporated with fecal matter and excreted61; (ii) adsorbed and entrapped across gut lining and block the intestine; or (iii) uptaken by gut enterocytes and accumulated in villi then pass through the blood stream and reaches other organs/tissues50 prior entering liver for recirculation into small intestine via bile62. It is noteworthy to mention that it has been speculated that increase in wildlife cancer might be reflected from global plastic contamination63 however, evidence to support or refute this claim as well as fate of NPs post-ingestion are scanty.
Biocompatibility of NPs in human
To substantiate the toxic effects in blood stream, human lymphocytes and erythrocytes were exposed to coronated-NPs under in vitro condition. Wherein, the cytotoxic effect was investigated via MTT assay64,65 and the erythrocytes lysis was determined by hemoglobin release via spectrophotometric analysis. The percentage of cytotoxicity and hemolysis caused by coronated-NPs is presented in Fig. 8. It is witnessed that the lymphocytotoxic activity and hemolysis activity are increasing with the coronated-NPs derived from increasing concentrations of NPs and with the proteins with increased conformational changes. Five and 7.5 μg/mL coronated-NPs caused 61 and 70% cytotoxicity and 91 and 83% hemolysis, respectively on WBC and RBC as a result of higher conformational changes in plasma protein whereas virgin-NPs caused 20 and 27% WBC inhibition and 22 and 36% RBC lysis. This observation evidences that the protein coronation with increased conformation greatly influences the cytotoxicity and hemolytic activity of NPs. On the other side, isolated-NPs from face scrubs caused 25% cytotoxicity and 40% hemolysis at 5 μg/mL concentration, while 25 μg/mL showed 40 and 70% activity, respectively. The increase in the toxicity of isolated-NPs than the virgin-NPs may be due to the chemical additives carried on its surface or the existence of other toxic polymer NPs. Additionally, the genotoxic effect of coronated-, virgin- and isolated-NPs against individual lymphocytes were manifested via single cell gel electrophoresis assay. The degree of DNA damage was quantified by measuring the migration of the genetic material from cell’s nucleus and resulting DNA tail, where the cells with significant DNA damage exhibits an increased migration of DNA towards electrophoresis direction. Among the comet parameters, the most frequently used tail parameters; per cent of DNA in tail, olive tail moment and tail migration66 were presented in Fig. 9. Certainly, the tail moment delivers the steadiest assessments for DNA damage66. In the present study, an extensive DNA damage in lymphocytes was observed at 5 μg/mL concentration of coronated-NPs when compare to virgin-NPs. The observed genotoxic in lymphocytes treated with coronated- and virgin-NPs were in good correlation with the cytotoxic and hemolytic effect. The increased effect of coronated-NPs at the tested concentrations signifies the effect magnitude can be influenced by plasma protein confirmation i.e. after interaction with NPs the plasma protein turns into bio-incompatible and delivering an altered biological activity. It is noteworthy to mention that isolated-NPs showed significant genotoxic effect than virgin-NPs, however the effect is lesser than the coronated-NPs.
Studies on polystyrene NPs mediated genotoxicity (DNA damage) and chromosome aberrations in human are limited. Previously, delayed G1 phase and decreased cyclin (D, E) expression was observed in cancer HeLa cells as well as normal NIH 3T3 cells exposed to NH2-Polystyrene (50 nm)67. Similarly, DNA strand breaks in haemocytes and neurotoxic effects was observed in mussels (Mytilus gallaprovincialis) treated with polyethylene and polystyrene MPs68. Whereas in some studies, upregulation of stress regulator proteins at low concentration of polystyrene NPs was observed evidencing the oxidative stress induction, while at high concentration, gene expression was downregulated, this could be due to the damage in the antioxidative system or DNA69. MPs/NPs mediated oxidative damage has been reported in wide range of organisms such as lugworm Arenicola marina70, algae Chlorella and Scenedesmus21, Crab Eriocheir sinensis71 and zebrafish Danio rerio72. Although, there is no direct evidence portraying nano-plastics mediated genotoxicity in human, chromosomal aberrations73, mutations in glycophorin A74, sister chromatid exchange75, micronuclei formation75 and DNA single strand breaks76 were reported in numerous works exposed to styrene. From the present study, it is assumed that the physical damage caused by the virigin- and coronated-NPs leads to increased reactive oxygen species production and oxidative stress which ultimately cause DNA damage in blood cells similar to that of metallic nanoparticles77. Further, the increase in genotoxicity of coronated-NPs may be either due to the stress induced by denatured protein molecules or by coronated NPs or by the migrated styrene molecules78 during dissolution and coalescence effect.
Environmental toxicity of NPs
On the other hand, the exposure of virgin- and isolated-NPs to onion root tips resulted in extreme decrease in mitotic index (MI) and increase in chromosome alterations (Fig. 10). Both NPs exhibited significant and dose and time dependent decrease in the mitotic index as a result of mitotic activity suppression in A. cepa. About, 10 μg/mL NPs caused 50% reduction in mitotic index and 25–30% chromosome aberration (CA) in 3 h treatment whereas 25 μg/mL NPs declined MI below 25% and caused 35–50% CA. Therefore, the concentrations 10 and 25 μg/mL are anticipated as sublethal79 and lethal80, respectively to A. cepa root cells for 3 h treatment. At these concentrations, 35% and 80% increase in oxidative stress was observed, respectively (data not presented). Further, the degree of decrease in MI and increase in CA displayed a positive correlation with increasing NPs concentration and treatment time. Additionally, we observed that depending on the treatment time the sublethal concentration can produce lethal effect to the cells. Both virgin- and isolated-NPs caused clastogenic (pulverized nucleus, ring chromosome, chromosome fragments, etc.) and non-clastogenic (C-mitosis, polyploidy, vagrant chromosomes, etc.) abnormalities in A. cepa (Fig. 11). Where the vagrants are the magnitudes of weak C-mitosis81 which lead to aneuploidy in which the chromosomes separation is unequal and the interphase nuclei is irregular82. C-mitosis is caused by inhibited spindle formation whereas chromosome fragmentations is caused from chromosome and chromatid breaks and these are lethal mutagenic effect83. The ring chromosomes are formed during chromosomes loss from the telomeric side84. Presence of polyploid cells attributes that the NPs can cause failure in the mitotic spindle following the C-mitosis and vagrant chromosomes formation. Alterations in the nucleic acid synthesis and protein synthesis can change the cell and/or nucleus volume producing giant strap nucleus cells. Migration of nucleus through cytomictic channels during cytomixis resulting enucleated cells85. The tested concentrations 5, 15, and 20 μg/mL were also caused severe mitotic inhibition signifying the increased cytotoxic, inhibitory, mitodepressive and anti-proliferative effects of virgin- and isolated-NPs. Certainly, drastic decrease in the MI suggests that there is a potential inhibition of DNA synthesis, seizure of mitotic phases and deceleration of cell progression. Apart from the prominent cytological aberrations presented, lesions, stickiness, polyploidy, hypoploid, chromosome bridges, chromosome coagulation, etc. were also detected in the root tips. The observed results clearly demonstrate the ability of NP/MPs to interrupt the nucleic acid metabolism, thereby affecting the DNA and protein synthesis, that results in an array of abnormalities. This study further provides valuable informations in relation to possible mutagenic effects of NPs on other plants and mammals. The observed abnormalities in cells demonstrates that the NP/MPs in the environment may possibly affect the mitotic spindle as well as chromosome structure of plant and animal cells when the concentration reaches the threshold level, and therefore it has to be regarded as hazardous substance.
At the outset, the present study provides direct evidences on; (i) multilayered corona formation on NPs during protein interaction and corona mediated protein-induced coalescence of NPs, while, from the protein point of view, the interaction caused conformational changes and denaturation of protein thereby turning it as bio-incompatible, (ii) the plasma coronated-NPs with increased protein structural alterations could cause extended cytotoxic and genotoxic effects on blood cells in compare to the virgin-NPs (Fig. 12), (iii) NPs released from cosmetics and other products could interrupt the nucleic acid metabolism; consequently affects the DNA and protein synthesis (Fig. 12). It is expected that the NPs with less/un-altered protein corona could inevitably provide a new biological identity to NPs and MPs, eventually promoting them to interfere with biological pathways and conceals them form immune response. As mentioned above, protein secondary and tertiary structural changes and deformation due to the NPs interaction and corona formation may turn the complex as immunogenic (immunogenic epitope generation) which could possibly induce the autoimmune reaction86,87. Recently, there has been increasing research interest in the potential application of NPs various medical applications, especially as drug delivery system88,89. In this circumstance, the present study highlights the urgent need for studying the adverse effects of NPs of different polymer type against human, plant and other animal systems using systematic as well as meticulous approaches, in addition to assessing the impacts of coronated-NPs on the immune system, vital organs and tissue cells and related defense response.
Polystyrene nano-plastics (Catalog # 108821-10) (NPs) with the size range of 100 nm were purchased from Corpuscular Inc., NY, USA. On the other hand, NPs (~100 nm) (Fig. S1) was isolated from commercial facial scrubs using sequential filtration technique8 and used for further studies. Detailed isolation procedure is presented in the Supplementary Information.
Interaction of virgin-NPs with human serum albumin and spectral analysis
In the neutral buffer system, 0.1% of human serum albumin (HSA, Sigma–Aldrich, India) was allowed to interact with variable concentrations (10, 25, 50, 75, 100 μg/mL) of virgin-NPs for 4 h at 110 rpm in an incubator shaker. After incubation, HSA-NPs complex was separated and subjected to spectral property analysis where the changes during interaction was monitored between 200–500 nm under double beam spectrophotometer (U-2910-HITACHI, Japan). Similarly, the intrinsic emission spectra of protein after interaction with NPs at different temperatures 283 K, 300 K, & 310 K were recorded with excitation and emission wavelengths of 280 nm and 340 nm, respectively using a spectrofluorimeter (JASCO FP-8300, Japan) equipped with thermostatically peltier compartment operating with the scan speed of 200 nm/min. Further, the modifications in the secondary structure of protein after NPs interaction was measured at far UV CD spectral range (200 to 260 nm) using Circular Dichorism Spectropolarimeter (JASCO J-715, Japan) and the element of secondary structure protein were analyzed using an in build software provided by the JASCO manufacture (Tokyo, Japan). Finally, the HSA-NPs interaction was analyzed in IRAffinity-1 FT-IR spectrophotometer (Shimadzu, Japan) between the wavenumber 4000 to 500 cm−1. All the experiments and analysis preformed in this study were triplicated.
Interaction of virgin-NPs with blood plasma
Human blood was collected from five healthy male volunteers (25 to 35 year old, non-alcoholic and non-smokers) through venipuncture into heparinized vacutainers followed by plasma, erythrocytes and lymphocytes were separated and used for further experiments. All the experiments were performed in accordance with relevant bioethics guidelines and regulations and approved by Institutional Ethical Committee for Studies on Human Subjects (VIT/IECH/014/01.2015). The healthy male volunteers gave informed consent. Similar to HSA studies, five different concentrations of NPs (10, 25, 50, 75, 100 μg/mL) were allowed to interact with 3 volumes of blood plasma of each individual at room temperature for 4 h, respectively. After incubation, the samples were subjected to HR-TEM, SDS-PAGE and toxicity analysis.
HSA and plasma samples of post-NPs interaction were subjected to SDS-PAGE analysis using a 5% stacking gel and 10% separating gel under Mini-PROTEAN tetra cell system (Bio-Rad Laboratories, Inc., USA). Electrophoresis was performed according to the manufacturer’s instructions and the protein was visualized by Coomassie blue staining90.
Physical changes in the virgin-NPs interacted with HSA and plasma was examined under HR-TEM (Technai, G2 20 Twin, FEI, USA) as well as HR-SEM (Carl Zeiss Evo 18 SEM, Germany) by fixing a thin film of HSA/plasma-NP complex on copper grid. Prior to SEM analysis, the sample was coated with gold using sputter coater.
Cytotoxic effect of virgin-, coronated-, and isolated-NPs, in vitro
Lymphocytotoxic effect of NPs was assessed by evaluating metabolic activity of cells via MTT (3-(4,5-dimethylthiazol-2-yl)-2, 5-diphenyl tetrazolium bromide) assay. Briefly, 100 μL of freshly isolated lymphocytes (106 cells/mL) were seeded in flat bottom 96-well plate containing serum free RPMI-1640 medium. Later, cells were treated with 100 μL of plasma-NPs complex containing 1, 2.5, 5, 7.5 and 10 μg of NPs derived respectively from 10, 25, 50, 75 and 100 μg/mL of NPs-plasma interaction. In similar fashion, virgin-NPs dissolved in PBS were also used for the treatment. On the other hand, the toxicity of isolated-NPs was tested using 2.5, 5 and 25 μg/mL concentrations. After 24 h incubation at 37 °C, 20 μL of MTT (5 mg/mL) was added and incubated for 4 h, then 10% of DMSO was added to the wells and kept for 20 min. Optical density at 590 nm was measured on ELISA plate reader (BioTek, PowerWave XS2, USA).
Genotoxic effects of NPs in vitro
Lymphocytes isolated from the volunteers were treated with plasma coronated-NPs, virgin-NPs and isolated-NPs as above for 24 h at 37 °C. The DNA damage was assessed via comet assay using established protocol with slight modifications64,65. Detailed procedure is presented in Supplementary Information.
Hemolysis activity of NPs
In vitro hemolysis activity of plasma coronated-, virgin-, and isolated-NPs were assayed according to Lin and Haynes,91. Briefly, isolated erythrocytes were washed twice and diluted in 50 mL of PBS. About 200 μL of erythrocyte suspension was transferred to PBS (700 μL) containing 1, 2.5, 5, 7.5 and 10 μg of NPs and incubated overnight at 37 °C. After incubation, the samples were centrifuged at 10000 g for 5 min and the supernatants were transferred to 96 well plate. The absorbance values at 570 nm were recorded using a ELISA plate reader (BioTek, PowerWave XS2, USA). Percentage of hemolysis was calculated by following formula;
Toxicity study in Allium cepa
Bulbs of A. cepa were allowed to grow in ultrapure water for 2–3 days at room temperature for achieving 2–4 cm root growth. The bulbs were transferred to ultrapure water containing 5, 10, 15, 20 and 25 μg/mL of virgin-NPs. Similar set of treatment was performed with isolated-NPs. For control, separate set of bulbs were maintained in ultrapure water. At 3, 6, 12 and 24 h interval, root tips were washed (ultrapure water), hydrolyzed (1 N HCl) at 60–70 °C for 15 min. Thin sections of root tips were made and stained with aceto-orcein92, prior to microscopic examination (Detailed procedure is presented in Supplementary Information).
Since the knowledge about biomolecule mediated transformation of NPs are scanty, it is very much required to understand the NPs behavior with biomolecules and its toxicity using a controlled reference system. Therefore, application of polystyrene beads to capture the critical causes at controlled biological system could pave the way to understand the effects of real world NPs. In this work, we have preliminarily showed the protein corona could possible cause coalescence effect in the NPs apart from the protein confirmation changes. Since the prominent proteins in blood are responsible for protein-induced coalescence of NPs, we believe such grain growth in NPs entered in blood stream could possibly block the in- and out-flow of body fluids. On the other hand, the NPs can interrupt mitotic activity and cause cytotoxicity to human and animal cells. This knowledgebase could be useful for acquiring/retrieving the perceptive toxicity information and health risk from real world NPs.
Geyer, R., Jambeck, J. R. & Law, K. L. Production, use, and fate of all plastics ever made. Science advances 3, e1700782 (2017).
Revel, M., Chatel, A. & Mouneyrac, C. Micro (nano) plastics: A threat to human health? Current Opinion in Environmental Science & Health 1, 17–23 (2018).
Lorenz, C., Von Goetz, N., Scheringer, M., Wormuth, M. & HungerbÃ¼hler, K. Potential exposure of German consumers to engineered nanoparticles in cosmetics and personal care products. Nanotoxicology 5, 12–29 (2011).
Wardrop, P. et al. Chemical pollutants sorbed to ingested microbeads from personal care products accumulate in fish. Environmental science & technology 50, 4037–4044 (2016).
Jemec, A., Horvat, P., Kunej, U., Bele, M. & Krzan, A. Uptake and effects of microplastic textile fibers on freshwater crustacean Daphnia magna. Environmental Pollution 219, 201–209 (2016).
Browne, M. A. et al. Accumulation of microplastic on shorelines woldwide: sources and sinks. Environmental Science & Technology 45, 9175–9179 (2011).
Phal, S. et al. A scientific perspective on microplastics in nature and society. SAPEA (2019).
Hernandez, L. M., Yousefi, N. & Tufenkji, N. Are there nanoplastics in your personal care products? Environmental Science & Technology Letters 4, 280–285 (2017).
Jiang, X. et al. Specific effects of surface amines on polystyrene nanoparticles in their interactions with mesenchymal stem cells. Biomacromolecules 11, 748–753 (2010).
Jiang, X. et al. Specific effects of surface carboxyl groups on anionic polystyrene particles in their interactions with mesenchymal stem cells. Nanoscale 3, 2028–2035 (2011).
Lundqvist, M. et al. Nanoparticle size and surface properties determine the protein corona with possible implications for biological impacts. Proceedings of the National Academy of Sciences 105, 14265–14270 (2008).
Pan, D. et al. The effect of polymeric nanoparticles on biocompatibility of carrier red blood cells. PLOS One 11, e0152074 (2016).
Mohr, K. et al. Aggregation behavior of polystyrene-nanoparticles in human blood serum and its impact on the in vivo distribution in mice. Journal of Nanomedicine & Nanotechnology 5, 1–10 (2014).
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 7, 46687 (2017).
Jeong, C.-B. et al. Microplastic size-dependent toxicity, oxidative stress induction, and p-JNK and p-p38 activation in the monogonont rotifer (Brachionus koreanus). Environmental Science & Technology 50, 8849–8857 (2016).
Lee, K.-W., Shim, W. J., Kwon, O. Y. & Kang, J.-H. Size-dependent effects of micro polystyrene particles in the marine copepod Tigriopus japonicus. Environmental Science & Technology 47, 11278–11283 (2013).
Von Moos, N., Burkhardt-Holm, P. & Kohler, A. Uptake and effects of microplastics on cells and tissue of the blue mussel Mytilus edulis L. after an experimental exposure. Environmental Science & Technology 46, 11327–11335 (2012).
Peda, C. et al. Intestinal alterations in European sea bass Dicentrarchus labrax (Linnaeus, 1758) exposed to microplastics: preliminary results. Environmental Pollution 212, 251–256 (2016).
Wright, S. L., Rowe, D., Thompson, R. C. & Galloway, T. S. Microplastic ingestion decreases energy reserves in marine worms. Current Biology 23, R1031–R1033 (2013).
Rodriguez-Seijo, A. et al. Histopathological and molecular effects of microplastics in Eisenia andrei Bouche. Environmental Pollution 220, 495–503 (2017).
Bhattacharya, P., Lin, S., Turner, J. P. & Ke, P. C. Physical adsorption of charged plastic nanoparticles affects algal photosynthesis. The Journal of Physical Chemistry C 114, 16556–16561 (2010).
Lusher, A. In Marine anthropogenic litter 245–307 (Springer, Cham, 2015).
Law, K. L. & Thompson, R. C. Microplastics in the seas. Science 345, 144–145 (2014).
Koelmans, A. A., Besseling, E. & Shim, W. J. In Marine anthropogenic litter 325–340 (Springer, Cham, 2015).
Barbero, F. et al. Formation of the Protein Corona: The Interface between Nanoparticles and the Immune System. Seminars in immunology 34, 52–60 (2017).
Piella, J., Bastus, N. G. & Puntes, V. Size-dependent protein-nanoparticle interactions in citrate-stabilized gold nanoparticles: the emergence of the protein corona. Bioconjugate Chemistry 28, 88–97 (2017).
Esser, P. Principles in adsorption to polystyrene. Thermo Scientific Nunc Bulletin, 1–5 (1988).
Adey, N. B., Mataragnon, A. H., Rider, J. E., Carter, J. M. & Kay, B. K. Characterization of phage that bind plastic from phage-displayed random peptide libraries. Gene 156, 27–31 (1995).
Qiang, X. et al. Discovery of a polystyrene binding peptide isolated from phage display library and its application in peptide immobilization. Scientific Reports 7, 2673 (2017).
Ramezani, F. & Rafii-Tabar, H. An in-depth view of human serum albumin corona on gold nanoparticles. Molecular BioSystems 11, 454–462 (2015).
Saptarshi, S. R., Duschl, A. & Lopata, A. L. Interaction of nanoparticles with proteins: relation to bio-reactivity of the nanoparticle. Journal of Nanobiotechnology 11, 1–26 (2013).
Greven, A. C. et al. Polycarbonate and polystyrene nanoplastic particles act as stressors to the innate immune system of fathead minnow (Pimephales promelas). Environmental Toxicology and Chemistry 35, 3093–3100 (2016).
Cheng, M. H. & Nauman, E. B. Phase ripening in particulate binary polymer blends. Journal of Polymer Science Part B: Polymer Physics 42, 603–612 (2004).
Alex, S. A., Chakraborty, D., Chandrasekaran, N. & Mukherjee, A. A comprehensive investigation of the differential interaction of human serum albumin with gold nanoparticles based on the variation in morphology and surface functionalization. RSC Advances 6, 52683–52694 (2016).
Gratton, E., Jameson, D. M. & Hall, R. D. Multifrequency phase and modulation fluorometry. Annual review of biophysics and bioengineering 13, 105–124 (1984).
Gull, N., Sen, P. & Khan, R. H. Interaction of bovine (BSA), rabbit (RSA), and porcine (PSA) serum albumins with cationic single-chain/gemini surfactants: a comparative study. Langmuir 25, 11686–11691 (2009).
Montero, M. T., Hernandez, J. & Estelrich, J. Fluorescence quenching of albumin. A spectrofluorimetric experiment. Biochemical Education 18, 99–101 (1990).
Gentili, P. L., Ortica, F. & Favaro, G. Static and dynamic interaction of a naturally occurring photochromic molecule with bovine serum albumin studied by UV- visible absorption and fluorescence spectroscopy. The Journal of Physical Chemistry B 112, 16793–16801 (2008).
Zhang, G., Que, Q., Pan, J. & Guo, J. Study of the interaction between icariin and human serum albumin by fluorescence spectroscopy. Journal of Molecular Structure 881, 132–138 (2008).
Sekar, G. et al. Multiple spectroscopic studies on the interaction of BSA with pristine CNTs and their toxicity against Donax faba. Journal of Luminescence 170, 141–149 (2016).
Ishtikhar, M., Rabbani, G., Khan, S. & Khan, R. H. Biophysical investigation of thymoquinone binding to ‘N’ and ‘B’ isoforms of human serum albumin: exploring the interaction mechanism and radical scavenging activity. RSC Advances 5, 18218–18232 (2015).
N′ soukpoe-Kossi, C. N. et al. Resveratrol binding to human serum albumin. Journal of Biomolecular Structure and Dynamics 24, 277–283 (2006).
Krimm, S. & Bandekar, J. In Advances in protein chemistry Vol. 38 (eds Edsall, J. T., Anfinsen, C. B. and Richards, F. M.) 181–364 (Elsevier, 1986).
Huang, H. et al. An evaluation of blood compatibility of silver nanoparticles. Scientific Reports 6, 25518 (2016).
Vroman, L., Adams, A. L., Fischer, G. C. & Munoz, P. C. Interaction of high molecular weight kininogen, factor XII, and fibrinogen in plasma at interfaces. Blood 55, 156–159 (1980).
Van Hong Nguyen, B.-J. L. Protein corona: a new approach for nanomedicine design. International journal of nanomedicine 12, 3137 (2017).
Schottler, S., Landfester, K. & Mailander, V. Controlling the stealth effect of nanocarriers through understanding the protein corona. Angewandte Chemie International Edition 55, 8806–8815 (2016).
Tenzer, S. et al. Nanoparticle size is a critical physicochemical determinant of the human blood plasma corona: a comprehensive quantitative proteomic analysis. ACS nano 5, 7155–7167 (2011).
Hajipour, M. J., Laurent, S., Aghaie, A., Rezaee, F. & Mahmoudi, M. Personalized protein coronas: a “key” factor at the nanobiointerface. Biomaterials Science 2, 1210–1221 (2014).
Snell, T. W. & Hicks, D. G. Assessing toxicity of nanoparticles using Brachionus manjavacas (Rotifera). Environmental Toxicology 26, 146–152 (2011).
Lu, Y. et al. Uptake and accumulation of polystyrene microplastics in zebrafish (Danio rerio) and toxic effects in liver. Environmental Science & Technology 50, 4054–4060 (2016).
Huerta Lwanga, E. et al. Microplastics in the terrestrial ecosystem: implications for Lumbricus terrestris (Oligochaeta, Lumbricidae). Environmental Science & Technology 50, 2685–2691 (2016).
Della Torre, C. et al. Accumulation and embryotoxicity of polystyrene nanoparticles at early stage of development of sea urchin embryos Paracentrotus lividus. Environmental Science & Technology 48, 12302–12311 (2014).
Bergami, E. et al. Nano-sized polystyrene affects feeding, behavior and physiology of brine shrimp Artemia franciscana larvae. Ecotoxicology and Environmental Safety 123, 18–25 (2016).
Codina-Garcia, M., Militao, T., Moreno, J. & Gonzalez-Solis, J. Plastic debris in Mediterranean seabirds. Marine Pollution Bulletin 77, 220–226 (2013).
FAO. The state of world fisheries and aquaculture (SOFIA 2016). Contributing to foodsecurity and nutrition for all. Rome, 200 (2016).
GESAMP. Sources, fate and effects of microplastics in the marine environment: part 2 of a global assessment. Reports and studies-IMO/FAO/Unesco-IOC/WMO/IAEA/UN/UNEP Joint Group of Experts on the Scientific Aspects of Marine Environmental Protection (GESAMP) eng no. 93, 220 (2016).
UNEP. Marine Plastic Debris and Microplastics: Global Lessons and Research to Inspire Action and Guide Policy Change. (United Nations Environment Programme, Nairobi, 2016).
UNEP/WHO. State of the science of endocrine disrupting chemicals 2012. (World Health Organization, 2013).
Zhao, S., Zhu, L. & Li, D. Microscopic anthropogenic litter in terrestrial birds from Shanghai, China: Not only plastics but also natural fibers. Science of the Total Environment 550, 1110–1115 (2016).
EFSA. Presence of microplastics and nanoplastics in food, with particular focus on seafood. EFSA Journal 14, e04501 (2016).
Garrett, N. L., Lalatsa, A., Uchegbu, I., Schatzlein, A. & Moger, J. Exploring uptake mechanisms of oral nanomedicines using multimodal nonlinear optical microscopy. Journal of Biophotonics 5, 458–468 (2012).
Erren, T., ZeuB, D., Steffany, F. & Meyer-Rochow, B. Increase of wildlife cancer: an echo of plastic pollution? Nature Reviews Cancer 9, 842 (2009).
Tice, R. R. et al. Single cell gel/comet assay: guidelines for in vitro and in vivo genetic toxicology testing. Environmental and molecular mutagenesis 35, 206–221 (2000).
Dhawan, A., Bajpayee, M. M., Pandey, A. K. & Parmar, D. Protocol for the single cell gel electrophoresis/comet assay for rapid genotoxicity assessment. Sigma 1077 (2003).
Lee, E., Oh, E., Lee, J., Sul, D. & Lee, J. Use of the tail moment of the lymphocytes to evaluate DNA damage in human biomonitoring studies. Toxicological Sciences 81, 121–132 (2004).
Liu, Y. et al. Intracellular dynamics of cationic and anionic polystyrene nanoparticles without direct interaction with mitotic spindle and chromosomes. Biomaterials 32, 8291–8303 (2011).
Avio, C. G. et al. Pollutants bioavailability and toxicological risk from microplastics to marine mussels. Environmental Pollution 198, 211–222 (2015).
Liu, Z. et al. Polystyrene nanoplastic exposure induces immobilization, reproduction, and stress defense in the freshwater cladoceran Daphnia pulex. Chemosphere 215, 74–81 (2019).
Browne, M. A., Niven, S. J., Galloway, T. S., Rowland, S. J. & Thompson, R. C. Microplastic moves pollutants and additives to worms, reducing functions linked to health and biodiversity. Current Biology 23, 2388–2392 (2013).
Yu, P. et al. Accumulation of polystyrene microplastics in juvenile Eriocheir sinensis and oxidative stress effects in the liver. Aquatic Toxicology 200, 28–36 (2018).
Chen, Q. et al. Enhanced uptake of BPA in the presence of nanoplastics can lead to neurotoxic effects in adult zebrafish. Science of the Total Environment 609, 1312–1321 (2017).
Somorovska, M. et al. Biomonitoring of occupational exposure to styrene in a plastics lamination plant. Mutation Research/Fundamental and Molecular Mechanisms of Mutagenesis 428, 255–269 (1999).
Bigbee, W. L. et al. Glycophorin A somatic cell mutation frequencies in Finnish reinforced plastics workers exposed to styrene. Cancer Epidemiology and Prevention Biomarkers 5, 801–810 (1996).
Laffon, B., Pasaro, E. & Mendez, J. Evaluation of genotoxic effects in a group of workers exposed to low levels of styrene. Toxicology 171, 175–186 (2002).
Shamy, M. Y., Osman, H. H., Kandeel, K. M., Abdel-Moneim, N. M. & El Said, K. F. DNA single strand breaks induced by low levels of occupational exposure to styrene: the gap between standards and reality. Journal of environmental pathology, toxicology and oncology 21 (2002).
Rocha, T. L. et al. Immunocytotoxicity, cytogenotoxicity and genotoxicity of cadmium-based quantum dots in the marine mussel Mytilus galloprovincialis. Marine environmental research 101, 29–37 (2014).
Date, K. et al. Endocrine-disrupting effects of styrene oligomers that migrated from polystyrene containers into food. Food and Chemical Toxicology 40, 65–75 (2002).
Panda, B. B. & Sahu, U. K. Induction of abnormal spindle function and cytokinesis inhibition in mitotic cells of Allium cepa by the organophosphorus insecticide fensulfothion. Cytobios 42, 147–115 (1985).
Antosiewicz, D. Analysis of the cell cycle in the root meristem of Allium cepa under the influence of ledakrin. Folia Histochemica et Cytobiologica 28, 79–95 (1990).
Kovalchuk, O. et al. The Allium cepa chromosome aberration test reliably measures genotoxicity of soils of inhabited areas in the Ukraine contaminated by the Chernobyl accident. Mutation Research/Genetic Toxicology and Environmental Mutagenesis 415, 47–57 (1998).
Mustafa, Y. & Suna Arikan, E. Genotoxicity testing of quizalofop-P-ethyl herbicide using the Allium cepa anaphase-telophase chromosome aberration assay. Caryologia 61, 45–52 (2008).
Evandri, M. G., Tucci, P. & Bolle, P. Toxicological evaluation of commercial mineral water bottled in polyethylene terephthalate: a cytogenetic approach with Allium cepa. Food Additives & Contaminants 17, 1037–1045 (2000).
Khanna, N. & Sharma, S. Allium cepa root chromosomal aberration assay: a review. Indian J. Pharm 1, 3 (2013).
Prajitha, V. & Thoppil, J. E. Genotoxic and antigenotoxic potential of the aqueous leaf extracts of Amaranthus spinosus Linn. using Allium cepa assay. South African Journal of Botany 102, 18–25 (2016).
Victor, F. Physicochemical Characteristics of Protein- NP Bioconjugates: The Role of Particle Curvature and Solution Conditions on Human Serum Albumin Conformation and Fibrillogenesis Inhibition. Langmuir 28, 9113–9126 (2012).
Zhang, D. et al. Gold nanoparticles can induce the formation of protein-based aggregates at physiological pH. Nano Letters 9, 666–671 (2009).
Forte, M. et al. Polystyrene nanoparticles internalization in human gastric adenocarcinoma cells. Toxicology In Vitro 31, 126–136 (2016).
Kim, B. Y. S., Rutka, J. T. & Chan, W. C. W. Nanomedicine. New England Journal of Medicine 363, 2434–2443 (2010).
Liu, J. & Jing, H. Glycation of bovine serum albumin with monosaccharides inhibits heat-induced protein aggregation. RSC Advances 6, 115183–115188 (2016).
Lin, Y.-S. & Haynes, C. L. Impacts of mesoporous silica nanoparticle size, pore ordering, and pore integrity on hemolytic activity. Journal of the American Chemical Society 132, 4834–4842 (2010).
Debnath, P., Mondal, A., Hajra, A., Das, C. & Mondal, N. K. Cytogenetic effects of silver and gold nanoparticles on Allium cepa roots. Journal of Genetic Engineering and Biotechnology 16, 519–526 (2018).
The author P.M.G. is grateful for financial support from the DST-SERB, Govt. of India in the form of National Post-Doctoral Fellowship (FILE NO.PDF/2016/002124).
The authors declare no competing interests.
Publisher’s note: Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.
About this article
Cite this article
Gopinath, P.M., Saranya, V., Vijayakumar, S. et al. Assessment on interactive prospectives of nanoplastics with plasma proteins and the toxicological impacts of virgin, coronated and environmentally released-nanoplastics. Sci Rep 9, 8860 (2019). https://doi.org/10.1038/s41598-019-45139-6
Particle and Fibre Toxicology (2022)
Differential aggregation of polystyrene and titanium dioxide nanoparticles under various salinity conditions and against multiple proteins types
Environmental Science and Pollution Research (2022)
To Waste or Not to Waste: Questioning Potential Health Risks of Micro- and Nanoplastics with a Focus on Their Ingestion and Potential Carcinogenicity
Exposure and Health (2022)
Prospects on the nano-plastic particles internalization and induction of cellular response in human keratinocytes
Particle and Fibre Toxicology (2021)
Combining microcavity size selection with Raman microscopy for the characterization of Nanoplastics in complex matrices
Scientific Reports (2021)