Anthropogenic microparticles in the emerald rockcod Trematomus bernacchii (Nototheniidae) from the Antarctic

Jul 23, 2023

Scientific Reports volume 12, Article number: 17214 (2022) Cite this article

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Anthropogenic microparticles (AMs) were found for the first time in specimens of Trematomus bernacchii collected in 1998 in the Ross Sea (Antarctica) and stored in the Antarctic Environmental Specimen Bank. Most of the identified AMs were fibers of natural and synthetic origin. The natural AMs were cellulosic, the synthetic ones were polyester, polypropylene, polypropylene/polyester, and cellulose acetate. The presence of dyes in the natural AMs indicates their anthropogenic origin. Five industrial dyes were identified by Raman spectroscopy with Indigo occurring in most of them (55%). Our research not only adds further data to the ongoing knowledge of pollution levels in the Antarctic ecosystem, it provides an interesting snapshot of the past, highlighting that microplastics and anthropogenic fiber pollution had already entered the Antarctic marine food web at the end of the ‘90 s. These findings therefore establish the foundations for understand the changes in marine litter pollution over time.

In the last half-century, one of the most ubiquitous and long-lasting change on the surface of our planet's oceans is the accumulation and fragmentation of plastic1. Microplastics (MPs) are plastic particles smaller than 5 mm, manufactured as small particles or originated from the fragmentation of larger plastic items2. MPs pollution is widespread all over the world and across global ocean ecosystems, from the tropics to the poles, including the Southern Ocean3,4. Despite their ubiquitous presence, there are relatively few reports of MPs in polar regions and particularly in the Southern Ocean5.

The Antarctic continent and the surrounding waters have been affected by human activity for approximately two centuries6. In most parts of the continent the effects of the scientific activities, fishing and tourism resulted in different types of pollution, including plastic pollution7. Moreover, terrestrial and marine habitats adjacent to current or abandoned Antarctic scientific bases are affected by localized contamination8.

The oldest reports on the plastic litter occurrence in Antarctic waters and birds date back to the 80s9,10. The first records of MP ingestion by seabirds were from the Southern Ocean, when prions Pachyptila spp. were found to contain plastic in 196011. Subsequent studies carried out after twenty years on sea ice (2009) have highlighted the presence of 14 different polymers, mainly polyethylene (PE), polypropylene (PP), and polyamide (PA)12 (Table 1). Some studies, carried out between 2010 and 2017, reported the presence of plastic polymers also in seawater and sediments, as summarized in Table 1.

Recent studies showed that Antarctic krill can carry out a biological fragmentation of polystyrene (PS) microspheres into nanoplastics (NPs, < 1 µm)13,14 and this may be related to the spreading of MPs and NPs in marine ecosystems and the potential repercussion on Antarctic food chains15.

Bivalves and gastropods displayed the highest MPs contamination among the Antarctic benthic invertebrates, comparable to the values reported for other less remote areas16. MPs ingestion was also highlighted in pelagic amphipods living in Antarctic surface waters17 (Table 2).

Recent articles reported the MPs presence (PE, PP, PA, polytetrafluoroethylene (PFTE), polyacrylonitrile (PAN), and nylon), in scats of various penguin species, including Pygoscelis papua, P. adeliae, P. antarcticus, and Aptenodytes patagonicus18,19,20.

The area south of 60 S latitude is governed by the Antarctic Treaty System (ATS) and, for the environmental issues, by the Protocol on Environmental Protection to the Antarctic Treaty, which entered into force in 1991. This protocol contains specific annexes on Waste Disposal and Waste Management (Annex III), and on the Prevention of Marine Pollution (Annex IV). Moreover, the Antarctic area is considered as a "Special Area", and under the IMO-MARPOL Convention for the Prevention of Pollution from Ships21; according to the Annex V, the deliberate release of plastic wastes from ships (such as plastic ropes, fishing nets and plastic bags) and other waste is forbidden. Due to the increasing evidence of plastic pollution in Antarctica, the Scientific Committee on Antarctic Research (SCAR) recently designed an action group on plastic pollution in the Southern Ocean22, and, in 2019, the Antarctic Treaty System adopted the resolution "Reducing Plastic Pollution in Antarctica and the Southern Ocean". This document recommends to eliminate plastics personal care products, to identify and exchange information to reduce MPs release from wastewater systems, to support the plastic pollution monitoring in Antarctica and, finally, to insert the MPs issue in the Annexes III and IV to the Protocol on Environmental Protection to the Antarctic Treaty.

Despite the significant efforts to monitor and assess the levels of plastic pollution around Antarctica, the extent, quantity and impacts of MPs in the marine environment of this special area remain largely unknown. Studies on the state of the marine pollution in the Antarctic continent at the dawn of this phenomenon are scarce and it would thus be crucial to shed light on its origin and changes over the decades. Very recently, a study on Antarctic snow revealed the presence of microplastics pollution linked to the work of researchers at the Antarctic Mc Murdo Station23.

The emerald rockcod Trematomus bernacchii (Boulenger, 1902), also known as the emerald notothen, is a marine fish species belonging to Nototheniidae family, and it is a very common teleost in the shallow waters of the High-Antarctic Zone24. It is native to the Southern Ocean where it is a commercially important species25. T. bernacchii lives in very shallow waters down to 700 m depth and it is adapted to living at extremely low temperature. It is a generalized feeder with a wide niche breadth composed almost exclusively of benthic organisms (mainly infaunal and epifaunal polychaetes, amphipods, and molluscs) and small fishes. T. bernacchii may be considered an opportunist feeder as it changes its usual feeding habits to exploit different food resources that are seasonally abundant (zooplankton)26. Notothenioids, as T. bernacchii, play a key role in the high-Antarctic food web of the Ross Sea representing the link between upper and lower trophic levels contributing to the dynamics and stability of the marine system27.

In this work, the presence and composition of anthropogenic microparticles (hereafter AMs) in the emerald rockcod were investigated, with the aim to evaluate if this kind of pollution already existed many decades ago. This was possible because specimens of T. bernacchii have been systematically collected since the late 90 s in the context of the Antarctic Environmental Specimen Bank28 (BCAA) and the Italian National Antarctic Museum (MNA) activities, and then properly stored to preserve their integrity. So, specimens of T. bernacchii collected from the Antarctic coastal environment of Terra Nova Bay (Ross Sea, Antarctica) in 1998 (the oldest available samples stored in the BCAA) provided an interesting snapshot of the MPs pollution in that time. In this study, the micro-Raman spectroscopy has been used to identify the chemical composition of the microparticles since it is among the most powerful techniques to detect and identify marine microparticles and associated chemical anthropogenic additives, as well as to differentiate between natural and synthetic particles29,30,31.

The study involved eight adult specimens of T. bernacchii; the length ranged from 215 to 275 mm, and the weight from 165 to 319 g (Table 3). Six specimens were positive for AMs (75%), a total of 37 particles (size range 0.4–4.2 mm) were detected in the GITs, mainly belonging to large AMs (63%; size range 1.1–4.2 mm) and small AMs (37%; size range 0.4–0.9 mm).

Of them, 35 (95%) were fibers and 2 (5%) were fragments. No plastic pellets, foams or spheres were found. Blue particles were the most abundant (32%), followed by white/transparent (27%) black (24%), red (8%), green (3%), violet (3%), and yellow (3%) (Fig. 1).

Selected set of anthropogenic microparticles (AMs) isolated from the gastrointestinal tract (GIT) of Trematomus bernacchii samples caught in 1998 in Antarctica (Terra Nova Bay, Ross Sea) and provided by the Antarctic Environmental Specimen Bank. AMs have been identified analyzing the spectra measured by means of micro-Raman spectroscopy (panels A.1, B.1, C.1, D.1), after image acquisition with an optical stereomicroscope (4x, Leica M205C; panels A.2, B.2, C.2, D.2, scale ratio for panel B.2 and D.2 as in panel A.2) and a Raman confocal microscopy (50\(\times\), Olympus BX41; panels (A.3, B.3, C.3, D.3), scale ratio for all panels indicated in panel (A.3). The 50 × magnification allows us to appreciate: the rigid-rod fiber of polyester (B.3); the texture of the cotton fabric (C.3); the flat and slightly twisted ribbons of cellulosic fibers (D.3). Bottom panels: Distribution percentage of colour (%) (panel E), composition (panel F) and dye type (panel G), for all the identified AMs ingested by Trematomus bernacchii.

The identified microparticles (n = 20; 57%) were of natural and synthetic origin, on the base of identified AMs, the abundance value was equal to 3.3 items/specimen; while fifteen microparticles were not identified because fluorescence overshadowed their Raman signal.

The finding of AMs in the GITs of T. bernacchii may be related to its feeding habits and its strong relationship with the seafloor as also suggested for other benthic fish32,33,34. Several studies in the Mediterranean Sea have found non-plastic fibres, mainly cellulose-based, in different benthivorous species35,36. AMs may be accidentally ingested during feeding activity or by secondary ingestion. T. bernacchii is a generalized predator37 with a wide array of dietary items26 and it can be also considered as opportunistic feeder, undertaking occasional vertical migrations to forage on locally and seasonally abundant planktonic prey26. In the light of this, T. bernacchii may also ingest the AMs along the water column.

Since this study is the first investigation carried out on Antarctic fish species, we could only make comparisons with recent studies on seawater, sediment and benthic organisms from the same study area.

Microfibers were the most frequent microparticles in sediments close to the Italian "Mario Zucchelli" Station (MZS)38 and in the waters close to the sewage treatment plant of MZS39, as well as in penguins of other Antarctic areas18,20.

Fish can act as an indirect source of microfiber contamination for marine predators as for seals40 and penguins of sub-Antarctic areas19 (21.9 items/g of scat).

The identified microparticles of natural origin were cellulosic (n = 14; 70%). One of the fragments showed the typical texture of the fabric (see Fig. 1, panel C.3). Cotton was the most abundant item (45%) followed by cellulose (18%). Mostly cellulosic microfibers have been found to be dyed, thus confirming their manufactured (anthropogenic) origin.

Among all microfibers examined, the industrial dye was identified by Raman spectroscopy in 11 items: Indigo, Cromophtal Violet B, Drimaren Navy Bue R-2RL, Vine black dye, and Sirius light green, with Indigo occurring in most of them (55%). The Raman spectra of selected identified items are shown in Fig. 1.

In accordance with our results, most of fibres (~ 88%) found in King Penguins scats of the South Georgia were made of natural cellulosic materials (cotton, linen), with only a few synthetic fibres19 (PES, PP, and acrylic).

Textiles are the main microfibers environmental source41,42. The synthetic textiles are responsible for the discharge of about 0.5 million tonnes of MPs into the sea each year43.

Man-made cellulose fibers associated with dyes or additives could be potentially harmful to marine organism35,44,45, in fact the industrial dyes are used in the industry with several polymers such as cellulose fibers. In particular, the indigo is used to dye cellulosic fibers of blue jeans the world's most popular garment46. The presence of Indigo-dyed microfibers has been recently, documented in the marine ecosystems47. The "blue jeans" microfibers has been proposed as an indicator of the widespread burden of anthropogenic pollution from temperate to Arctic regions48. Moreover, the textile dyes, are very toxic and are related to the environmental degradation49.

The textile dyes may compromise the aestethic quality of water bodies, increase biochemical and chemical oxygen demand (BOD and COD), alter photosynthesis, and reduce plant growth43. Textile dyes may enter the food chain43, bioaccumulate, biomagnificate50, promote toxicity, mutagenicity, and carcinogenicity 51,52,53,54.

In their very recent review on 202255 Athey and Erdle suggested that the abundance of natural and semisynthetic microfibers in the marine biota may be underestimated55. They enumerate different possible causes for this under-evaluation, the methods used to isolate microfibers are designed for the recovery and identification of synthetic materials. Some chemicals, used to isolate synthetic microfibers, may cause the degradation of non-synthetic fibers; several studies exclude natural and semisynthetic microparticles from their analyses4 with the assumption that non-plastic fibers are readily biodegradable or non-dangerous for the marine biota56. Athey and Erdle also point out that, although natural fibers can degrade faster than synthetic polymers, these fibers can persist in the marine environment for decades in relation to the nature of the fiber and environmental factors55. Moreover, the degradation of natural and semisynthetic fibers involves release of toxics adsorbed to the surface into the environment56. Industrial textile dyes may also protract the microfibers persistence in the environment55. We suggest that more attention has to be paid for the experimental detection of dyes in natural fibers, since dyes are indicators of anthropogenic processing and potential causes of biological damage. The effect of natural and semisynthetic microfibers on the marine biota is under studied and deserves particular attention, especially from the polar research community.

The synthetic microparticles reported in this study were polyester (PES; 3), polypropylene (PP; 1) polypropylene/polyester (1) and cellulose acetate (1) (Fig. 1).

PES and PP were also the main polymers found in seawater next to the sewage treatment plant at MZS39. PP has been also found in sediments of the Ross Sea38, as well as in seawater, sediment and sea ice in other Antarctic areas (Table 1). In accordance with our data, one the most common polymers in penguins of Antarctic Peninsula and Scotia Sea region was PP20 (Table 2). Fish can act as indirect source of microplastic contamination when preyed by other organisms. The main risks are linked not only to the spread of MPs along the food chain that reaches humans, but above all to the release of dangerous xenobiotics adhered to the MPs57.

Currently 76 scientific research stations are located below 60° S belonging to 29 nations; 31% are permanent stations whereas 69% of the stations are active only during summer.

The wastewater treatment plants are present only in half of research stations (48%). This is the case of the MZS, which is open from mid-October to mid-February. However, conventional wastewater treatment, including tertiary treatment techniques, may remove about 90% of MPs58, and this situation may be exacerbated in remote areas where operational difficulties may reduce treatment efficiency59. The non-retained MPs can be released in a largely unaltered state, into the nearshore marine environment having passed through facilities. In the same way, textile dyes are not easily removed by conventional wastewater treatment processes due to their intrinsic properties60 (i.e. stability and resistance towards light or oxidizing agents). Based on a very recent study on snow fallen in Antarctica, microplastics and anthropogenic fiber contamination can be related to the Antarctic research stations, and originate from the polar clothing and equipment23.

This paper provides a snapshot from the past on the AMs ingestion by specimens of emerald rockcod collected 24 years ago, representing the first evidence of this phenomenon in an Antarctic fish.

Moreover, this finding will be useful to compare the past pollution level with the current situation, by analyzing of gastrointestinal tract of Trematomus bernacchii caught during the last Antarctic survey (XXXVII expedition – 2021/2022). This comparison will allow to understand the changes in marine litter pollution over time, especially in the Antarctic ecosystem, with its peculiar environmental features and fragility, worthy to be protected and preserved.

This study further stresses the importance of anthropogenic microparticles and textile dyes monitoring in Antarctica and, hopefully, it will help current policy measures on plastic pollution under the Antarctic Treaty to improve surveillance and promote mitigation actions. In the future, a connection network to retrieve older samples in monitoring pollution changes over time is strongly desirable.

The study area was located in Gerlache Inlet (74° 41′ S; 164° 6′ E), a 7-km wide inlet in the northwest corner of Terra Nova Bay (Ross Sea), a coastal marine area encompassing 29.4 km2 between Cape Washington and the Drygalski Ice Tongue (Fig. 2).

Study area (Terranova Bay, Ross Sea). Map was created using Google Earth (https://earth.google.com/web/@74.6953791,164.0961781,0.4171455a,2467.23579724d,30.00002056y,0h,0t,0r) on which sampling sites and wastewater treatment plant discharge were indicated.

This site is an important littoral area for long-term scientific investigations, and it has been proposed as an Antarctic Specially Protected Area (ASPA) by Italy, in 2003. Samplings were carried out on February 1998 in two sites: B5 (74° 41′ 60′′ S, 164° 07′ 00′′ E) and B806 (74° 43′ 025'' S, 164° 08′ 648'' E). B5 and B806 are 3.8 and 7 km from the wastewater outfall, respectively (Fig. 2). The specimens were caught by trammel net, immediately frozen, sent to Italy at the end of the expedition, and finally stored at the Antarctic Environmental Specimen Bank. The samples were kept at -20 °C from the sampling to the analysis, performed in June 2021.

Each specimen was slowly thawed at 4 °C overnight, and then GITs, from the oesophagus to the end of the intestine, were removed and stored in a glass Petri dish. Each GIT, was weighted and under a microbiological hood, placed in conical glass flask and treated with 10% K-OH solution, in a ratio of 1: 5 (w/v). The flask was stirred at 50 °C for 48 h. Then each sample was placed in a glass cylinder adding hypersaline 15% NaCl solution to obtain density separation of the two phases. The supernatant was collected in a glass beaker, and filtered through a fiberglass filters (1.6 μm Whatman GF/F, UK) using a vacuum system (Millipore). After filtration procedures, the membranes were placed in sterile Petri glass dishes for subsequent observations under the stereomicroscope (Leica M205C) to isolate the plastic debris61. All particles were visually identified, counted, measured, and photographed. All items were classified based on their size (small-microparticle: 0.1–1 mm; large-microparticle: 1–5 mm; meso: 5–25 mm; macro: > 25 mm), shape (pellet, fiber, foam, fragment, sheet and sphere) and colour according to the protocol of the Marine Strategy Framework Directive62.

The anthropogenic items found in the GITs were expressed as number of identified AMs per specimens. All items isolated from each fish specimen was assayed for the characterization.

To avoid airborne contamination during laboratory analysis, workspaces and tools were rigorously cleaned from any particle contamination, following succeeding protocol63, the samples were processed in a room with restricted access, to prevent any accidental external contamination, and all the operations were performed under a microbiological hood. All materials used for the dissection, the extraction and analysis steps were thoroughly cleaned with ethanol and filtered deionized water. Glassware was used and all instruments and equipment (including tweezers and scissors) were rinsed thoroughly with ultrapure water. Additionally, operators wore cotton coats. The beakers were covered with aluminium foil between each step to prevent airborne contamination. Procedural blanks were also run concurrently to avoid fibers overestimation, moist filters in Petri dishes were put under the microbiological hood and exposed to the laboratory air near the stereomicroscope64. Procedural blanks without tissue were also run concurrently with samples. One procedural blank every two samples was performed. The procedural blank samples were free of any AM contamination.

All particles isolated from the GITs were assessed with by Raman micro-spectroscopy. A preliminary analysis of the Raman results was aimed at identifying and grouping the similar spectra. Subsequently, the molecular identification of the component of the AMs was accomplished by comparing the Raman spectra with those available in libraries.

Micro-Raman spectroscopy was used to identify the polymer compositions of the AMs. Fibers showing branching or changed thickness along their length were rejected, both features being evidence for a biological origin (root or plant fibers).

Raman spectra of micro fibers and particles were taken in a backscattering geometry on a HR Evolution micro confocal Raman system (Horiba Scientific) using a green-light-emitting diode laser (λ = 532 nm), a × 100 (NA = 0,90) or a × 50 objective (NA = 0.45), an 1800 g/mm grating and a 77 K—cooled charged couple device detector. To avoid sample photodegradation, the laser power was maintained below 5 mW using a lower percent transmission filter. Spectra were collected in the range of 200–4000 cm-1, while the duration of laser exposure and the number of spectra accumulations were varied in the range 5–20 s and 2–20, respectively, depending on the specific dye in the MP. Analysis was performed at different points on the same MP to confirm identification. To remove background interference due to fluorescence, fluorescent samples data were corrected by the Flat correction routine of the LabSpec6. Furthermore, besides FLAT correction, baseline correction was applied prior to the spectral analysis. The spectra were identified by comparing them to those of standard materials catalogued in the spectral databases of the Bio-Rad KnowItAll Spectral Library and the Spectral Library of Plastic Particles (SLoPP and SLoPP-E). A Hit Quality Index (HQI) value of 80% or greater has been accepted as true math.

The authors declare that they have obtained permission for the use of Antarctic fish samples for research purposes from the Italian National Antarctic Museum (MNA) and from the Bank of Antarctic Environmental Samples (BCAA) of Genoa.

The datasets used and/or analysed during the current study available from the corresponding author on reasonable request.

Barnes, D. K. A., Galgani, F., Thompson, R. C. & Barlaz, M. Accumulation and fragmentation of plastic debris in global environments. Philos. Trans. R. Soc. Lond. B Biol. Sci. 364, 1526 (2009).

Article Google Scholar

Cole, M., Lindeque, P., Halsband, C. & Galloway, T. S. Microplastics as contaminants in the marine environment: A review. Mar. Pollut. Bull. 62, 2588–2597 (2011).

Article CAS PubMed Google Scholar

Waller, C. L. et al. Microplastics in the Antarctic marine system: An emerging area of research. Sci. Total Environ. 598, 220–227 (2017).

Article ADS CAS PubMed Google Scholar

Fang, C. et al. Microplastic contamination in benthic organisms from the Arctic and sub-Arctic regions. Chemosphere 209, 298–306 (2018).

Article ADS CAS PubMed Google Scholar

Suaria, G. et al. Floating macro- and microplastics around the Southern Ocean: Results from the Antarctic Circumnavigation Expedition. Environ. Int. 136, 105494 (2020).

Article PubMed Google Scholar

Stark, J.S., Raymond, T., Deppeler, S.L. & Morrison, A.K. Antarctic Seas in World Seas: An Environmental Evaluation (ed. Sheppard, C.) 44 (Academic Press 2019).

Mishra, A. K., Singh, J. & Mishra, P. P. Microplastics in Polar Regions: An early warning to the world's pristine ecosystem. Sci. Total Environ. 784, 147149 (2021).

Article ADS CAS PubMed Google Scholar

Bargagli, R. Environmental contamination in Antarctic ecosystems. Sci. Total Environ. 400, 212–226 (2008).

Article ADS CAS PubMed Google Scholar

Gregory, M. R., Kirk, R. M. & Mabin, M. C. G. Pelagic tar, oil, plastics and other litter in surface waters of the New Zealand sector of the Southern Ocean, and on Ross Dependancy shores. N. Z. Antarct. Rec. 6, 12–26 (1984).

Google Scholar

Van Franeker, J. A. & Bell, P. J. Plastic Ingestion by Petrels Breeding in Antarctica. Mar. Poll. Bull. 19(12), 672–674 (1988).

Article Google Scholar

Harper, P. C. & Fowler, J. A. Plastics pellets in New Zeland storm-killed prions (Pachyptila spp) 1958–1977. Notornis 34, 65–70 (1987).

Google Scholar

Kelly, A. et al. Microplastic contamination in east Antarctic sea ice. Mar. Poll. Bull. 154, 111130 (2020).

Article CAS Google Scholar

Gigault, J. et al. Current opinion: What is a nanoplastic?. Environ. Pollut. 235, 1030–1034 (2018).

Article CAS PubMed Google Scholar

Dawson, A. et al. Turning microplastics into nanoplastics through digestive fragmentation by Antarctic krill. Nat. Commun. 9, 1001 (2018).

Article ADS PubMed PubMed Central Google Scholar

Bergami, E. et al. Plastics everywhere: First evidence of polystyrene fragments inside the common Antarctic collembolan Cryptopygus antarcticus. Biol. Lett. 16, 20200093 (2020).

Article CAS PubMed PubMed Central Google Scholar

Sfriso, A. A. et al. Microplastic accumulation in benthic invertebrates in Terra Nova Bay (Ross Sea, Antarctica). Environ. Int. 137, 105587 (2020).

Article CAS PubMed Google Scholar

Jones-Williams, K. et al. Close encounters—microplastic availability to pelagic amphipods in sub-Antarctic and Antarctic surface waters. Environ. Int. 140, 105792 (2020).

Article CAS PubMed Google Scholar

Bessa, F. et al. Microplastics in gentoo penguins from the Antarctic region. Sci Rep 9, 14191 (2019).

Article ADS PubMed PubMed Central Google Scholar

Le Guen, C. et al. Microplastic study reveals the presence of natural and synthetic fibres in the diet of King Penguins (Aptenodytes patagonicus) foraging from South Georgia. Environ. Int. 134, 105303 (2020).

Article PubMed Google Scholar

Fragão, J. et al. Microplastics and other anthropogenic particles in Antarctica: Using penguins as biological samplers. Sci. Total Environ. 20, 788 (2021).

Google Scholar

International Maritime Organization (IMO), Resolution A. 1087 (28): Guidelines for the Designation of Special Areas under MARPOL, in Assembly, 28th Session, Agenda Item 12, (2013).

Waller, C. L. & Hughes, K. A. Plastics in the Southern Ocean. Antarct. 30, 269 (2018).

Article Google Scholar

Aves, A. R. First evidence of microplastics in Antarctic snow et al. First evidence of microplastics in Antarctic snow. Cryosphere 16, 2127–2145 (2022).

Article ADS Google Scholar

Vacchi, M., La Mesa, M. & Castelli, A. Diet of two coastal nototheniid fish from Terra Nova Bay, Ross Sea. Antarct. 6, 61–65 (1994).

Article Google Scholar

Froese, R., & Pauly D. (eds) FishBase. World Wide Web electronic publication—FishBase (September, 2022).

La Mesa, M., Dalù, E. M. & Vacchi, M. Trophic ecology of the emerald notothen Trematomus bernacchii (Pisces, Nototheniidae) from Terra Nova Bay, Ross Sea, Antarctica. Polar Biol. 27, 721–728 (2004).

Article Google Scholar

Lamesa, M., Eastman, J. T. & Vacchi, M. The role of notothenioid fish in the food web of the Ross Sea shelf waters: A review. Polar Biol. 27, 321–338. https://doi.org/10.1007/s00300-004-0599-z (2004).

Article Google Scholar

Soggia, F., Ianni, C., Magi, E. & Frache, R. Antarctic environmental Specimen Bank in Environmental Contamination in Antarctica, a Challenge to Analytical Chemistry (ed. Caroli, S., Cescon, P., Walton, B.T.) 305–325 (Elsevier, 2001).

Anger, P. M. et al. Raman microspectroscopy as a tool for microplastic particle analysis. TrAC Trends Analyt. Chem. 109, 214–226 (2018).

Article CAS Google Scholar

Savoca, S. et al. Microplastics occurrence in the Tyrrhenian waters and in the gastrointestinal tract of two congener species of seabreams. Environ. Toxicol. Pharmacol. 67, 35–41 (2019).

Article CAS PubMed Google Scholar

Capillo, G. et al. Quali-quantitative analysis of plastics and synthetic microfibers found in demersal species from Southern Tyrrhenian Sea (Central Mediterranean). Mar. Poll. Bull. 150, 110596 (2020).

Article CAS Google Scholar

Bottari, T. et al. Plastics occurrence in the gastrointestinal tract of Zeus faber and Lepidopus caudatus from the Tyrrhenian Sea. Mar. Poll. Bull. 146, 408–416 (2019).

Article CAS Google Scholar

Filgueiras, A. V., Preciado, I., Cartón, A. & Gago, J. Microplastic ingestion by pelagic and benthic fish and diet composition: A case study in the NW Iberian shelf. Mar. Poll. Bull. 160, 111623 (2020).

Article CAS Google Scholar

Mancuso, M. et al. Investigating the effects of microplastic ingestion in Scyliorhinus canicula from the South of Sicily. Sci. Total Environ. 850, 157875 (2022).

Article ADS Google Scholar

Savoca, S. et al. Ingestion of plastic and non-plastic microfibers by farmed gilthead sea bream (Sparus aurata) and common carp (Cyprinus carpio) at different life stages. Sci. Total Environ. 782, 146851 (2021).

Article ADS CAS Google Scholar

Rodrìguez-Romeu, O. et al. Are anthropogenic fibres a real problem for red mullets (Mullus barbatus) from the NW Mediterranean?. Sci. Total Environ. 733, 139336 (2020).

Article ADS PubMed Google Scholar

Bansode, M. A., Eastman, J. T. & Aronson, R. B. Feeding biomechanics of five demersal Antarctic fishes. Polar Biol. 37, 1835–1848. https://doi.org/10.1007/s00300-014-1565-z (2014).

Article Google Scholar

Munari, C. et al. Microplastics in the sediments of Terra Nova Bay (Ross Sea, Antarctica). Mar. Poll. Bull. 122, 161–165 (2017).

Article CAS Google Scholar

Cincinelli, A. et al. Microplastic in the surface waters of the Ross Sea (Antarctica): Occurrence, distribution and characterization by FTIR. Chemosphere 175, 391–400 (2017).

Article ADS CAS PubMed Google Scholar

Eriksson, C. & Burton, H. Origins and biological accumulation of small plastic particles in fur seals from Macquarie Island. Ambio 32, 380–384 (2003).

Article PubMed Google Scholar

Carr, S. A. Sources and dispersive modes of micro-fibers in the environment. Integr. Environ. Assess. Manag 13(3), 466–469 (2017).

Article CAS PubMed Google Scholar

Gavigan, J. et al. Synthetic microfiber emissions to land rival those to waterbodies and are growing. PLoS ONE 15(9), e0237839 (2020).

Article CAS PubMed PubMed Central Google Scholar

Manshoven, E. et al. Microplastic pollution from textile consumption in Europe. Eionet Report - ETC/CE 2022/1 (2022).

Remy, F. et al. When microplastic is not plastic: The ingestion of artificial cellulose fibers by macrofauna living in seagrass macrophytodetritus. Environ. Sci. Technol. 49, 11158–11166 (2015).

Article ADS CAS PubMed Google Scholar

Savoca, S. et al. Detection of anthropogenic cellulose microfibers in Boops boops from the northern coasts of Sicily (Central Mediterranean). Sci. Total Environ. 691, 455–465 (2019).

Article ADS CAS PubMed Google Scholar

Raina, M.A., Gloy, Y.S. & Gries, T. Weaving technologies for manufacturing denim in Denim. Woodhead Publishing Series in Textiles (ed. Paul, R.) 159–187 (2015).

Lots, F. A. E. et al. A Large-Scale Investigation of Microplastic Contamination: Abundance and Characteristics of Microplastics in European Beach Sediment. Mar. Pollut. Bull. 123, 219–226 (2017).

Article CAS PubMed Google Scholar

Athey, S. N. et al. The Widespread Environmental Footprint of Indigo Denim Microfibers from Blue Jeans. Environ. Sci. Technol. Lett. 7, 840–847 (2020).

Article CAS Google Scholar

Lellis, B. et al. Effects of textile dyes on health and the environment and bioremediation potential of living organisms. Biotech. Res. Inn. 3, 275–290 (2019).

Article Google Scholar

Sandhya, S. Biodegradation of azodyes under anaerobic condition: Role of azoreductase Biodegradation of azo dyes. The handbook of environmental chemistry (ed. Erkurt ,H.A.) 9, 39–57 (Springer, 2010).

Oehlmann, J.R. et al. A critical analysis of the biological impacts of plasticizers on wildlife. Philos. Trans. R. Soc. Lond. B Biol. Sci. 364 (1526), 2047e2062 (2009).

Aquino, J. M. et al. Electrochemical degradation of a real textile wastewater using β-PbO2 and DSA® anodes. Chem. Eng. J. 251, 138–145 (2014).

Article CAS Google Scholar

Newman, M. C. Fundamentals of Ecotoxicology: The Science of Pollution (CRC Press, 2015).

Google Scholar

Khatri, J., Nidheesh, P. V., Singh, T. A. & Kumar, M. S. Advanced oxidation processes based on zero-valent aluminium for treating textile wastewater. Chem. Eng. J. 348, 67–73 (2018).

Article CAS Google Scholar

Athey, S. N. & Erdle, L. M. Are we underestimating anthropogenic microfiber pollution? A critical review of occurrence, methods, and reporting. Environ. Tox. Chem. 41, 822–837 (2022).

Article CAS Google Scholar

Stone, C., Windsor, F. M., Munday, M. & Durance, I. Natural or synthetic – how global trends in textile usage threaten freshwater environments. Sci. Total Environ. 718, 134689 (2020).

Article ADS CAS PubMed Google Scholar

Wright, S. L. & Kelly, F. J. Plastic and human health: A micro issue?. Environ. Sci. Technol. 51, 6634–6647 (2017).

Article ADS CAS PubMed Google Scholar

Ziajahromi, S., Neale, P. A. & Leusch, F. D. Wastewater treatment plant effluent as a source of microplastics: Review of the fate, chemical interactions and potential risks to aquatic organisms. Water Sci. Technol. 74(10), 2253–2269 (2016).

Article CAS PubMed Google Scholar

Aronson, R. B., Thatje, S., McClintock, J. B. & Hughes, K. A. Anthropogenic impacts on marine ecosystems in Antarctica. Ann. N. Y. Acad. Sci. 1223, 82–1072011 (2011).

Article ADS PubMed Google Scholar

Hynes, N. R. J. et al. Modern enabling techniques and adsorbents based dye removal with sustainability concerns in textile industrial sector - A comprehensive review. J. Clean. Prod. 272, 122636 (2020).

Article CAS Google Scholar

Savoca, S. et al. Plastics occurrence in juveniles of Engraulis encrasicolus and Sardina pilchardus in the Southern Tyrrhenian Sea. Sci Total Environ. 718, 137457 (2020).

Article ADS CAS PubMed Google Scholar

Galgani, F., Hanke, G., Werner, S. D. V. L. & De Vrees, L. Marine litter within the European marine strategy framework directive. Ices J. Mar. Sci. 70, 1055–1064 (2013).

Article Google Scholar

Bottari, T. et al. Microplastics in the bogue, Boops boops: A snapshot of the past from the southern Tyrrhenian Sea. J. Hazardous Mat. 424(15), 127669 (2022).

Article CAS Google Scholar

Pedà, C. et al. Coupling gastro-intestinal tract analysis with an airborne contamination control method to estimate litter ingestion in demersal elasmobranchs. Front. Environ. Sci. 8, 119 (2020).

Article Google Scholar

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The authors would like to thank the Italian National Antarctic Museum (MNA) and the Antarctic Environmental Specimen Bank (BCAA) of Genoa (Italy) for having kindly provided Trematomus bernacchii specimens used in this study.

Institute for Marine Biological Resources and Biotechnology (IRBIM) – CNR, Messina, Italy

Teresa Bottari, Serena Savoca, Nunziacarla Spanò & Monique Mancuso

Department of Integrative Marine Ecology (EMI), Stazione Zoologica Anton Dohrn - National Institute of Biology, Ecology and Marine Biotechnology, Sicily Marine Centre, Messina, Italy

Teresa Bottari, Teresa Romeo & Monique Mancuso

Department of Mathematical and Computational Sciences, Physical Science and Earth Science, University of Messina, Messina, Italy

Valeria Conti Nibali, Caterina Branca & Giovanna D’Angelo

Department of Chemistry and Industrial Chemistry (DCCI), University of Genoa, Genoa, Italy

Marco Grotti

Department of Biomedical, Dental, and Morphological and Functional Imaging, University of Messina, Messina, Italy

Serena Savoca & Nunziacarla Spanò

Institute for Environmental Protection and Research (ISPRA), Milazzo, ME, Italy

Teresa Romeo

Institute of Polar Sciences (ISP) – CNR, Messina, Italy

Maurizio Azzaro

Research Infrastructures for Marine Biological Resources Department (RIMAR), Stazione Zoologica Anton Dohrn, National Institute of Biology, Ecology and Marine Biotechnology, Calabrian Researches Centre and Marine Advanced Infrastructures (CRIMAC), Amendolara, CS, Italy

Silvestro Greco

Institute for Chemical-Physical Processes, National Research Council of Italy (IPCF-CNR), Messina, Italy

Giovanna D’Angelo

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T.B. contributed by writing the original draft, reviewing and supervising. V.C.N. contributed by doing the formal analysis, curating data, and writing. C.B., M.G., S.S., T.R., N.S., M.A. and S.G. contributed reviewing and editing. G.D. contributed to do the formal analysis, data and writing curation, supervision. M.M. contributed by the project administration, conceptualization, formal analysis, writing and supervision. All authors provided approval for publication of the content and contributed drafting the work and critically revisiting the manuscript.

Correspondence to Giovanna D’Angelo or Monique Mancuso.

The authors declare no competing interests.

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Bottari, T., Nibali, V.C., Branca, C. et al. Anthropogenic microparticles in the emerald rockcod Trematomus bernacchii (Nototheniidae) from the Antarctic. Sci Rep 12, 17214 (2022). https://doi.org/10.1038/s41598-022-21670-x

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Received: 04 July 2022

Accepted: 29 September 2022

Published: 14 October 2022

DOI: https://doi.org/10.1038/s41598-022-21670-x

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