The Mediterranean Sea has been recently proposed as one of the most impacted regions of the world with regards to microplastics, however the polymeric composition of these floating particles is still largely unknown. Here we present the results of a large-scale survey of neustonic micro- and meso-plastics floating in Mediterranean waters, providing the first extensive characterization of their chemical identity as well as detailed information on their abundance and geographical distribution. All particles >700 μm collected in our samples were identified through FT-IR analysis (n = 4050 particles), shedding for the first time light on the polymeric diversity of this emerging pollutant. Sixteen different classes of synthetic materials were identified. Low-density polymers such as polyethylene and polypropylene were the most abundant compounds, followed by polyamides, plastic-based paints, polyvinyl chloride, polystyrene and polyvinyl alcohol. Less frequent polymers included polyethylene terephthalate, polyisoprene, poly(vinyl stearate), ethylene-vinyl acetate, polyepoxide, paraffin wax and polycaprolactone, a biodegradable polyester reported for the first time floating in off-shore waters. Geographical differences in sample composition were also observed, demonstrating sub-basin scale heterogeneity in plastics distribution and likely reflecting a complex interplay between pollution sources, sinks and residence times of different polymers at sea.
Global production of plastic materials increased twenty-fold in the last fifty years, exceeding 300 million tonnes in 20151. Demand is growing exponentially and production is expected to quadruple by 2050, taking up 20% of total oil consumption and 15% of the global carbon budget2. Single-use packaging applications represent the largest share of the European plastic market, accounting for 40% of the total production1 and for more than 10% of the municipal solid waste3. As a result, 275 million tonnes of plastic litter were generated in 2010 by the world’s coastal countries, of which 4.8 to 12.7 million tonnes were estimated to have ended up in the oceans, a scenario projected to increase by an order of magnitude within 20253.
Since the first reports on the presence of plastic in the oceans, worldwide attention has been focussed to this problem and the number of scientific publications has seen an exponential growth4. Vast accumulation areas have been discovered in all main oceanic gyres5,6,7,8, and every part of the oceans examined so far, revealed the presence of marine litter, including polar seas9 and deep-sea sediments10. Plastic is now so abundant that it has been proposed as a new stratigraphic indicator of Anthropocene11.
Over 92% of all plastic items found at sea are generally smaller than 5 mm12. These tiny particles – hereinafter referred to as microplastics – may either result from the breakdown of larger objects, or they can directly enter the marine environment as granules, pellets and fibers. Microplastics can act as dispersal vectors of chemical additives, organic and metal pollutants accumulated from surrounding waters13 and provide habitats for a wide range of rafting organisms and microbial communities14. Being in the same size class of many planktonic organisms, ingestion of microplastics is widely reported and the first evidences of trophic transfer are emerging15,16. As a result, indications of negative effects at both, individual and sub-organismal levels are starting to appear, to the extent that the classification of plastic waste as hazardous was recently suggested17.
Global models consistently predict some of the highest concentrations of floating plastics in the world to occur in the Mediterranean Sea12,18, to the extent that together with the main five oceanic gyres, it has been proposed as the sixth great accumulation zone for marine litter19. Mainly owing to limited outflow of surface waters, a densely populated coastline and intensive fishing, shipping, touristic and industrial activities, substantial amounts of marine litter are accumulating in the Mediterranean basin, which according to the most recent simulations is retaining between 21% and 54% of all plastic particles (i.e. between 3.2 and 28.2 × 1012 particles) and between 5% and 10% of the global plastic mass (i.e. between 4.8 and 30.3 thousand tonnes)20.
Mediterranean biodiversity is certainly not immune from interaction with marine litter21. Artificial polymers have been found in the stomach contents of Mediterranean pelagic predators22, deep-sea fishes23 and commercial species24. Large amounts of plastic debris have been reported from the Mediterranean seafloor25 and floating on its surface26, as well as on beaches27,28 and coastal environments29,30. Studies on the abundance of floating micro-sized particles however, mostly focused on the NW part of the basin (Table 1) and the polymeric identity of such floating particles is still largely unknown.
The European Marine Strategy Framework Directive (2008/56/EC) highlighted concerns for the environmental implications of marine litter and underlined the urgent need for member countries to “Determine trends in the amount, distribution and composition of micro-particles (mainly microplastics) in European waters and to establish baseline quantities, properties and potential impacts”31. More recently, the importance of this issue has also been acknowledged by the Contracting Parties to the Barcelona Convention and by the G7 world leaders, who committed to a global action plan to combat marine litter32. Most of the surveys conducted so far however, mainly relied on the visual identification of particles, or characterized only a restricted subset of samples. Thus, detailed information on the actual polymeric diversity of these emerging pollutant is lacking.
Within this context, we present the results of a large-scale survey of micro (<5 mm) and meso-plastics (5–20 mm) occurrence in central-western Mediterranean waters, providing the largest polymeric characterization of floating microplastics ever performed (n = 4,050 particles). In agreement with numerical predictions, we confirm the Mediterranean Sea as severely contaminated by plastic pollution and describe for the first time the complex mixture of synthetic polymers floating on its surface. We tested the hypothesis that plastic distribution and composition are not homogeneous and that geographical differences exist between Mediterranean sub-basins. Such information is urgently required to identify sources and sinks of these emerging pollutants and to better understand fate and impacts of different polymers in the marine environment, so that knowledge-based reduction and prevention measures can be effectively implemented.
A total of 74 neuston samples were collected during the survey (Fig. S1). Plastic-like particles were found in all samples with a mean total abundance of 1.25 ± 1.62 particles/m2 (see Table S1 for other units of measurement). Most of these particles (93.2%) were visually classified as irregularly shaped fragments, while pellets, films and foams constituted only a small fraction of the total (2.2%, 1.6% and 3.1% respectively). Due to the high risk of external contamination, all fibers and filaments were removed from our dataset and not considered in density calculations.
The overall size-class distribution revealed a marked prevalence of smaller particles (Fig. 1). 26% of all counted particles were smaller than 300 μm and 51% were smaller than 500 μm (ntot = 14,106 particles). Only 197 items (1.4% of the total) were larger than 5 mm. The mean abundance of these meso-particles was very low (0.016 ± 0.028 particles/m2) but strongly correlated to the abundance of micro-particles (rs = 0.8, p = 3.6118E-18).
The polymeric identity of all particles >700 μm was verified through ATR FTIR (n = 4,050 particles). This subset was considered highly representative since it comprised 96.2% of the total weight of collected material. 16 different polymer typologies were identified (Fig. 2 and Fig. S3). Polyethylene (HD-PE and LD-PE) was the predominant form with an overall frequency of 52%, followed by polypropylene (PP) (16%) and synthetic paints (7.7%). Polyamides (PA) accounted for 4.7% of all characterized particles (excluding nylon which accounted alone for 1.9%), whereas polyvinyl chloride (PVC), polystyrene (PS) and polyvinyl alcohol (PVA) represented 2.6%, 2.8% and 1.2% respectively. Other less frequent polymers (<1%) included: poly(ethylene terephthalate) (PET), polyisoprene (synthetic rubber), poly(vinyl stearate) (PVS), ethylene-vinyl acetate (EVA) and cellulose acetate. Ten fragments of polycaprolactone, a biodegradable polymer, were found in seven different samples throughout the study area, while 201 fragments of epoxy resin (polyepoxide) were collected at a single location in the Balearic Sea. Similarly, several residues of paraffin wax were found exclusively in an off-shore sample in the Adriatic Sea. The molecular characterization also revealed a relatively low misidentification rate during visual sorting. Only 4.4% of all analyzed particles did not consist of plastic but were rather made of cotton, chitin, cellulose and other non-synthetic materials.
Because we could not be sure about the synthetic nature of particles <700 μm (see methods and section below), abundances were computed for two additional sub-categories, i.e. particles bigger and smaller than 700 μm, resulting in two mean concentrations of 0.40 ± 0.74 and 0.85 ± 0.95 particles/m2 respectively (Fig. S2 and Table S1). Yet, the number of particles counted in each of these two categories, exhibited a strong positive correlation (rs = 0.8233, p = 2.2163E-19), suggesting a link between size classes and slightly enhancing the level of confidence in our detection rates.
In terms of weight, the amount of particles >700 μm, whose synthetic nature was verified through FT-IR spectroscopy, showed a very high spatial heterogeneity spanning two or three orders of magnitude across the study area (Fig. 3). The maximum value (10.43 kg/km2) was observed in the Corsica Channel, between Cap Corse and Capraia island, while the two lowest concentrations were found in the southern Adriatic Sea. Overall, plastic was significantly (p = 0.002) less abundant in the Adriatic Sea (467.79 ± 1133.88 g/km2; n = 30) than in western Mediterranean samples (811.08 ± 1769.75 g/km2; n = 44). A mean total density of 671.91 ± 1544.16 g/km2 was found throughout the study area. Yet, two samples accounted together for one third of the collected plastic mass (34%). When removing these two samples from the dataset, the mean total concentration dropped to 463.49 ± 823.52 g/km2. A first-order approximation of the total mass of plastic floating in Mediterranean waters was obtained by computing 95% BCa bootstrapped confidence intervals of our mean density value averaged over the surface of the entire basin (2.5 × 106 km2). This resulted in a total estimated load ranging from 873.55 to 2576.03 tonnes of plastic.
Geographical differences between sub-basins were found also in the relative occurrence of different polymers (Fig. 4). The composition of western Mediterranean samples was dominated by low-density polymers such as polyethylene and polypropylene. Adriatic samples instead were more heterogeneous and rather characterized by a higher presence of paint chips, PS, PVC, PVA and PAs. PCA ordination of samples produced a two dimensional pattern, with the first two components explaining 75.7% of the total variance (Fig. 5). Despite some overlapping, most of the separation between sub-basins occurred along PC1 axis, mainly referring to PE (0.80) and paint (−0.57). On the other side, PP (−0.52) determined most of the separation along PC2.
When testing for the effect of environmental variables on the abundance of particles >700 μm, no significant correlation was found with surface temperature or salinity (p > 0.05). Conversely, wind stress and particle concentration were negatively correlated (rs = −0.31481, p = 0.0062991), with high densities being found only at relatively low wind speeds (Fig. 6). When correcting the abundance of particles >700 μm for the effect of wind-induced mixing, a mean correction coefficient of 2.06 was obtained (max 8.97), resulting in an increased average concentration of 0.61 ± 0.94 particles/m2 throughout the study area.
The proportion of different polymers found in our study roughly corresponds to the global production stocks of plastic materials, with polyolefins (PE and PP) accounting for 62% of the global plastic demand33 and for 68% of our sampled particles. Being widely used in the disposable packaging industry and having lower densities than seawater, it is not surprising that these polymers consistently account for the majority of the plastic particles floating in surface waters worldwide34,35,36. Also being less susceptible to sinking, the contribution of these low-density polymers has been shown to increase with distance from land37, hence potentially representing a proxy of the sample’s distance from pollution sources. From this perspective, the higher heterogeneity in the polymeric composition of Adriatic samples, together with an higher occurrence of high-density polymers, would indicate shorter residence times of particles at sea and a closer proximity to pollution sources, likely reflecting the distinctive hydrological features of the Adriatic basin.
The presence of paint and paraffin wax for instance, seems to suggest an high influence of ship-based pollution in the Adriatic Sea. Paint chips are typically generated during the ongoing repair, maintenance and cleaning of vessel decks and hulls38 and large quantities of synthetic paints have been recently related to intense marine traffic and shipping activities in Korean waters39. Paraffin wax on the other hand, is used for insulation and impregnation, as corrosion protective, additive to rubber products and in cosmetics and candle production. Large quantities are transported by cargo ships and tank-washing residues may be legally discharged at sea beyond the 12 nautical mile zone, including MARPOL designed “special areas” such as the Mediterranean Sea40. Paraffin clumps have been previously reported along the coasts of the North and Baltic Sea and in the stomach contents of northern fulmars41,42, nevertheless its presence in Mediterranean waters had never been explicitly recorded before.
Polycaprolactone (PCL), is a petroleum-based polyester commonly used in 3D printing, hobbyists and biomedical applications. It is considered biodegradable in terrestrial environment, with a degradation time of 6–12 days in laboratory conditions43, while some some signs of degradation appeared after 12 months in the marine environment44. PCL fragments were found in 9.5% of our net tows throughout our survey area and its presence in Mediterranean off-shore waters provides further evidence that some “biodegradable plastics” do not readily degrade in natural conditions, thus not representing an a priori solution for reducing marine litter33,45.
The range of synthetic materials found in our samples included several polymers – such as PVC, PVA, Paints and PET – whose densities are higher than many solutions commonly used for the extraction of microplastics from the organic matrix34,46. Although the mechanism through which high-density polymers can persist on the sea surface have yet to be clarified37,47,48, we provide empirical confirmation that, unless heavier solutions are used, such as zinc chloride or sodium iodide, the use of density gradient separation methods can result in a strong underestimation of many polymers commonly encountered in marine surface waters.
Despite general consensus about the loss of particles smaller than 1–2 mm from the sea surface8,19,49,50,51, we have found no clear indication about this process (Fig. 1), similarly to what was recently reported in the Atlantic Ocean37. Certainly without chemical identification of particles smaller than 700 μm we could not be sure about the synthetic nature of our smallest fractions, especially because a growing body of evidences is showing that the error rate during visual sorting noticeably increases with decreasing particle size34,46,52. However the strong correlation found between the abundance of characterized vs non-characterized particles together with a relatively low misidentification rate of 4.4% for characterized particles, seem to suggest good detection rates also for smaller particles, thus slightly enhancing the reliability of our density estimates.
Even considering only particles >700 μm, our measured concentration values are substantially higher than most studies previously performed in the Mediterranean Sea (Table 1). Nevertheless, because the larger size fractions always account for most of the weight, a closer agreement with previous studies is obtained when comparing plastic densities expressed in terms of mass concentrations, rather than particle counts. After removing two outliers from our dataset for instance, our mean density drops to 463.5 g/km2, which is incredibly similar to the values reported from the inner accumulation zones of all main oceanic gyres8 and to the values of 423 g/km2 and 579.3 g/km2 obtained in two previous large-scale surveys of the Mediterranean Sea19,53.
Among the various factors that can explain differences between studies, the way of computing tow distances is likely playing a major role. As a matter of fact, preliminary observations from a recent cruise showed that tow distances calculated through GPS positions are on average twice longer than those calculated using the flowmeter, with this critically resulting in halved plastic abundances (unpublished data). Since the flowmeter’s rotor revolutions measure the effective volume of water passing through the net, taking into account also any eventual clogging, flow-back, transversal currents and vertical movements, GPS may be a less reliable way of calculating the actual sampled area.
Although relatively high plastic concentrations were observed in the Balearic Sea, which was already indicated as a potential short-term retention area by numerical models54, no clear accumulation pattern and a high small-scale variability in plastic abundance and composition emerged from our survey, similarly to what was previously reported in the same area for floating macro-debris26. In this respect, the formation of permanent accumulation zones in the Mediterranean Sea is realistically hampered by the highly dynamic character of the surface circulation19,54, of which the observed heterogeneity in plastic distribution is very likely a reflection.
Our reported wind-mixing correction factor (mean 2.06; max 8.97) is very similar to those previously found in the Mediterranean Sea (mean 1.55; max 11.00)55, North Atlantic (mean 2.50; max 27.00)56 and Australian waters (mean 2.80; max 10.00)35. Wind-correction however, should be treated with great care, especially because of the considerable number of approximations and assumptions inherently related to the density of seawater, the buoyant rise speeds of the different polymers, sizes and shapes and to the reliability of modeled wind and wave fields. For these reasons, we preferred to present un-corrected density values in all tables and figures throughout the text.
Lastly, although disparity between numerical models and field observations has been often highlighted, when considering all our particles putatively identified as plastics, our mean total estimate for the whole Mediterranean (3.1 × 1012 particles) is in striking agreement with one of three very recent interpolations of ocean circulation models with measured plastic concentrations (3.2 × 1012 particles), but substantially lower than the two other predictions20. Thus, the goal of future research should be to better understand fate, sinks and fragmentation patterns of different polymers at sea, so that mismatch between plastic sinks and inputs can be eventually explained.
Our results demonstrate the pervasiveness of plastic pollution in Mediterranean waters and, confirming model predictions, provide further evidence that in this basin, microplastic abundances are amongst the highest in the world. The Mediterranean Sea is the largest and deepest enclosed sea on earth, hot-spot of marine biodiversity and cradle of human civilization, whose unique outflow of water occurs at depth from the narrow Strait of Gibraltar. Being one of the busiest navigation crossroads and top touristic destinations in the world, surrounded by a heavily populated and industrialized coastline, it is not surprising that in this basin, the impacts of human activities are proportionally stronger than in any other sea57. Sinks, sources, fate and residence times of different polymers are the main knowledge gaps to be addressed, especially with regard to the smaller size classes. In addition, data from the eastern Mediterranean Sea are urgently needed, as numerical simulations predict preferential accumulation in the levantine basin. The polymeric characterization of plastic particles is of paramount importance for a proper assessment of plastic contamination in the marine environment and for the effective identification of specific solutions and alternatives. However, irrespective of different polymers sources and typologies, the problem of plastic pollution is a social and behavioural issue, whose causes require to be mostly sought upstream in the consumption chain.
Sampling and laboratory analys
74 neuston samples were collected during two consecutive cruises (CoCoPro13 and Venus2-ArgoIT) carried out in the Mediterranean Sea on board the Italian research vessel Urania between May 9th and June 24th 2013 (see Fig. S1 and Table S1 for details on sampling dates and locations). Samples were all collected using a Neuston net (100 × 50 cm rectangular frame opening) equipped with a 200 μm mesh size. At each station, the net was towed for ~5 minutes at a speed of 1.5–2 knots. All deployments were made from the ship’s starboard side beyond the bow wave, in order to avoid the wake turbulence. Once on board, the net was rinsed with seawater and the content of the cod end was emptied over a 50 μm metal sieve. Plankton samples were transferred to 50 ml falcon tubes, fixed with EtOH at a final concentration of 80% and stored for laboratory analysis. Sea surface temperature and salinity, were continuously recorded by the ship’s data logger and averaged over the duration of each tow. The length of the trawls (mean: 175.7 ± 85.5 m) was calculated using a mechanical flowmeter positioned at the center of the net mouth (Hydro-Bios).
In the laboratory, samples were examined under a dissecting stereo-microscope (Leica). Plastic particles were carefully hand-picked using laboratory tweezers and transferred to glass jars. All samples were double-checked by two different researchers to ensure detection of all particles and to reduce operator bias during sorting. Particles were then separated into seven size classes by sequential sieving through a series of stacked stainless steel meshes (0.2–0.3 mm, 0.3–0.5 mm, 0.5–0.7 mm, 0.7–1.0 mm, 1.0–2.8 mm, 2.8–5.0 mm and 5.0–20 mm). All particles in each size category were counted, dried in oven for 1 h at 50 °C, weighed on an electronic balance (accuracy: 0.1 mg) and classified according to five shape categories (industrial pellets, fragments, foam, thin films and filaments/fibers). The sampled area and the volume filtered during each trawl were calculated using the frame dimensions, the tow distance (derived from the flowmeter readings) and considering the net mouth as partially submerged in water for four-fifths (40 cm). Microplastic concentrations – expressed as mg/m3, g/km2, particles/m3 and particles/m2 for better comparison with previous studies – were then computed and plotted in Fig. 3 (See also Table S1 and Fig. S2). The examination of sample blanks during laboratory analysis, together with growing scientific evidence suggests that unless drastic precautions are taken, airborne contamination during sampling or processing is not negligible58. Hence, after being counted and classified, all filaments and fibers suspected of having a textile origin were excluded from density calculations.
In order to characterize the polymeric identity of the collected material, FT-IR (Fourier Transform Infrared Spectroscopy) analyses were performed on all particles >700 μm (n = 4,050). The subset was considered highly representative since it comprised 96.16% of the total weight of collected plastic. Analyses were performed using a Cary 660 FTIR spectrometer (Agilent) equipped with ATR (GladiATR Diamond Crystal Plate, Pike technologies) which allowed only the characterization of particles with grain size larger than 700 μm. Following background scans, 128 scans per particle were performed and CO2 interference (adsorption at approximately 2300–2400 cm−1) was removed for clarity. For each particle, scans were performed with a resolution of 4 cm−1. Agilent Resolution Pro v5.2 was used for the output spectra and identification of polymers was performed by comparison with a library of standard spectra. Only polymers matching reference spectra for more than 60% were accepted, in line with suggestions from previous studies24. Selected examples of output and reference spectra of the most common polymers found in our samples are shown in Fig. S4.
Wind correction factor
Wind-driven mixing can extend the vertical distribution of buoyant particles below the sampling layer, therefore plastic concentrations were corrected using a widely used theoretical model56. Wind stress (τ) and significant wave height (Hs) data were extracted from ECMWF ERA-Interim reanalysis product59, freely downloadable at http://apps.ecmwf.int/datasets/data/interim-full-daily/levtype=sfc/ (Date of access: 16/01/2016). Both fields were available with an original spatial resolution of 1/8° × 1/8° and a time frequency of 3 h and 6 h for τ and Hs respectively. The extracted data were linearly interpolated in time and space to each trawl date and location and conservatively incremented by 20% in order to compensate for well-known model underestimation in enclosed seas60. Friction velocities in water () were derived from τ values assuming density of seawater ρw = 1.026 g/cm3. As suggested by the authors, wind correction was then applied only to net tows carried out with cm/s56 (n = 30; 40.5% of the tows), considering the immersion depth of the net (d) equal to 0.4 m and the buoyant rise velocity of plastics (Wb) equal to 0.005 m/s61.
Spearman’s correlation coefficient was used to test significant relationships between the abundance of floating particles and environmental variables, as well as between the abundance of different size classes. Spatial differences in the polymeric composition were highlighted through Principal Component Analysis (PCA) based on a variance-covariance matrix of the relative frequencies of the seven most common polymer classes: PP, PE, PS, PA, PVC, Nylon and Paint. Mann-Whitney U test was used to verify significant differences in plastic concentration and in the occurrence of the main polymer classes between sub-basins. Normality and homogeneity of variance was checked and the level of statistical significance was set at p < 0.05. Data analysis was performed using GraphPad Prism 6© and PAST v3.1162.
How to cite this article: Suaria, G. et al. The Mediterranean Plastic Soup: synthetic polymers in Mediterranean surface waters. Sci. Rep. 6, 37551; doi: 10.1038/srep37551 (2016).
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Plastics Europe. Plastics - the Facts 2015 - An analysis of European plastics production, demand and waste data. Association of Plastic Manufacturers, Brussels 34 http://www.plasticseurope.org/Document/plastics—the-facts-2015.aspx. (Access date: 2016-01-02) (2015).
World Economic Forum. The New Plastics Economy - Rethinking the future of plastics. Ellen MacArthur Foundation and McKinsey & Company 118 pp. https://www.ellenmacarthurfoundation.org/publications/the-new-plastics-economy-rethinking-the-future-of-plastics. (Access date: 2016-03-03) (2016).
Jambeck, J. R. et al. Plastic waste inputs from land into the ocean. Science 347, 768–771 (2015).
Ryan, P. A brief history of marine litter research in Marine Anthropogenic Litter (eds Bergmann, M. et al.) Ch. 1, 1–25 (Springer, 2015).
Moore, C. J., Moore, S. L., Leecaster, M. K. & Weisberg, S. B. A comparison of plastic and plankton in the North Pacific central gyre. Marine Pollution Bulletin 42, 1297–1300 (2001).
Law, K. L. et al. Plastic accumulation in the North Atlantic subtropical gyre. Science 329, 1185–1188 (2010).
Eriksen, M. et al. Plastic pollution in the South Pacific subtropical gyre. Marine Pollution Bulletin 68, 71–76 (2013).
Cózar, A. et al. Plastic debris in the open ocean. Proceedings of the National Academy of Sciences 111, 10239–10244 (2014).
Lusher, A. L., Tirelli, V., O’Connor, I. & Officer, R. Microplastics in Arctic polar waters: the first reported values of particles in surface and sub-surface samples. Scientific reports 5 (2015).
Woodall, L. C. et al. The deep sea is a major sink for microplastic debris. Royal Society Open Science 1, 140317 (2014).
Zalasiewicz, J. et al. The geological cycle of plastics and their use as a stratigraphic indicator of the anthropocene. Anthropocene 13, 4–17 (2016).
Eriksen, M. et al. Plastic pollution in the world’s oceans: more than 5 trillion plastic pieces weighing over 250,000 tons afloat at sea. PloS ONE 9, e111913 (2014).
Rochman, C. M. The complex mixture, fate and toxicity of chemicals associated with plastic debris in the marine environment in Marine anthropogenic litter (eds Bergmann, M. et al.) Ch. 5, 117–140 (Springer, 2015).
Zettler, E. R., Mincer, T. J. & Amaral-Zettler, L. A. Life in the ‘plastisphere’: Microbial communities on plastic marine debris. Environmental Science & Technology 47, 7137–7146 (2013).
Farrell, P. & Nelson, K. Trophic level transfer of microplastic: Mytilus edulis (l.) to Carcinus maenas (l.). Environmental Pollution 177, 1–3 (2013).
Setälä, O., Fleming-Lehtinen, V. & Lehtiniemi, M. Ingestion and transfer of microplastics in the planktonic food web. Environmental pollution 185, 77–83 (2014).
Rochman, C. M. et al. Policy: Classify plastic waste as hazardous. Nature 494, 169–171 (2013).
Lebreton, L.-M., Greer, S. & Borrero, J. Numerical modelling of floating debris in the world’s oceans. Marine Pollution Bulletin 64, 653–661 (2012).
Cózar, A. et al. Plastic Accumulation in the Mediterranean Sea. PloS ONE 10, e0121762 (2015).
van Sebille, E. et al. A global inventory of small floating plastic debris. Environmental Research Letters 10, 124006 (2015).
Deudero, S. & Alomar, C. Mediterranean marine biodiversity under threat: Reviewing influence of marine litter on species. Marine Pollution Bulletin 98, 58–68 (2015).
Romeo, T. et al. First evidence of presence of plastic debris in stomach of large pelagic fish in the Mediterranean Sea. Marine Pollution Bulletin 95, 358–361 (2015).
Anastasopoulou, A., Mytilineou, C., Smith, C. J. & Papadopoulou, K. N. Plastic debris ingested by deep-water fish of the Ionian Sea (Eastern Mediterranean). Deep Sea Research Part I: Oceanographic Research Papers 74, 11–13 (2013).
Avio, C. G., Gorbi, S. & Regoli, F. Experimental development of a new protocol for extraction and characterization of microplastics in fish tissues: First observations in commercial species from Adriatic Sea. Marine Environmental Research 111, 18–26 (2015).
Pham, C. K., Ramrez-Llodra, E., Tyler, P. A. et al. Marine Litter Distribution and Density in European Seas, from the Shelves to Deep Basins. PLoS ONE 9, e95839 (2014).
Suaria, G. & Aliani, S. Floating debris in the Mediterranean Sea. Marine Pollution Bulletin 86, 494–504 (2014).
Turner, A. & Holmes, L. Occurrence, distribution and characteristics of beached plastic production pellets on the island of Malta (central Mediterranean). Marine Pollution Bulletin 62, 377–381 (2011).
Laglbauer, B. J. et al. Macrodebris and microplastics from beaches in Slovenia. Marine Pollution Bulletin 89, 356–366 (2014).
Vianello, a. et al. Microplastic particles in sediments of Lagoon of Venice, Italy: First observations on occurrence, spatial patterns and identification. Estuarine, Coastal and Shelf Science 130, 54–61 (2013).
Alomar, C., Estarellas, F. & Deudero, S. Microplastics in the Mediterranean sea: Deposition in coastal shallow sediments, spatial variation and preferential grain size. Marine Environmental Research 115, 1–10 (2016).
Galgani, F. et al. (Office for Official Publications of the European Communities, Luxembourg, 2010). http://ec.europa.eu/environment/marine/pdf/9-Task-Group-10.pdf (Access date: 2016-04-09).
G7. World leaders Declaration - G7 Summit. Think Ahead. Act Together, Schloss Elmau, Germany, 7-8 June 2015 23 pp. (2015). https://www.bundesregierung.de/Content/DE/_Anlagen/G8_G20/2015-06-08-g7-abschluss-eng.pdf?__blob=publicationFile v=6 (Access date: 2016-02-01).
Andrady, A. L. Plastics in the Oceans. In Plastics and Environmental Sustainability, 295–318 (John Wiley and Sons, Inc, 2015).
Hidalgo-Ruz, V., Gutow, L., Thompson, R. C. & Thiel, M. Microplastics in the marine environment: a review of the methods used for identification and quantification. Environmental science & technology 46, 3060–3075 (2012).
Reisser, J. et al. Marine plastic pollution in waters around Australia: Characteristics, concentrations, and pathways. PLoS ONE 8 (2013).
Frias, J., Otero, V. & Sobral, P. Evidence of microplastics in samples of zooplankton from Portuguese coastal waters. Marine Environmental Research 95, 89–95 (2014).
Enders, K., Lenz, R., Stedmon, C. A. & Nielsen, T. G. Abundance, size and polymer composition of marine microplastics ≥ 10 μm in the Atlantic Ocean and their modelled vertical distribution. Marine Pollution Bulletin 100, 70–81 (2015).
Turner, A. Marine pollution from antifouling paint particles. Marine Pollution Bulletin 60, 159–171 (2010).
Song, Y. K. et al. Large accumulation of micro-sized synthetic polymer particles in the sea surface microlayer. Environmental science & technology 48, 9014–9021 (2014).
UEG. Pollution of the North and Baltic Seas with Paraffin. Independent Environmental Group of Experts “Consequences of Pollution Incidents”, Opinion dated 22 July 2014 (2014). URL http://www.bfr.bund.de/cm/349/pollution-of-the-north-and-baltic-seas-with-paraffin.pdf. (Access date: 2016-03-02).
Van Franeker, J. A. et al. Monitoring plastic ingestion by the northern fulmar Fulmarus glacialis in the North Sea. Environmental Pollution 159, 2609–2615 (2011).
Esiukova, E. Plastic pollution on the Baltic beaches of Kaliningrad region, Russia. Marine Pollution Bulletin, In press, http://dx.doi.org/10.1016/j.marpolbul.2016.10.001 (2016).
Tokiwa, Y., Calabia, B. P., Ugwu, C. U. & Aiba, S. Biodegradability of plastics. International Journal of Molecular Sciences 10, 3722–3742 (2009).
Sekiguchi, T. et al. Biodegradation of aliphatic polyesters soaked in deep seawaters and isolation of poly (ε-caprolactone)-degrading bacteria. Polymer Degradation and Stability 96, 1397–1403 (2011).
UNEP. Biodegradable plastics and marine litter. Misconceptions, concerns and impacts on marine environments. United Nations Environment Program - Nairobi, Kenya (2015).
Ivleva, N. P., Wiesheu, A. C. & Niessner, R. Microplastic in Aquatic Ecosystems. Angewandte Chemie International Edition 1521–3773 (2016). http://dx.doi.org/10.1002/anie.201606957.
Lattin, G. L., Moore, C. J., Zellers, A. F., Moore, S. L. & Weisberg, S. B. A comparison of neustonic plastic and zooplankton at different depths near the southern California shore. Marine Pollution Bulletin 49, 291–294 (2004).
Browne, M. A., Galloway, T. S. & Thompson, R. C. Spatial patterns of plastic debris along estuarine shorelines. Environmental Science & Technology 44, 3404–3409 (2010).
Pedrotti, M. L. et al. Changes in the Floating Plastic Pollution of the Mediterranean Sea in Relation to the Distance to Land. PloS one 11, e0161581 (2016).
Lusher, A. L., Burke, A., O’Connor, I. & Officer, R. Microplastic pollution in the Northeast Atlantic Ocean: Validated and opportunistic sampling. Marine Pollution Bulletin 88, 325–333 (2014).
Morét-Ferguson, S. et al. The size, mass, and composition of plastic debris in the western North Atlantic Ocean. Marine Pollution Bulletin 60, 1873–1878 (2010).
Löder, M. G. J. & Gerdts, G. Methodology used for the detection and identification of microplastics – A critical appraisal in Marine Anthropogenic Litter (eds Bergmann, M. et al.) Ch. 8, 201–227 (Springer, 2015).
Ruiz-Orejón, L. F., Sardá, R. & Ramis-Pujol, J. Floating plastic debris in the Central and Western Mediterranean Sea. Marine Environmental Research 120, 136–144 (2016).
Mansui, J., Molcard, A. & Ourmières, Y. Modelling the transport and accumulation of floating marine debris in the Mediterranean basin. Marine Pollution Bulletin 91, 249–257 (2015).
Faure, F. et al. An evaluation of surface micro-and mesoplastic pollution in pelagic ecosystems of the Western Mediterranean Sea. Environmental Science and Pollution Research 22, 12190–12197 (2015).
Kukulka, T., Proskurowski, G., Morét-Ferguson, S., Meyer, D. & Law, K. The effect of wind mixing on the vertical distribution of buoyant plastic debris. Geophysical Research Letters 39 (2012).
Coll, M. et al. The Mediterranean Sea under siege: spatial overlap between marine biodiversity, cumulative threats and marine reserves. Global Ecology and Biogeography 21, 465–480 (2012).
Woodall, L. C. et al. Using a forensic science approach to minimize environmental contamination and to identify microfibres in marine sediments. Marine Pollution Bulletin 95, 40–46 (2015).
Dee, D. et al. The ERA-interim reanalysis: Configuration and performance of the data assimilation system. Quarterly Journal of the Royal Meteorological Society 137, 553–597 (2011).
Ardhuin, F. et al. Comparison of wind and wave measurements and models in the Western Mediterranean Sea. Ocean Engineering 34, 526–541 (2007).
Reisser, J. et al. The vertical distribution of buoyant plastics at sea: an observational study in the North Atlantic Gyre. Biogeosciences 12, 1249–1256 (2015).
Hammer, Ø., Harper, D. A. T. & Ryan, P. D. PAST - Palaeontological statistics. Software package for education and data analysis. Palaeontologia Electronica 4, 1–9 (2001).
Kornilios, S., Drakopoulos, P. & Dounas, C. Pelagic tar, dissolved/dispersed petroleum hydrocarbons and plastic distribution in the Cretan Sea, Greece. Marine Pollution Bulletin 36, 989–993 (1998).
Collignon, A. et al. Neustonic microplastic and zooplankton in the North Western Mediterranean Sea. Marine Pollution Bulletin 64, 861–864 (2012).
Fossi, M. C. et al. Are baleen whales exposed to the threat of microplastics? A case study of the Mediterranean fin whale (Balaenoptera physalus). Marine Pollution Bulletin 64, 2374–2379 (2012).
Collignon, A., Hecq, J.-H., Galgani, F., Collard, F. & Goffart, A. Annual variation in neustonic micro-and meso-plastic particles and zooplankton in the Bay of Calvi (Mediterranean–Corsica). Marine Pollution Bulletin 79, 293–298 (2014).
de Lucia, G. A. et al. Amount and distribution of neustonic micro-plastic off the western Sardinian coast (Central-Western Mediterranean Sea). Marine Environmental Research 100, 10–16 (2014).
Pedrotti, M. L. et al. Plastic fragments on the surface of Mediterranean waters. In CIESM Workshop Monograph n° 46 – Marine litter in the Mediterranean and Black Seas (ed. Briand, F. ) Ch. 3, 115–123 (CIESM Publisher, 2014).
Panti, C. et al. Occurrence, relative abundance and spatial distribution of microplastics and zooplankton NW of Sardinia in the Pelagos Sanctuary Protected area, Mediterranean Sea. Environmental Chemistry 12, 618–626 (2015).
Fossi, M. C. et al. Fin whales and microplastics: The Mediterranean Sea and the Sea of Cortez scenarios. Environmental Pollution 209, 68–78 (2016).
We are thankful to Mireno Borghini (CNR-ISMAR) and to all crew and officers of R/V Urania for their for their help with sample collection, to Silvia Cocito and Chiara Lombardi for having kindly provided access to ENEA laboratory facilities and to the entire Algalita staff for their hospitality and for having drawn worldwide attention to the problem of plastic pollution. Fundings were provided through EU FP7 project COCONET (Grant agreement no: 287844), RITMARE (the Italian marine research program), JPI-O BASEMAN and a 30 days Short-Term Mobility grant awarded by CNR.
The authors declare no competing financial interests.
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Suaria, G., Avio, C., Mineo, A. et al. The Mediterranean Plastic Soup: synthetic polymers in Mediterranean surface waters. Sci Rep 6, 37551 (2016). https://doi.org/10.1038/srep37551
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