For over 60 years, our oceans have been a reservoir for exponentially increasing amounts of plastic waste. Plastic has been documented at all levels of the marine food web, from the deepest oceanic trenches to the most far-flung beaches. Here, we present data on the presence of significant quantities of plastic on the remote Cocos (Keeling) Island group, located 2,100 km off the northwest coast of Australia. From our comprehensive surveys of debris on the beach surface, buried, and beach-back vegetation, we estimate there are 414 million anthropogenic debris items, weighing 238 tonnes, currently deposited on the Cocos (Keeling) Island group. Of the identifiable items, ~25% were classified as disposable plastics, including straws, bags, and toothbrushes. Debris buried up to 10 cm below the surface is estimated to account for 93% (~383 million items) of all debris present on Cocos, the majority of which (~60%) is comprised of micro-debris (2–5 mm). In the absence of meaningful change, debris will accumulate rapidly on the world’s beaches. Small, buried items pose considerable challenges for wildlife, and volunteers charged with the task of cleaning-up, thus preventing new items from entering the ocean remains key to addressing this issue.
Global plastic production has increased exponentially over the last 60 years1. Nearly half of all plastic manufactured during this time (~8,300 million metric tons; Mt) was produced in the last 13 years (3,900 Mt) with ~40% of items entering the waste stream in the same year they were produced (e.g., single-use packaging)2. Insufficient or ineffective waste management contributed to an estimated 12.7 million Mt of plastic entering our oceans in 20102,3 with a recent global estimate (5.25 trillion items)4 suggesting there are now more pieces of plastic in the ocean than there are stars in the Milky Way5. Numbers as large as these make it difficult to comprehend the scale of the issue and the feasibility of possible solutions6,7. Unfortunately, unless drastic steps are taken, the numbers and challenges will only grow, with the quantity of waste entering the ocean predicted to increase ten-fold by 20253.
Once in the ocean, plastic items exposed to wave action and sunlight begin to fragment into small particles that persist for decades, perhaps centuries8. Therefore, the characteristics that make plastic such a popular material (e.g. durability, light-weight, low cost) also contribute to its abundance in the ocean, and to its role as a significant environmental threat9. Removing the significant quantities of plastic already in the ocean is not possible10,11, making the prevention of new items entering the ocean at their source critically important12.
Anthropogenic debris (hereafter ‘debris’) harms a diversity of aquatic wildlife directly via entanglement and ingestion13, as well as indirectly through exposure to plastic-associated chemicals and microbes14,15,16. There is an urgent need to quantify and mitigate these impacts, establish patterns of temporal change, and recognise plastic debris for what it is: a persistent, hazardous, and rapidly expanding environmental pollutant17,18.
Because there are few local sources of pollution and little human interference (i.e., no recreational beach users or debris removal via beach clean-ups), isolated islands with little or no human occupation can act as marine pollution monitors, providing unique insights into debris accumulation trends19. Here we present quantitative data from beach surveys of inhabited and uninhabited islands in the Cocos (Keeling) Island group (henceforth CKI). Using a comprehensive beach debris sampling method19, we highlight the ubiquitous and problematic nature of plastics on remote islands, especially that of “single-use” items, and the utility of beach survey data as a sentinel for the state of the world’s oceans.
The Cocos (Keeling) Islands (CKI; 12°05′S, 96°53′E) comprise two small, mid-oceanic atolls (total land area 14 km2) located approximately 2,100 km north-west of Exmouth, Western Australia (Fig. 1) in the Indian Ocean. The islands are an Australian external territory. The much larger, southern atoll consists of a horse-shoe chain of 26 islands around a shallow, central lagoon with West and Home Island inhabited by ~600 people20. The northern atoll (North Keeling, designated as Pulu Keeling National Park) is a rarely visited, uninhabited island that is an important breeding site for seabirds21. Seven out of 27 islands in the CKI group were sampled during our 2017 survey. These seven islands account for 88% of the landmass of CKI (i.e., the remaining islands not surveyed were very small) and included both inhabited and uninhabited islands. Data were collected from two beaches (lagoon- and ocean-facing) per island to capture the variability in debris density, with additional beaches sampled on West and South Island (the largest islands in the CKI group). Where possible, transects or quadrats were also completed on a range of sediment types (e.g., sand, pebbles).
The standing stock of accumulated micro- (2–5 mm) and macro-debris (>5 mm), including plastic, glass, wood, and metal items, was sampled along a total of 25 beaches (seven islands) of the CKI group (total sampled area 1,110 m2). Most sites were surveyed from 13–24 March 2017, however, due to the difficulty in accessing North Keeling, it was not possible to survey this island until 21 September 2017. To ensure beach debris data collected on CKI were comparable with the data from other remote islands, the sampling methods used on CKI were identical to those developed for Henderson Island in the South Pacific19. As shown in Fig. 2 of Lavers and Bond19, we used three different transect and quadrat designs aimed at providing specific types of data: (1) we sampled surface beach debris along fifteen 30 × 6 m transects which covered most of the distance from the water’s edge to the start of the vegetation. Within this area, the transect was positioned with the middle 2 m wide strip centred over the high tide mark (i.e., area of known debris accumulation). (2) We collected data on the density of debris located within the low-lying beach-back vegetation using twelve 10 × 2 m transects on five islands. The transects were run perpendicular to the water’s edge, extending 10 m from the vegetation line toward the centre of each island. Only macro-debris (≥5 mm) was recorded in the beach-back area because of the difficulty in detecting smaller items amongst vegetation. (3) Buried debris (to a depth of 10 cm) was sieved from all sediment excavated in seven paired quadrats following the method of Kusui and Noda22, with each pair comprising one quadrat along the high tide line, and one located approximately 2 m below the vegetation line. At each quadrat, a 0.4 × 0.4 m wooden frame was inserted into the sand, and the contents of the frame were exhumed to a depth of 10 cm. Items located above a depth of 1 cm were considered to be surface debris and were excluded. The inner island, beyond the beach-back transect area, was not surveyed and has not been included in any extrapolations.
All debris items encountered in transects or quadrats were counted, sorted by type, and weighed using an electronic balance to 0.001 g (for micro-debris 2–5 mm) or 1 g using a spring balance (for macro-debris ≥5 mm). We used the same standard debris type categories as Lavers and Bond20, including glass, foam, metal, hard plastic fragments, film (e.g., soft plastics such as bags), and threads (e.g., rope and fishing line). Additional sub-categories included readily identifiable items or those commonly reported in the recent literature (e.g., industrial resin pellet (“nurdle”), melted plastic, shoes, cigarette lighters, and toothbrushes). All values are presented as mean ± SD unless specified otherwise.
The total amount of debris present on each island in the Cocos (Keeling) Island group in 2017 was estimated in five steps. (1) The total beach area and perimeter for each island was measured using aerial imagery in Google Earth Pro. (2) We then multiplied the mean density of items recorded from beach transects by the total beach area to estimate the total debris visible on the beach surface of each island. (3) Next, we estimated the total amount of debris buried to a depth of 10 cm on each island based on the mean buried density recorded from quadrats and total beach surface area of each island. (4) The quantity of debris present within a 10 m wide zone of beach-back vegetation was estimated using the mean density values generated from 10 m transects running perpendicular from the beach edge multiplied by the perimeter of each island. (5) Missing data on the density and/or mass of debris (e.g., North Keeling) were estimated based on the combined mean of the remaining islands in the CKI group. Finally, the total number and mass of items recorded on the seven islands surveyed (representing 88% of the landmass) were extrapolated using mean debris numbers and mass to provide estimates for the entire CKI group.
We recorded a total of 23,227 anthropogenic debris items, weighing a total of 96.67 kg. Based on these data, and the density estimates detailed below, we estimate there were 414 million pieces of anthropogenic debris weighing 238 tonnes present on the entire Cocos (Keeling) Islands group in 2017 (i.e., extrapolated to include all 27 islands, Table 1).
The mass and number of debris items recorded across all 15 beach surface transects (868 m2) was 70.73 kg (excluding North Keeling samples, which were not weighed) and 18,928 items, respectively. Mean density of visible debris on the beach surface ranged from 4.72 items m−2 (Gun Beach 2, West Island) to 55.67 items m−2 (North Cove, Home Island; Table 2; overall mean 21.68 ± 19.01 items m−2). About half of the collected surface debris by number was comprised of microplastics (51.35 ± 9.31%; Fig. 2, panel D). Extrapolated to the total beach area for all of CKI, an estimated 14.29 million pieces of visible debris weighing 47.96 tonnes were present on beach surfaces of the CKI group (Table 1).
Total buried debris (top 10 cm) recorded in 14 quadrats from seven sites on three islands (2.24 m2) accounted for only 6.32% of all beach debris items collected by number (n = 1,467) and 0.32% by weight (0.23 kg). Mean density of buried items (both micro- and macro-debris) varied from 28.13 items m−2 (South Beach, Home Island) to 2,506.25 items m−2 (Central SE, South Island; overall mean 654.91 ± 869.97 items m−2), while the mean mass of items ranged from 0.01 kg m−2 (Home Island) to 0.29 kg m−2 (South Island; Table 2). Between 10–70× more debris items m−2 were found buried compared to items visible on the surface of beaches, and 76.42 ± 10.99% of buried debris items were comprised of micro-debris. The estimated total number of buried debris items for CKI is 383.99 million pieces weighing 61.60 tonnes (Table 1).
The 12 beach-back transects completed on five islands (240 m2) recovered 2,622 items, weighing 25.71 kg. The mean density of beach-back debris (macro only) ranged from 2.28 items m−2 (Pulu Marya Island) to 51.25 items m−2 on (Home Island; Table 2 and Fig. 2, panel C; overall mean 10.93 ± 15.39 items m−2). Data from Home and Horsburgh Islands indicated the average mass of macro-debris found in beach-back areas was 3–6× heavier than on the beach surface. Extrapolated to the total beach-back area of the island group, we estimate that there were 15.32 million debris items present in the beach-back, weighing a total of 128.42 tonnes, across the CKI (Table 1).
Plastic items accounted for 95.41% (n = 22,161) of all debris recorded, followed by foam (3.96%, n = 919). All other debris types combined (glass, metal, wood and fabric) made up 0.63% (n = 147) of the total count. Plastic fragments were the most common item encountered on CKI beaches (69.34%, n = 16,106). Of the identifiable items recorded during the survey, 9.84% were categorised as disposable single-use items (n = 2,285), 3.84% as resin pellets (‘nurdles’, n = 891) and 1.57% as fishing-related (n = 365). The most common identifiable consumer items were bottle caps and lids (n = 840), shoes (predominantly ‘flip-flops’, n = 549) and plastic drinking straws (n = 235).
Results of the first, comprehensive survey of debris on the Cocos (Keeling) Islands in 2017 indicated there are an estimated 413.6 million pieces of debris weighing 238 tonnes (Table 1) distributed across these remote, tropical islands. While these numbers are among the highest reported on remote islands19,23 the data underestimate the true amount of debris present on CKI as we were unable to sample all possible debris sources. For example, we excluded items buried >10 cm below the surface and were unable to survey some debris ‘hotspots’ within the atoll, including the south-east side of South Island (Fig. 2; panel A and D) due to accessibility issues (i.e., unfavourable tides, vessel mechanical failure). As a result, our data on debris densities for CKI are conservative and values should be interpreted as minimum estimates.
The density of debris appeared to vary according to a range of factors on CKI, depending on the island. For example, the density of macro-debris on Horsburgh Island ranged from 4.72 to 22.02 items m−2 on the lagoon-facing and ocean-facing beaches, respectively (Table 2). However, as Horsburgh Island is located at the northern end of the atoll (Fig. 1), it is partially sheltered from ocean currents. In contrast, the ocean-facing beaches on South Island face directly into the predominant currents in this region (Fig. 1), which tend to flow in a westerly direction24 and cause vast quantities of debris to accumulate on these exposed beaches (Fig. 2, panel A & D).
Most studies of beach debris focus on large, visible plastics because these items are readily observed, easily collected, and can provide additional information when intact (e.g., country of manufacture)25. In contrast, paired data on micro- and macro-debris are limited, primarily due to the difficulty in identifying small items25,26,27. On CKI, where both micro- and macro-debris were recorded, micro-debris accounted for 60.29 ± 16.72% of items, comparable to Henderson Island in the remote South Pacific (~62% of beach-washed items were micro-debris)19. The removal of micro-debris from beaches poses a significant challenge even at small scales, due to the time required to separate plastics <5 mm from sediment and other organic materials25. As a result, large-scale estimates of debris accumulation generated by researchers and citizen scientists (e.g., International Coastal Cleanup, Clean-up Australia Day) rarely account for micro-debris items, meaning the data commonly referenced by media and policy makers are very conservative.
Based on the estimated totals for the CKI group (Table 1), the quantity of debris predicted to be buried 1–10 cm below the beach surface (n = 338,355,473 items) is 26x greater than the amount of debris visible on the beach surface (3.80%, n = 12,868,379 items). Again, this suggests global debris surveys, the majority of which are focused solely on surface debris, have drastically underestimated the scale of debris accumulation. These findings highlight a growing need for the development of effective policy and mitigation, which are currently focused primarily on localised clean-up of visible debris, and raises questions regarding the potential impact of buried plastic on wildlife nesting or living within beach sediments, such as sea turtles, crustaceans, and meiofauna. Furthermore, the removal of buried debris would require major mechanical disturbance of sediments, with potentially significant environmental impacts on inhabiting biota. Cozar et al.28 suggested the deposition of millimetre-sized plastic on shorelines was unlikely to explain the gap in size distribution or global surface load of floating plastic debris. However, these conclusions were largely based on studies of surface macro-debris. On CKI, 78.12% of the estimated 384 million buried items (Table 1) were 2–5 mm in size, thus new, more comprehensive data on the deposition of debris, including micro- and buried items on remote islands, may be of increasing importance when interpreting patterns observed at-sea.
While some plastic types (e.g., fragments) are ubiquitous and reported in most beach surveys, other items appear to accumulate only in specific areas. For example, fishing activities are often implicated with respect to marine debris, with around 15–60% of items recorded at sea and washed up on beaches attributed to commercial or recreational fishing29. In contrast, fishing-related debris was relatively uncommon on CKI (1.6% of items recorded, n = 365; Table 3), compared to other remote islands where 8–46% of beach-washed items were fishing related19,23. Instead, shoes (n = 549) and “single-use” or “disposable” consumer items (e.g., food packaging, drink bottles, straws, plastic cutlery, bags, toothbrushes; n = 2,285; Fig. 2, Table 3) accounted for nearly 25% of the debris present on CKI beaches. Thus, the debris on CKI seems to mirror global data on plastic production2, and highlights a worrying trend in the production and discharge of single-use products2,30.
Our excessive and unrelenting demand for plastics, coupled with ineffective policy and waste management, has resulted in myriad negative effects on marine, freshwater, and terrestrial environments, including entanglement and ingestion of debris, and subsequent exposure to plastic-associated chemicals13,31,32,33. Damaged environmental aesthetics, with consequent impacts on tourism, are also widely documented34,35. CKI is touted as “Australia’s last unspoilt paradise”, with tourism a primary source of income for the local community36. However, the impact of debris on tourism and CKI’s beaches, is increasingly difficult to avoid. For example, Cossie’s Beach on the south side of Direction Island was recently named “Australia’s top stretch of sand”37, yet beaches <200 m away on the northern side of the island exhibit some of the highest debris densities in the CKI group (Table 1, Fig. 2 panel B). Correspondingly, pollution of the marine environment has been identified as an emerging management issue for CKI (action 3.2.2)38.
Sadly, the situation on the Cocos (Keeling) Islands is not unique, with significant quantities of debris documented on islands and coastal areas from the Arctic to the Antarctic (see Fig. 3)39,40. Together, these islands and coastal areas reflect the acute symptoms of an otherwise rapidly increasing environmental hazard. Legal protection (e.g., World Heritage listing, marine/national park designation) and a lack of human activity has not afforded remote sites like CKI and Henderson Island protection from debris washing up on their shores19. On CKI, infrastructure (e.g., waste management) has also failed to protect these islands against debris accumulation. So, what will provide effective protection? With the quantity of debris entering the world’s oceans predicted to increase by an order of magnitude by 20253, that question is now urgent. Clean-up events focused solely on surface debris of a single remote island can take months to negotiate, require significant staff time, cost tens of thousands of dollars, and typically deposit the collected debris into landfill (authors’ personal observations). With an estimated 2,000 oceanic islands worldwide, and thousands of new plastic items washing up on remote beaches every day19, clean-ups cannot keep pace. The beaches of CKI are already home to an estimated 373,000 toothbrushes and 977,000 shoes - equivalent to what the CKI community would produce as waste in ~4000 years. In the absence of rapid and meaningful change, anthropogenic debris will accumulate on beaches19, with impacts increasingly felt by biodiversity41,42 and marine plastic mitigation will remain a perpetual game of catch-up. Mitigation initiatives, including policy, should be mindful of the challenges faced by remote islands, and the communities that reside there. For example, CKI has struggled to identify an appropriate location for landfill (a challenge on many, low-lying islands) and is unable to export recyclable items to the Australian mainland due to complex biosecurity legislation43. Prevention is key, and for that, a multi-prong approach is urgently required, including significant investment in strategies designed to limit plastic production and consumption (e.g., widespread bans on single-use items), and effective waste management that prevents entry of plastic items into the ocean at the source (‘source reduction’)44.
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Neufeld, L., Stassen, F., Sheppard, R. & Gilman, T. The new plastics economy: rethinking the future of plastics. (World Economic Forum, 2016).
Geyer, R., Jambeck, J. R. & Law, K. L. Production, use, and fate of all plastics ever made. Sci. Adv. 3, https://doi.org/10.1126/sciadv.1700782 (2017).
Jambeck, J. R. et al. Plastic waste inputs from land into the ocean. Science 347, 768–771, https://doi.org/10.1126/science.1260352 (2015).
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).
Bell, G. & Levin, S. Mass of the Milky Way and Dwarf Spheroidal Stream Membership. Bulletin of the American Astronomical Society 29, 1384 (1997).
Boyd, D. & Crawford, K. Critical questions for big data: Provocations for a cultural, technological, and scholarly phenomenon. Info. Comm. Soc. 15, 662–679, https://doi.org/10.1080/1369118X.2012.678878 (2012).
Marx, V. Biology: The big challenges of big data. (2013).
Andrady, A. L. Plastics and the environment. (John Wiley & Sons, 2003).
UNEP. Year Book 2014: Emerging issues in our global environment. Chapter 8: Plastic debris in the ocean. 46–53 (United Nations Environment Programme, Nairobi, Kenya, 2014).
Rochman, C. M. Strategies for reducing ocean plastic debris should be diverse and guided by science. Environ. Res. Lett. 11, 014006 (2016).
Sherman, P. & van Sebille, E. Modeling marine surface microplastic transport to assess optimal removal locations. Environ. Res. Lett. 11, 014006 (2016).
Ryan, P. G., Moore, C. J., van Franeker, J. A. & Moloney, C. L. Monitoring the abundance of plastic debris in the marine environment. Philos. Trans. Royal Soc. B. 364, 1999–2012, https://doi.org/10.1098/rstb.2008.0207 (2009).
Gall, S. C. & Thompson, R. C. The impact of debris on marine life. Mar. Pollut. Bull. 92, 170–179, https://doi.org/10.1016/j.marpolbul.2014.12.041 (2015).
Zettler, E. R., Mincer, T. J. & Amaral-Zettler, L. A. Life in the “Plastisphere”: microbial communities on plastic marine debris. Environ. Sci. Technol. 47, 7137–7146, https://doi.org/10.1021/es401288x (2013).
Lavers, J. L., Bond, A. L. & Hutton, I. Plastic ingestion by Flesh-footed Shearwaters (Puffinus carneipes): Implications for chick body condition and the accumulation of plastic-derived chemicals. Environ. Pollut. 187, 124–129, https://doi.org/10.1016/j.envpol.2013.12.020 (2014).
Chua, E. M., Shimeta, J., Nugegoda, D., Morrison, P. D. & Clarke, B. O. Assimilation of Polybrominated Diphenyl Ethers from microplastics by the marine amphipod, Allorchestes compressa. Environ. Sci. Technol. 48, 8127–8134, https://doi.org/10.1021/es405717z (2014).
Rochman, C. M. et al. Policy: Classify plastic waste as hazardous. Nature 494, 169–171 (2013).
Worm, B., Lotze, H. K., Jubinville, I., Wilcox, C. & Jambeck, J. R. Plastic as a persistent marine pollutant. Annu. Rev. Environ. Resour. 42, 1–26, https://doi.org/10.1146/annurev-environ-102016-060700 (2017).
Lavers, J. L. & Bond, A. L. Exceptional and rapid accumulation of anthropogenic debris on one of the world’s most remote and pristine islands. Proc. Nat. Acad. Sci. 114, 6052–6055, https://doi.org/10.1073/pnas.1619818114 (2017).
ABS. Census QuickStats for Cocos (Keeling) Islands, viewed 19 February 2018, http://www.censusdata.abs.gov.au/census_services/getproduct/census/2016/quickstat/90102 (2016).
Misso, M. & MacRae, I. The conservation management of Pulu Keeling National Park: challenges and perspectives. Raff. Bull. Zool. 30, 24–28 (2014).
Kusui, T. & Noda, M. International survey on the distribution of stranded and buried litter on beaches along the Sea of Japan. Mar. Pollut. Bull. 47, 175–179 (2003).
Ribic, C. A., Sheavly, S. B. & Klavitter, J. Baseline for beached marine debris on Sand Island, Midway Atoll. Mar. Pollut. Bull. 64, 1726–1729, https://doi.org/10.1016/j.marpolbul.2012.04.001 (2012).
Schott, F. A., Xie, S. P. & McCreary, J. P. Jr. Indian Ocean circulation and climate variability. Reviews of Geophysics 47, RG1002, https://doi.org/10.1029/2007RG000245 (2009).
Hanvey, J., Lewis, P. J., Crosbie, N., Lavers, J. L. & Clarke, B. O. A review of analytical techniques for quantifying microplastics in sediments. Anal. Methods 9, 1369–1383, https://doi.org/10.1039/C6AY02707E (2017).
Lavers, J. L., Oppel, S. & Bond, A. L. Factors influencing the detection of beach plastic debris. Mar. Environ. Res. 119, 245–251 (2016).
Serra-Gonçalves, C., Lavers, J. L. & Bond, A. L. Global review of beach debris monitoring and future recommendations. Environ. Sci. Technol. (in review).
Cózar, A. et al. Plastic debris in the open ocean. Proc. Nat. Acad. Sci. 111, 10239–10244, https://doi.org/10.1073/pnas.1314705111 (2014).
Andrady, A. L. Microplastics in the marine environment. Mar. Pollut. Bull. 62, 1596–1605, https://doi.org/10.1016/j.marpolbul.2011.05.030 (2011).
PlasticsEurope. Plastics - the facts 2018: an analysis of European plastics production, demand and waste data. (PlasticsEurope Market Research Group, Brussels, Belgium, 2018).
Lambert, S. & Wagner, M. In Freshwater Microplastics: Emerging Environmental Contaminants? (eds Wagner M. & Lambert S.) 1–23 (Springer International Publishing, 2018).
Rillig, M. C. Microplastic in terrestrial ecosystems and the soil? Environ. Sci. Technol. 46, 6453–6454 (2012).
Lavers, J. L. & Bond, A. L. Ingested plastic as a route for trace metals in Laysan Albatross (Phoebastria immutabilis) and Bonin Petrel (Pterodroma hypoleuca) from Midway Atoll. Mar. Pollut. Bull. 110, 493–500, https://doi.org/10.1016/j.marpolbul.2016.06.001 (2016).
Botero, C. M. et al. Litter assessment on 99 Cuban beaches: A baseline to identify sources of pollution and impacts for tourism and recreation. Mar. Pollut. Bull. 118, 437–441, https://doi.org/10.1016/j.marpolbul.2017.02.061 (2017).
Jang, Y. C., Hong, S., Lee, J., Lee, M. J. & Shim, W. J. Estimation of lost tourism revenue in Geoje Island from the 2011 marine debris pollution event in South Korea. Mar. Pollut. Bull. 81, 49–54, https://doi.org/10.1016/j.marpolbul.2014.02.021 (2014).
Carlsen, J. Tourism impacts on small islands: a longitudinal study of community attitudes to tourism on the Cocos (Keeling) Islands. Pac. Tour. Rev. 3, 25–35 (1999).
Farmer, B. & Short, A. 101 Best Beaches, viewed 5 March 2018, https://www.101bestbeaches.com (2018).
Parks Australia. Pulu Keeling National Park: Management plan 2015–2025. (Parks Australia, Canberra, 2015).
Waller, C. L. et al. Microplastics in the Antarctic marine system: An emerging area of research. Sci. Total Environ. 598, 220–227, https://doi.org/10.1016/j.scitotenv.2017.03.283 (2017).
Cózar, A. et al. The Arctic Ocean as a dead end for floating plastics in the North Atlantic branch of the Thermohaline Circulation. Sci. Adv. 3, https://doi.org/10.1126/sciadv.1600582 (2017).
Uneputty, P. & Evans, S. M. The impact of plastic debris on the biota of tidal flats in Ambon Bay (eastern Indonesia). Mar. Environ. Res. 44, 233–242 (1997).
Carson, H. S., Colbert, S. L., Kaylor, M. J. & McDermid, K. J. Small plastic debris changes water movement and heat transfer through beach sediments. Mar. Pollut. Bull. 62, 1708–1713, https://doi.org/10.1016/j.marpolbul.2011.05.032 (2011).
UNEP. Management of wastes in small island developing States. (United Nations Environment Programme, Inter-Agency Committee on Sustainable Development, Geneva, 1998).
Wu, W.-M., Yang, J. & Criddle, C. S. Microplastics pollution and reduction strategies. Front. Env. Sci. Eng. 11, 6, https://doi.org/10.1007/s11783-017-0897-7 (2016).
Our sincere thanks to Tangaroa Blue, the Two Hands Project, Government of Western Australia (Dept. of Environment Regulation), Keep Australia Beautiful, and Sea Shepherd Marine Debris Australia for generously providing accommodation, funding, or logistical support for this project. Samples were collected with approval from the Australian Director of National Parks (permit no. PKNP_2016_2). Assistance in the field was provided by a dedicated group of volunteers from the Two Hands Project (S. Stuckenbrock & P. Sharp), Tangaroa Blue Foundation (especially H. Taylor, M. Wheldon, and C. McCartney), Plastic Free July (R. Prince-Ruiz), Keep Australia Beautiful (M. Maher), the local Cocos community (particularly E. Washer & C. Edwards), and National Parks staff (T. Flores, M. Lenane, I. MacRae, & G. Williams). Finally, our thanks to S. Bin Muzaffar, G. McClelland, C. Ratajczak, J. & D. Rogers, S. Stuckenbrock (Two Hands Project), and the Seychelles Islands Foundation for generously providing photos for Figure 3. Comments from A. Bond, S. Claflin, and two anonymous reviewers improved earlier drafts.