Anthropogenic plastic pollution is a global problem. In the marine environment, one of its less studied effects is the transport of attached biota, which might lead to introductions of non-native species in new areas or aid in habitat expansions of invasive species. The goal of the present work was to assess if the material composition of beached anthropogenic litter is indicative of the rafting fauna in a coastal area and could thus be used as a simple and cost-efficient tool for risk assessment in the future. Beached anthropogenic litter and attached biota along the 200 km coastline of Asturias, central Bay of Biscay, Spain, were analysed. The macrobiotic community attached to fouled litter items was identified using genetic barcoding combined with visual taxonomic analysis, and compared between hard plastics, foams, other plastics and non-plastic items. On the other hand, the material composition of beached litter was analysed in a standardized area on each beach. From these two datasets, the expected frequency of several rafting taxa was calculated for the coastal area and compared to the actually observed frequencies. The results showed that plastics were the most abundant type of beached litter. Litter accumulation was likely driven by coastal sources (industry, ports) and river/sewage inputs and transported by near-shore currents. Rafting vectors were almost exclusively made up of plastics and could mainly be attributed to fishing activity and leisure/ household. We identified a variety of rafting biota, including species of goose barnacles, acorn barnacles, bivalves, gastropods, polychaetes and bryozoan, and hydrozoan colonies attached to stranded litter. Several of these species were non-native and invasive, such as the giant Pacific oyster (Crassostrea gigas) and the Australian barnacle (Austrominius modestus). The composition of attached fauna varied strongly between litter items of different materials. Plastics, except for foam, had a much more diverse attached community than non-plastic materials. The predicted frequency of several taxa attached to beached litter significantly correlated with the actually observed frequencies. Therefore we suggest that the composition of stranded litter on a beach or an area could allow for predictions about the corresponding attached biotic community, including invasive species.
Citation: Rech S, Borrell Pichs YJ, García-Vazquez E (2018) Anthropogenic marine litter composition in coastal areas may be a predictor of potentially invasive rafting fauna. PLoS ONE 13(1): e0191859. https://doi.org/10.1371/journal.pone.0191859
Editor: Christopher A. Lepczyk, Auburn University, UNITED STATES
Received: May 25, 2017; Accepted: January 13, 2018; Published: January 31, 2018
Copyright: © 2018 Rech et al. This is an open access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited.
Data Availability: The FASTA sequences of the analyzed individuals are published in the GenBank database with the accession numbers KY607884-KY607909, KY614195-KY614223, KY628986, KY661434-KY661534, KY683467-KY683511, KY944812-KY944984, KY963587-KY963595, KY986731-KY986745, MF037237-MF037246, MF043915. All other relevant data are within the paper and its Supporting Information files.
Funding: This work was supported by the European Commission [Marie Curie 2014 ITN H2020 AQUAINVAD-ED; grant agreement no. 642197].
Competing interests: The authors have declared that no competing interests exist.
Since plastics have been made available to a broad spectrum of consumers after the Second World War, their global production has risen to 322×109 kg in 2015 . Although plastic production is concentrated in China, Europe, the USA, Canada and Mexico, plastics and recyclable plastic waste, which are not classified as hazardous , are exported internationally [1,3,4], posing a global threat to human health, interests, and ecosystems [2,5]. The pollution by plastic litter has advanced to such a level that today it is present in virtually every environment and every location of the Earth [6,7]. The marine environment is especially affected, as it receives not only direct pollution from sea-based activities, but also land-based plastics [7–9]. Plastic pollution causes the death of a high number of marine animals, as well as severe damages to ecosystems and human health and interests, like tourism, fishing, or leisure activities at beaches [10–13]. Plastics do not degrade naturally but fragment to smaller pieces, which multiplies their abundance . In recent decades, campaigns are being conducted to combat the excessive production and consumption of single-use plastics, for example plastic bags from supermarkets, microbeads in cosmetic products, or PET (Polyethylene terephthalate) beverage bottles (e.g. http://storyofstuff.org/, http://www.beatthemicrobead.org/). Policy changes have been requested after increasing scientific evidence and public awareness about the pollution problem [14,15].
While research and actions on several aspects of the plastic litter problem are steadily advancing, there are still many important aspects that have gained little scientific attention so far. One problem that has received less attention is the role of anthropogenic litter items serving as artificial rafts for non-native and possibly invasive species. Notably, rafting has been mentioned in several publications  and public media, but at present there is no clear understanding of the scale and the underlying processes of this phenomenon. Research priorities include an estimation of its global impact, the localization of natural sink areas, and the identification of high-risk anthropogenic litter items/materials and sources .
Rafting of biota on floating objects, like driftwood, macro algae or volcanic pumice has importantly shaped the species composition of islands [16,18,19]. Floatable litter items of anthropogenic origin greatly enhance the number of stable rafts, particularly in areas where natural vectors are scarce. Anthropogenic litter pollution is estimated to double marine rafting opportunities [16,20] and on some beaches more than 60% of all anthropogenic litter items carried attached organisms . Although the vast majority of anthropogenic litter used as rafts are plastic items, there are also cases of macrobiotic rafting on glass, metal, and paper objects . Notably, a metal gas cylinder encrusted by the stony coral Favia fragum had probably crossed the Atlantic Ocean from the USA to the Netherlands . Another invading coral, Oculina patagonica, is commonly found on submerged metal objects , while some pelagic barnacles are frequently recorded on glass and metal objects . Biofouling was also reported for air-filled glass floats, used in (mainly Japanese) fisheries before plastics became widely available and still afloat in the world´s oceans nowadays [21,24–26].
Differences between materials in the abundance and composition of the micro fauna in early stages of biofouling have been found [27,28]. Particularly, polystyrene seems to carry a higher number of both species and individuals than other types of plastics, which may be due to its higher surface roughness [27,29]. Settlement of individuals of the invasive species Bugula neritina was significantly higher on several plastic surfaces [Polyvinylchloride (PVC), Polypropylene (PP), Polycarbonate (PC), Polyethylene terephthalate (PET) and Polystyrene (PS)] than on glass surfaces, under both field and laboratory conditions, whereas the invasive barnacle Austrominius modestus settled more on glass than on plastic surfaces (tested under field conditions) . In contrast, no significant differences between biofilm composition on PET and glass surfaces were found in another study and object softness, rather than the type of material, was suggested to be an important factor for biota attachment . On the other hand, laboratory experiments and controlled field studies with fixed floaters do not incorporate the buoyancy or floating behaviour of the different materials, which may also influence the biotic colonization by some taxonomic groups [16,27,29,32]. The ability of items to float over long distances depends not only on their buoyancy, but also on their stability and shape, with thinner and more flexible plastic items (like plastic bags and packaging material) sinking faster than thicker and more robust plastic items .
The origin of litter could have an influence in the attached biota. Marine anthropogenic litter stems from various sources, like households, beach-based leisure activities, sea-going activities, industries, and sewage . The contribution of each source to anthropogenic litter has been investigated at many locations [9,35–37], but the main sources of litter rafts with biota are less known. For particular items, macroscopic attached biota has been reported. Examples are lines, ropes, nets and bait pots [38–40], aquaculture and other buoys [39,41], plastic packaging bands used in Antarctic bases and fishing boats , virgin plastic pellets , glass bottles , a gas cylinder reported above , a plastic spool , and tennis shoes and slippers , amongst others. Those reports might point to a higher contribution of litter items originated from sea-based activities such as aquaculture and fisheries. However, this first impression needs to be investigated in depth and on a larger geographic scale.
Floating objects displace along with currents and tides, thus their role in the dispersal of attached species may be important. Rafting on marine litter has been suggested to be involved in regional dispersal of several invertebrates [23,45,46]. For example, juveniles of the bivalve Pinctada imbricata and adults of Isognomon bicolor, which are considered invasive in Brazil, were found attached to anthropogenic litter for the first time at the Uruguayan coast, where they are regarded as potentially invasive as well [38,44]. In the Spanish part of the Bay of Biscay, several alien invasive species are registered , some of which are already known to attach to floating anthropogenic litter in other regions . The invasive pygmy mussel Xenostrobus securis was first reported in the Bay of Biscay in 2012, attached to natural as well as plastic and metal objects, among others . The invasive Crassostrea gigas and the exotic Ostrea stentina were also found attached to artificial materials on regional ports . According to EU Regulation (EU) No 1143/2014 there are about 12,000 alien species in European countries, of which 10–15% are regarded as invasive and pose a serious threat to the environment and human interests . Such species can be regarded as ecosystem infestations or epidemics, with the anthropogenic litter carrying it, being infested vectors.
Given the concern of anthropogenic beach litter our goal was to determine whether the composition of anthropogenic beach litter can predict macrobiotic communities attached to stranded litter items in a region. In answering this goal, we had three main objectives. First, determine which native, non-native, and potentially invasive macroscopic animal species are present on stranded anthropogenic litter items. Second, determine the principal material and sources of the infested vectors. Third, test if the occurrence of a certain species/ taxon can be predicted based on the general litter composition at a beach or a coastal area.
Material and methods
No specific permissions were required for sampling because all the organisms analysed in this study were obtained from litter items. Those items must be removed from the beaches as they are not natural substrate. The field studies did not involve endangered or protected species.
To address our main research goal and objectives, we evaluated the coast of Asturias region in the south-central Bay of Biscay (north of Spain). The coast is under the influence of currents going eastwards , with a boundary in Cape Peñas (central cape marked in Fig 1) that divides the coast into the colder west and the warmer east zone . The sampling sites cover a wide spectrum of factors that may influence marine litter distribution, like land-use, distance to human settlements, industry, and geomorphology [53–55]. There are two international cargo ports in the sampled area (Gijón and Avilés), as well as shellfish aquaculture areas in two estuaries (Ría del Eo and Villaviciosa). There are several villages and two bigger cities, Gijón and Avilés, along the coastline in Spain (Fig 1). The central area of the region is strongly polluted by industrial activities [56,57], which are mainly based in the area of Avilés. Among the several rivers discharging into the Cantabrian Sea in the sampling area, the rivers Nalón, Navia, Sella, and Esva have the largest stream basins (Fig 1).
Sampling sites are numbered and are specified in Table 1.
Beach litter samplings and analysis
A total of fifteen sandy beaches, covering a linear distance of 190 km along the Cantabrian coastline in Asturias, Spain, were sampled in a 26-day period between February and March 2016 (Fig 1). Each beach was sampled one day during low tide and daylight. We conducted two independent surveys: 1) A sampling of fouled beached items along the whole area of each beach to test if there are material-related differences in the taxonomic composition of the macro fauna attached to beached litter, and 2) a count and material-based classification of beached anthropogenic litter in general (both fouled and non-fouled) in a smaller standardized area. Please see the supporting figure for a graphic sampling scheme (S1 Fig).
Survey 1: The whole area of each beach was searched for anthropogenic litter items with attached macrofauna (visible fauna). Each of the items found was photographed with a Motorola Moto G3 camera (resolution 13 MP) next to a size reference (a finger or any other object of known dimensions) and given an identification code. The type of object (e.g. buoy, fragment, rope; Table 2), type of material and colour was noted down for each item. We did not only classify the fouled items by material as plastic and non-plastic (e.g. metal, paper, glass; abbreviated NPl), but moreover separated plastic items in three categories, based on their stability and surface roughness: Hard plastics (abbreviated HPl), synthetic foams (e.g. Polystyrene; abbreviated foams), and other plastics (abbreviated OPl). Litter items found on the beaches were associated to three sources: Sewage, Fishing/Aquaculture and Household/Leisure. All objects or fragments that were not identifiable or not attributable to one of the categories above were classified as N/A (not attributable; Table 2).
Attached biota was visually assigned to the most specific distinguishable taxonomic group based on morphology and the number of individuals (colonies for bryozoans and hydrozoans) was counted and noted down for each group. A representative number of individuals (≤ 50) of each morphotype was detached from each litter item using forceps and a scraper. They were stored in commercially available hard plastic sampling pots in 50–500 ml (depending on the size and number of stored individuals) of ethanol 80% for further analysis and labelled with the identification code of the corresponding litter item. Some smaller litter items and items of complex shapes were stored in plastic bags and taken to the laboratory for measurement, while the dimensions of bigger items and of items with a simple shape were estimated based on the photos, and the surface area was calculated for each item. The native distribution area and the potential invasive capacity of each attached species were examined from relevant current literature [49,58–62] and databases, namely the global invasive species database (GISD, http://www.issg.org/database) and World Register of Marine Species .
Survey 2: A standardized quantification and characterization of anthropogenic beach litter (not restricted to fouled objects) was done at all beaches, except for Figueras, Silencio, and S. Juan de Nieva (for location of the beaches see Fig 1). On the other 12 beaches, of similar sandy granulation, standardized litter counts were conducted in 2 horizontal transects at every beach, each consisting of four adjoined quadrats of 3×3m2 each. The two transects were placed parallel to the water line, the upper transect along the most recognizable higher tideline, and the lower transect along the most recognizable lower tideline, to account for possible differences in litter composition with shore height  and to include both recently stranded litter (lower tide line) and litter stranded less recently (most recognizable high tide line). The area for the counts was defined at every beach after visual inspection, where accumulation of flotsam (both natural and anthropogenic) was representative of the whole beach (i.e. neither exceptionally high, nor exceptionally low, relating to the rest of the beach). This method was chosen over a random approach to avoid bias due to the small transect area (36 m2 per transect) and the limited number of replicates (two transects per beach), as anthropogenic litter and other flotsam is often distributed heterogeneously along the beach [64,65].
The sampling quadrats were defined with a tape measure and their outlines were marked in the sand using a stick. In each quadrat all macro litter (items and fragments bigger than 1.5 cm) was inspected and sorted by object type (e.g. lid, drinking straw, fragment) and material. Then the number of items of each combination of object type and material (e.g. hard plastic lids, metal lids, paper fragments; Table 2) was counted and noted down for each quadrat in situ. All items and fragments were then assigned to a source category. The material categories and source categories used for classification were the same as described above for Survey 1.
DNA was extracted from a small piece of tissue (about 2×2 mm) using Chelex (Bio Rad BT Chelex® 100 Resin). For DNA extraction from very small individuals with non-tissue parts, like shells (e.g., molluscs), the complete individual was treated with E.Z.N.A® Mollusc DNA Kit. PCRs were performed with the universal primers detailed in Table 3. When necessary, the PCR product was purified using EURx® Gene Matrix Agarose Out DNA Purification Kit. DNA sequencing was performed by Macrogen Europe, Amsterdam, Netherlands.
Sequence editing and alignment was done using the freeware BIOEDIT Version 7.2.5 . From the DNA Barcode the species was assigned using the BLAST database  and the best match with the maximum hit score (minimum 97% nucleotide identity). Phylogenetic trees for confirming species assignation were built with MEGA 7  from the sequences obtained in this study and reference sequences of voucher specimens taken from GenBank (https://www.ncbi.nlm.nih.gov/nucleotide/), based on the maximum likelihood reconstruction method, with 500 bootstraps.
Analysis of rafting fauna was done at regional level after confirming large dispersal capacity of the species found. Comparison among materials for the attached biotic community was done using the number of individuals per object as a standardized unit. To compare among communities we classified biota as goose barnacles, acorn barnacles, bryozoan and hydrozoan colonies, decapods, molluscs and polychaetes.
Composition and sources of beach litter found along the main accumulation lines (from standardized samplings) were compared to composition and sources of the litter items used as rafts, employing the PERMANOVA function of PRIMER 6 software [69,70]. PERMANOVA results were regarded as statistically significant at a p-value of ≤ 0.05. The contribution of each litter source to the differences was tested by SIMPER (= similiarity percentage) analysis. Both analyses were based on Bray- Curtis similarities.
The abundance of anthropogenic litter was compared between and within beaches using boxplots, showing the mean value, quartiles and variability for each beach. Heterogeneity in composition and abundance of anthropogenic beach litter in general, and of items used as artificial rafts by biota, were tested using PERMANOVA, based on Euclidean distances. Multidimensional scaling (MDS) based on Bray-Curtis similarities was used to graphically represent the grouping of the sampled beaches, based on dominant litter material: beaches dominated by hard plastics (termed HPl–dominant), beaches dominated by other plastics (termed OPl-dominant), and beaches with mixed litter composition and less than 25 litter items in the standardized sampling area (> 0.35 items×m2; termed Mix). These analyses were done for the subsample of beaches where standardized litter analysis was carried out.
Since litter composition and litter with rafting biota in a beach were independent datasets, a correlation approach was followed to determine if rafting biota in a beach area can be inferred from litter composition. Biota expectation from litter composition was estimated for 12 beaches based on the characteristic community profile of the beaches’ litter materials. The goodness of adjustment between estimated and observed taxa was tested using a correlation approach, based on Spearman´s rank correlation coefficient and the linear correlation was graphically illustrated in a scatter plot.
Where TB (x) is the expected number of individuals for taxon B on beach x, fM(i) is the frequency of litter material i (HPI, OPI, Foams or NPI) found on beach x, fTBM (i, r) is the frequency of taxon B on material i in the region r and Nt (x) is the total number of rafting biota found on beach x.
Standardized quantification and categorization of anthropogenic beach litter
All the sampled beaches were polluted with anthropogenic litter. The mean abundance of anthropogenic litter ranged from 0.17 ± 0.21 items×m-2 (Barayo) to 5 ± 3.95 items×m-2 (Xivares). The abundance of anthropogenic litter varied strongly, not only between beaches, but also between quadrats within beaches, indicating a patchy distribution (Fig 2). The composition of beached litter in the region was not significantly different of the composition of litter rafts with biota (Table 4: PERMANOVA 1).
Data are presented in a box-and whisker plot, with the middle box representing 50% of the values and the upper and lower whiskers representing the values outside of the 50% range. The median and outliers are indicated by a middle line and a circle (◦), respectively. Litter items were counted in a standardized area at each beach.
The highest pollution levels were found in direct proximity to the coastal region´s main industrial and populational centers, Gijón (Xivares beach: 5 ± 3.95 items×m-2) and Avilés (Salinas and Xagó beaches: 2 ± 1 items×m-2 and 2.7 ± 1.9 items×m-2, respectively) both of which have a national port and a sewage treatment plant, as well as at the river mouth of the Navia river, in proximity to a fishing port and a marina (Navia beach: 4.3 ± 4 items×m-2, see map in Fig 1). The abundance of beach litter at the other sampled beaches along the Cantabrian coastline seems to reflect the geomorphology of the coastline and its exposure to the prevailing eastward surface current, with a maximum peak in the northernmost Cape Peñas: Pollution rose from Barayo eastwards up to Xagó, situated on the western side of Cape Peñas, which is more exposed to the eastward surface current, and subsequently declined on the eastern side of the cape, which is more protected from the prevailing currents (Fig 1, Fig 2).
Plastics (including foams) made up the highest share of anthropogenic litter on all beaches (75% to 100%), except at Andrín beach, where non-plastic litter was more abundant (55%; Table 5). The sampled beaches differed significantly from each other regarding both abundance and composition of anthropogenic litter (Table 4: PERMANOVA 2). Beaches were classified based on the prevalent litter material, forming three groups in the sampling area that significantly differed from each other (Table 4: PERMANOVA 3) and could be graphically distinguished by multidimensional scaling (MDS; Fig 3). The treatment of beaches in categories facilitated further analyses.
HPl = hard plastics, OPl = Other plastics, Mix = beaches with mixed litter composition and less than 25 litter items in the standardized sampling area (> 0.35 items×m2).
Most anthropogenic litter items found on the sampled beaches could not be attributed to a source, as many of them were small fragments. For the objects that could be likely assigned to a source, most were sewage-related. At Xagó and Penarronda fishing and aquaculture activities were also important sources of beached litter (Table 5).
Anthropogenic litter items used as rafts
A total of 94 litter objects with attached fauna were found on the surveyed beaches (Fig 4). High prevalence of hard plastics and plastics in general (71 ± 30% and 98 ± 6%, respectively), was found among rafting vectors, while the share of non-plastic objects was very low (2 ± 6%, Table 5). In fact, only five non-plastic objects with attached fauna were found on three beaches: three glass bottles (one with a metal cap), one piece of processed wood, and one sandal, which was counted as nonplastic as the attached organism was found on its textile part. Within the plastics the share of other plastics tended to be less abundant in rafting vectors than in general beach litter (17 ± 24% versus 27 ± 26%), while the share of foams was rather similar in rafting vectors and general litter (9 ± 12% and 9 ± 8%, respectively). The standard deviation between beaches however was high (Table 5).
a) Hard plastic object with oyster, polychaetes and acorn barnacles b) PET bottle with goose barnacles c) float of fishing net with bryozoan colonies and polychaetes, d) shoe sole with oyster, snail and acorn barnacles, e) duct tape with goose barnacles.
The main sources of fouled litter items were significantly different from the main sources of other non-fouled beach litter (Table 5, Table 4: PERMANOVA 4). SIMPER showed that the source category with the highest contribution to the differences (after unidentified litter NA, contribution: 37%) was Fishing and Aquaculture (contribution: 34%; Table 6). This particularly important role of fishing/aquaculture related litter for the rafting of biota in the sampling area was especially noticeable at the beaches of Xagó, Navia and Rodiles, where all the identifiable items with attached biota were from this source (Table 5). Leisure and household-related items also had a high share in rafting vectors. Items from this source were found on six beaches and consisted of 20 shoes/sandals and one cosmetic container. Leisure and household was the main litter source for Andrín beach (Table 5). On the other hand, sewage-related litter made up to 11% (mean) of all anthropogenic beach litter, although none of the biota rafts was related to this source (Tables 5 and 6).
Fauna attached to anthropogenic rafts
More than 3300 individuals (or colonies for bryozoans and hydrozoans) were found attached to the litter objects found in the beaches surveyed (Table 7). With genetic analyses, more than 400 DNA barcodes were obtained, identifying 23 species of attached animals from four phyla (Fig 5, Table 7). The Barcodes were submitted to GenBank database, where they are available with the Accession Numbers KY607884-KY607909, KY614195-KY614223, KY628986, KY661434-KY661534, KY683467-KY683511, KY944812-KY944984, KY963587-KY963595, KY986731-KY986745, MF037237-MF037246, MF043915. Crustaceans (Phylum Arthropoda) such as Lepadidae (Goose barnacles), Balanidae and Verrucidae (Barnacles), and the amphipod Caprella andreae were the most abundant animals in this study (> 1000 individuals; Table 7), followed by annelids, which all belonged to the family Serpulidae (~700 individuals). Hydrozoan and bryozoan colonies were also very numerous (~400) and might be underestimated in this study, due to the difficulty of counting them individually. As most of the colonies were dried out and in a state of advanced degradation, DNA was degraded in most cases and only two species of Cnidarians were identified from genetic techniques: Bougainvillia muscus and Obelia dichotoma. The animals found in the present study were morphologically diverse and it is possible that the hydrozoan and bryozoan colony group actually included more species and taxa. Around 100 molluscs were found attached to anthropogenic litter items, with the majority of them belonging to the genus Mytilus, followed by the oysters Crassostrea gigas and Ostrea stentina. Moreover, we found two species of gastropods: the marine species Gibbula umbilicalis, and the land snail Helix aspersa. For the latter, which is terrestrial, taking into account its common occurrence in the sampled area, it seems likely it did not arrive on the beach by rafting but from the land.
a) molluscs, b) crustaceans, c) polychaetes, d) hydrozoans. Frame = Species not native to the study area; * = Species listed in the invasive species database; + = Terrestrial species; # = reference without species voucher.
Most of the rafting animals were native to the study region or recognized as cosmopolitans (Lepadidae). Five species were not native: Crassostrea gigas, Ostrea stentina, Austrominius modestus, Serpula columbiana, and Neodexiospira sp. C. gigas and A. modestus are listed in the global invasive species database (GISD, http://www.issg.org/database). The native M. galloprovincialis and the terrestrial species H. aspersa are included in GISD as well. The species identification provided by BLAST was confirmed from phylogenetic analysis after clustering analyses including voucher species references from GenBank (Fig 5).
Regarding the type of material carrying each species, differences occurred in this region between taxonomic groups. While molluscs like Mytilus and Crassostrea were found on all types of anthropogenic litter, Polychaetes were exclusively found on hard plastic and other plastic items. Barnacles, like Austrominius, were found on all materials except foams, but were most important on hard plastic items. Therefore, each type of litter seemed to exhibit a particular profile of attached biota (Fig 6). Foams carried almost exclusively goose barnacles (99%) and, to a much lesser extent, molluscs (1%). Non-plastic items contained a similar biota profile, with an additional small share of barnacles (2%). Hard plastic and other plastic objects on the other hand carried a broad spectrum of attached taxa. On hard plastic items the main share of attached biota were barnacles (37%), polychaetes (31%) and bryozoan colonies (18%). They also carried goose barnacles, molluscs, and decapods (7%, 4%, and 2%, respectively). On other plastics, the main share of attached biota was made up of polychaetes (66%) and goose barnacles (23%), while barnacles, bryozoan colonies, and molluscs were less common (5%, 5%, and 2%, respectively). Differences between materials regarding the biota profile were indeed highly statistically significant (Table 4: PERMANOVA 5).
Inference of litter-related biotic community from beach litter composition
We tested if the composition of an area´s macrobiotic communities attached to stranded litter items can be predicted based on its composition of anthropogenic beach litter, using the data of the 12 beaches where standardized litter counts have been conducted. The predicted frequency of attached biota of several taxa, estimated from litter composition significantly correlated with the actually observed frequencies on both sides of cape Peñas (Western side: Spearman`s rank correlation coefficient (R) = 0.498; p = 0.002; Eastern side: R = 0.629; p = 0.027), as well as for the whole sampling area (R = 0.565; p < 0.001; Fig 7). For the exact figures of estimated and observed biota, please see the Supporting table (S1 Table).
In this study six rafting species were recorded for the first time on anthropogenic beach litter: Verruca stroemia, Ostrea stentina, Gibbula umbilicalis, Spirobranchus taeniata, Serpula columbiana, and Neodexiospira sp. Although many rafting species have been documented on anthropogenic marine litter during the last years  and the recent discovery of 289 living marine species, which had crossed the Pacific Ocean on objects detached by a tsunami, showed the importance of floating marine litter as a rafting vector , many rafting species are not known or reported yet and knowledge of the actual dimension and impact of marine litter rafting is still far from complete. The finding of Perforatus perforatus on anthropogenic litter is particularly interesting, as large numbers of this species, probably originating from NW Spain, have been found on beach litter in Wales . A similar range expansion might also occur for invasive barnacles, such as Austrominius modestus.
Besides the species listed above, most of the taxa found in our study are known rafters and have already been found on anthropogenic litter (floating or stranded) in other regions . The predominance of cosmopolitan stalked barnacles among marine rafters is a common phenomenon, with the small and light-weight species L. pectinata and D. fascicularis being especially suited for the colonization of smaller rafts [16,23]. Lepas barnacles may influence the rafting community on plastic debris: the ratio Lepas cover /surface area was found positively correlated with the diversity of mobile rafters, while negatively with sessile rafters’ diversity, in a study by Gil and Pfaller (2016). Our results were concordant with this study, since the debris dominated by goose barnacles contained a very low diversity of other sessile rafting species (only molluscs and acorn barnacles), while materials with a lower share of goose barnacles exhibited a relatively diverse attached community (Fig 6). Another common rafter found in this study was the amphipod Caprella andreae. The genus Caprella is generally adapted to rafting because of their reduced abdominal appendages, and C. andreae is the only known obligate rafter in its genus .
Two non-native oysters were found on Figueras beach, close to the region´s only active site of mollusc aquaculture. While C. gigas is a recognized invasive species and quite common along the Asturian coast, O. stentina has only been reported in the region once before, in the port of Avilés . These two findings with a linear distance of less than 100 km may indicate that this species is already established in the region, and may use anthropogenic litter for dispersal beyond the range of its propagules. The results show a link between the composition of anthropogenic beach litter in an area and the frequency of several taxa of fauna attached to stranded litter objects. This finding should be valid for a broad range of coastal regions, as it is based on taxa composition and general litter materials, rather than on particular species and/or litter items, which may vary more strongly between regions.
The strong prevalence of (hard) plastic rafts confirms the results of previous studies . The very low share of non-plastic rafts may be due to the fact that the majority of these items are not buoyant and/or of very little persistence. Plastic foams, despite being highly buoyant and having rather rough surfaces, which facilitate initial colonization , are less stable and persistent than hard plastics . This may explain their low share amongst rafting vectors. For the potential sources of litter with rafting biota, there was a high share of unidentified items but still some important conclusions may be drawn from our results. Firstly, rafting vectors could be identified and attributed to a source much more frequently than other items of anthropogenic beach litter. The reason is probably that small plastic fragments whose source cannot be identified, which are quite common in beach litter in general, are too small for serving as rafts. Fazey and Ryan (2016) proposed size and buoyancy as predictors of dispersal distance for floating debris . Given that biofouling reduces an item´s buoyancy, smaller items will sink faster than bigger items and travel much smaller distances . This phenomenon may also explain why sewage litter, although quite abundant on beaches, was never found as a rafting vector. Rafting vectors from fishing and aquaculture, as well as other sea-based activities, have been reported in other studies [41,76]. An explanation for the high occurrence of items from these sources among rafts may be their buoyancy, stability, size and persistence. 12 of the 23 fishing/aquaculture-related rafting vectors were buoys or netfloats, which are obviously highly buoyant and seven were grids or cages made from stable plastic wire, which are big items with a rather small surface/volume ratio. The other four rafts were rather big items (min. 10x2x2 cm3) made from hard plastics. Leisure and household-related litter is quite difficult to define, because many of the items which might stem from this source might as well stem from sea-based sources (e.g. PET bottles). These items have not been assigned to a source category, so perhaps the actual contribution of this source was higher. Shoes and sandals, clearly sourced household or leisure, are known to be able to float over large distances and have already been reported as rafting vectors [44,77–79].
The patchy abundance of beach litter, with high variances both within and between beaches was congruent with the situation reported in many other studies [7,9,80]. Although comparisons of abundance between different locations, observers, and studies with different approaches (regarding for example transect size, choice of strand lines and/or ground between strand lines sampled, minimum size of items counted, biological material present in the sampled area etc.) are rather difficult [7,65,81], the abundance of beach litter found in this study falls within the same range as reported for many other sampling sites around the globe. As this study focuses on stranded litter which had already been at sea, the litter counts were conducted in transects targeting tidelines, where natural and anthropogenic litter is deposited by the sea. Targeting areas of litter accumulations, the results are likely overestimating the total litter abundances of the sampled beaches, and are not representative for the whole area of the beaches. They do however allow for comparisons of stranded litter abundances between the beaches sampled during this study, where the same method was used for all beaches.
Plastics (including plastic foams) are reported as the main constituents of beach litter in most studies . According with that, the share of plastics found on beaches along the Cantabrian coast (present study) was rather high. Source attribution of the stranded litter items was a difficult task because the majority of items could not be clearly related to a litter category, either because the item could stem from several sources, or because the item was not identifiable (i.e. fragments). Notwithstanding it, our results indicate that sewage-related litter is a problem in the sampled area. In fact, waste-water discharging pipelines and accumulations of preproduction pellets in the sand below such pipelines were noted on several of the sampled beaches (personal observation SR), but did not enter in the present study due to their small size. Fishing and aquaculture have also been identified as important litter sources in the sampling area. This finding is consistent with the fact that pollution by lost or discarded fishing gear is a common problem in the world’s seas (including the benthos) and on beaches [37,82–84]. There is a high activity of small-scale fishery, with 19 fishing ports along Asturias coastline and a large area of fishing grounds near- and off-shore, plus one active site of mollusc aquaculture (mainly oysters) near Figueras, and several crustacean ponds (http://www.sigmarinoasturias.es/).
The exposure to the prevalent currents may make the sampling area a sink for anthropogenic floating litter and attached biota from other areas. In fall and winter, the sampling area is dominated by a warm poleward surface current, referred to as ‘Navidad’, which enters near Cape Finisterre and moves eastward along the Cantabrian shelf and slope . As the samplings presented in this study were conducted from mid-February to mid-March, it could be assumed that the overall accumulation pattern, particularly the increase of litter abundances from more western beaches towards the tip of Cape Peñas, was driven by this current. On the eastern side of cape Peñas, sediments are transported from the coastal currents to the beaches . This transport may explain the observed abundances of litter on these beaches, which are not directly exposed to the prevalent current. Apart from this main driver, there seems to be an effect of rivers in the area, contributing to the high litter abundance on the beaches Navia and Xivares. Both are situated at the mouth of rivers (Rio Navia and Rio Aboño, respectively). Riverine influence was also reflected in the relatively high share of sewage-linked litter on both beaches.
Although the present study clearly showed the relation between anthropogenic beach litter composition and attached fouling biota in a coastal area, it had some limitations. The samplings were restricted to one geographic area (the south-central Bay of Biscay) and season (february to march), and each beach was sampled only once. Moreover, our study concentrated on stranded anthropogenic litter and did not include litter which was still floating in the water. Thereby we ensured to sample only taxa/species which are still present after a beaching event and might therefore pose a risk of invasion. On the other hand, it should be considered that the biota found on beach litter in this study probably do not represent the complete macrobiotic rafting community of the respective items before the beaching event, as beached litter is often biased towards sessile biota .
In summary, the results presented here give several important insights in the mechanisms on biota rafting on anthropogenic marine litter. Plastic items, except for foams, house a much more diverse biota community than non-plastic items and foams, which may be due to their stability and buoyancy. Several non-native and invasive species were present on litter items along the sampled beaches. Aquaculture and fishing activities were a major source of biota rafts, while sewage discharge was the most important source of all anthropogenic beach litter in the study region. We found that the frequency of a specific taxon of rafting biota in a coastal area may be predicted based on each litter material’s characteristic biota profile and the beaches’ litter composition. This approach, after refined and tested from more regions, could serve as a simple and cost-efficient tool for risk assessment in the future.
- 1. PlasticsEurope. Plastics—the Facts 2016. An analysis of European plastics production, demand and waste data. 2016;38.
- 2. Rochman CM, Browne MA, Halpern BS, Hentschel BT, Hoh E, Karapanagioti HK, et al. Policy: Classify plastic waste as hazardous. Nature. 2013;494(7436):169–71. pmid:23407523
- 3. Regulation (EU) No 1418/2007. COMMISSION REGULATION (EC) No 1418/2007 of 29 November 2007 concerning the export for recovery of certain waste listed in Annex III or IIIA to Regulation (EC) No 1013/2006 of the European Parliament and of the Council to certain countries to which the OEC. Off J Eur Union. 2007;(1418):6–52.
- 4. Velis CA. Global recycling markets—plastic waste: A story for one player–China. Int Solid Waste Assoc—Glob Waste Manag Task Force. 2014;1–66.
- 5. Kühn S, Bravo Rebolledo EL, van Franeker JA. Deleterious Effects of Litter on Marine Life. In: Bergmann M, Gutow L, Klages M, editors. Marine Anthropogenic Litter. Cham: Springer International Publishing; 2015. p. 75–116.
- 6. Barnes DKA, Galgani F, Thompson RC, Barlaz M. Accumulation and fragmentation of plastic debris in global environments. Philos Trans R Soc Lond B Biol Sci. 2009;364(1526):1985–98. pmid:19528051
- 7. Galgani F, Hanke G, Maes T. Global distribution, composition and abundance of marine litter. In: Bergmann M, Gutow L, Klages M, editors. Marine Anthropogenic Litter. 2015. p. 29–56.
- 8. Araújo MCB, Costa MF. An analysis of the riverine contribution to the solid wastes contamination of an isolated beach at the Brazilian Northeast. Manag Environ Qual An Int J. 2007;18(1):6–12.
- 9. Rech S, Macaya-Caquilpán V, Pantoja JF, Rivadeneira MM, Jofre Madariaga D, Thiel M. Rivers as a source of marine litter–A study from the SE Pacific. Mar Pollut Bull. 2014;82(1–2):66–75. pmid:24726186
- 10. Gregory MR. Environmental implications of plastic debris in marine settings—entanglement, ingestion, smothering, hangers-on, hitch-hiking and alien invasions. Philos Trans R Soc Lond B Biol Sci. 2009;364(1526):2013–25. pmid:19528053
- 11. Newman S, Watkins E, Farmer A. he economics of marine litter. In: Bergmann M, Gutow L, Klages M, editors. Marine Anthropogenic Litter. 2015. p. 367–94.
- 12. Gall SC, Thompson RC. The impact of debris on marine life. Mar Pollut Bull. 2015;92(1–2):170–9. pmid:25680883
- 13. Galloway TS. Micro- and Nano-plastics and Human Health. In: Bergmann M, Gutow L, Klages M, editors. Marine Anthropogenic Litter. 2015. p. 343–66.
- 14. Clapp J, Swanston L. Doing away with plastic shopping bags: international patterns of norm emergence and policy implementation. Env Polit. 2009;18(3):315–32.
- 15. Doughty R, Eriksen M. The Case for a Ban on Microplastics in Personal Care Products. Tulane Environ Law J. 2015;27(277):277–98.
- 16. Kiessling T, Gutow L, Thiel M. Marine litter as habitat and dispersal vector. In: Bergmann M, Gutow L, Klages M, editors. Marine Anthropogenic Litter. 2015. p. 141–80.
- 17. Rech S, Borrell Y, García-Vazquez E. Marine litter as a vector for non-native species: What we need to know. Mar Pollut Bull. 2016;113:40–3. pmid:27587232
- 18. Nikula R, Spencer HG, Waters JM. Passive rafting is a powerful driver of transoceanic gene flow. Biol Lett. 2012;9(1):20120821. pmid:23134782
- 19. Fraser CI, Nikula R, Waters JM. Oceanic rafting by a coastal community. Proc R Soc B Biol Sci. 2011;278(1706):649–55.
- 20. Barnes DKA. Biodiversity: Invasions by marine life on plastic debris. Nature. 2002;416(6883):808–9. pmid:11976671
- 21. Hoeksema BW, Roos PJ, Cadée GC. Trans-Atlantic rafting by the brooding reef coral Favia fragum on man-made flotsam. Mar Ecol Prog Ser. 2012;445:209–18.
- 22. Fine M, Zibrowius H, Loya Y. Oculina patagonica: A non-lessepsian scleractinian coral invading the Mediterranean sea. Mar Biol. 2001;138(6):1195–203.
- 23. Whitehead TO, Griffiths C, Biccard A. South African pelagic goose barnacles (Cirripedia, Thoracica): substratum preferences and influence of plastic debris on abundance and distribution. Crustaceana. 2011;84(5):635–49.
- 24. Jokiel PL. Coral Reefs Long Distance Dispersal of Reef Corals by Rafting. Coral Reefs. 1984;3:113–6.
- 25. Dell R. The oceanic crab Pachygrapsus marinus (Rathbun) in the South-West Pacific. Crustaceana. 1964;7(1):79–80.
- 26. Newman WA. Lepadids From the Caroline Islands (Cirripedia Thoracica). Crustaceana. 1972;22(1):31–8.
- 27. Carson HS, Nerheim MS, Carroll KA, Eriksen M. The plastic-associated microorganisms of the North Pacific Gyre. Mar Pollut Bull. 2013;75(1–2):126–32. pmid:23993070
- 28. Zettler ER, Mincer TJ, Amaral-Zettler LA. Life in the ‘plastisphere’: Microbial communities on plastic marine debris. Environ Sci Technol. 2013;47(13):7137–46. pmid:23745679
- 29. Bravo M, Astudillo JC, Lancellotti D, Luna-Jorquera G, Valdivia N, Thiel M. Rafting on abiotic substrata: Properties of floating items and their influence on community succession. Mar Ecol Prog Ser. 2011;439:1–17.
- 30. Li HX, Orihuela B, Zhu M, Rittschof D. Recyclable plastics as substrata for settlement and growth of bryozoans Bugula neritina and barnacles Amphibalanus amphitrite. Environ Pollut. 2016;218:973–80. pmid:27569057
- 31. Oberbeckmann S, Osborn AM, Duhaime MB. Microbes on a bottle: Substrate, season and geography influence community composition of microbes colonizing marine plastic debris. PLoS One. 2016;11(8):1–24.
- 32. Goldstein MC, Carson HS, Eriksen M. Relationship of diversity and habitat area in North Pacific plastic-associated rafting communities. Mar Biol. 2014;161(6):1441–53.
- 33. Ryan PG. The importance of size and buoyancy for long-distance transport of marine debris. Environ Res Lett. 2015;10(8):84019.
- 34. Law KL. Plastics in the Marine Environment. Ann Rev Mar Sci. 2017;9:205–9. pmid:27620829
- 35. Browne MA. Sources and pathways of microplastics to habitats. In: Bergmann M, Gutow L, Klages M, editors. Marine Anthropogenic Litter. 2015. p. 229–44.
- 36. Williams AT, Simmons SL. Estuarine litter at the river/beach interface in the Bristol Channel, United Kingdom. J Coast Res. 1997;13(4):1159–1165.
- 37. Liu T-K, Kao J-C, Chen P. Tragedy of the unwanted commons: Governing the marine debris in Taiwan’s oyster farming. Mar Policy. 2015;53:123–30.
- 38. Marques RC, Breves A. First record of Pinctada imbricata Röding, 1798 (Bivalvia: Pteroidea) attached to a rafting item: a potentially invasive species on the Uruguayan coast. Mar Biodivers. 2014;45(2):333–7.
- 39. Farrapeira CMR. Invertebrados macrobentônicos detectados na costa brasileira transportados por resíduos flutuantes sólidos abiogênicos. Rev Gestão Costeira Integr. 2011;11(1):85–96.
- 40. Holmes AM, Oliver PG, Trewhella S, Hill R, Quigley DT. Trans-Atlantic rafting of inshore Mollusca on Macro-Litter: American molluscs on British and Irish shores, new records. J Conchol. 2015;42(1):1–9.
- 41. Astudillo JC, Bravo M, Dumont CP, Thiel M. Detached aquaculture buoys in the SE Pacific: Potential dispersal vehicles for associated organisms. Aquat Biol. 2009;5(3):219–31.
- 42. Barnes DKA, Fraser KPP. Rafting by five phyla on man-made flotsam in the Southern Ocean. Mar Ecol Prog Ser. 2003;262:289–91.
- 43. Gregory MR. Accumulation and distribution of virgin plastic granules on New Zealand beaches. New Zeal J Mar Freshw Res. 1978;12(4):399–414.
- 44. Breves A, Scarabino F, Carranza A, Leoni V. First records of the non-native bivalve Isognomon bicolor (C. B. Adams, 1845) rafting to the Uruguayan coast. Check List. 2014;10(3):684–6.
- 45. Serrano E, Coma R, Ribes M, Weitzmann B, Garcia M, Ballesteros E. Rapid Northward Spread of a Zooxanthellate Coral Enhanced by Artificial Structures and Sea Warming in the Western Mediterranean. PLoS One. 2013;8(1).
- 46. Davidson TM. Boring crustaceans damage polystyrene floats under docks polluting marine waters with microplastic. Mar Pollut Bull. 2012;64(9):1821–8. pmid:22763283
- 47. Boletín Oficial del Estado (BOE). Real Decreto 630/2013, de 2 de agosto, por el que se regula el Catálogo español de especies exóticas invasoras. 2013;56764–86.
- 48. Adarraga I, Martínez J. First record of the invasive brackish water mytilid Limnoperna securis (Lamarck, 1819) in the Bay of Biscay. Aquat Invasions. 2012;7(2):171–80.
- 49. Pejovic I, Ardura A, Miralles L, Arias A. DNA barcoding for assessment of exotic molluscs associated with maritime ports in northern Iberia. Mar Biol Res. 2016;12(2):851–61.
- 50. Regulation (EU) No 1143/2014. Regulation (EU) No 1143/2014 of the European Parliament and of the Council of 22 October 2014 on the prevention and management of the introduction and spread of invasive alien species. Off J Eur Union. 2014;2014(1143):35–55.
- 51. Garcia-Soto C, Pingree RD, Valdés L. Navidad development in the southern Bay of Biscay: Climate change and swoddy structure from remote sensing and in situ measurements. J Geophys Res. 2002;107(C8):1–29.
- 52. Lavín A, Valdés L, Sánchez F, Abaunza P, Forest A, Boucher J, et al. The Bay of Biscay: the encountering of the ocean and the shelf. In: Robinson AR, Brink KH, editors. The Sea. 2006. p. 933–1002.
- 53. Araújo MCB, Costa MF. Visual diagnosis of solid waste contamination of a tourist beach: Pernambuco, Brazil. Waste Manag. 2007 Jan;27(6):833–9. pmid:16842985
- 54. Carson HS, Lamson MR, Nakashima D, Toloumu D, Hafner J, Maximenko N, et al. Tracking the sources and sinks of local marine debris in Hawai’i. Mar Environ Res. 2013;84:76–83. pmid:23268778
- 55. Lechner A, Keckeis H, Lumesberger-Loisl F, Zens B, Krusch R, Tritthart M, et al. The Danube so colourful: a potpourri of plastic litter outnumbers fish larvae in Europe’s second largest river. Environ Pollut. 2014;188:177–81. pmid:24602762
- 56. García-Pérez J, Boldo E, Ramis R, Pollán M, Pérez-Gómez B, Aragonés N, et al. Description of industrial pollution in Spain. BMC Public Health. 2007;7(1):40.
- 57. Ordóñez A, Loredo J, De Miguel E, Charlesworth S. Distribution of heavy metals in the street dusts and soils of an industrial city in Northern Spain. Arch Environ Contam Toxicol. 2003;44(2):160–70. pmid:12520388
- 58. O’Riordan RM, Ramsay NF. Two new location records in the Algarve, Portugal for the non-indigenous barnacle Austrominius modestus. Mar Biodivers Rec. 2013;6:1–4.
- 59. Grade A, Chairi H, Lallias D, Power DM, Ruano F, Leit?o A, et al. New insights about the introduction of the Portuguese oyster, Crassostrea angulata, into the North East Atlantic from Asia based on a highly polymorphic mitochondrial region. Aquat Living Resour. 2016;29(4).
- 60. Cabezas MP, Navarro-Barranco C, Ros M, Guerra-Garcia JM. Long-distance dispersal, low connectivity and molecular evidence of a new cryptic species in the obligate rafter Caprella andreae Mayer, 1890 (Crustacea: Amphipoda: Caprellidae). Helgol Mar Res. 2013;67(3):483–97.
- 61. Bastida-Zavala JR, Mccann LD, Keppel E, Ruiz GM. The fouling serpulids (Polychaeta: Serpulidae) from United States coastal waters: an overview. Eur J Taxon. 2017;344:1–76.
- 62. Calder DR, Choong HHC, Carlton JT, Chapman JW, Miller JA, Geller J. Hydroids (Cnidaria: Hydrozoa) from Japanese tsunami marine debris washing ashore in the northwestern United States. Aquat Invasions. 2014;9(4):425–40.
- 63. WoRMS editorial board. World Register of Marine Species. http://www.marinespecies.org. 2017.
- 64. Browne MA, Chapman MG, Thompson RC, Amaral Zettler LA, Jambeck J, Mallos NJ, et al. Spatial and Temporal Patterns of Stranded Intertidal Marine Debris: Is There a Picture of Global Change? Environ Sci Technol. 2015;49(12):7082–94. pmid:25938368
- 65. Velander K, Mocogni M. Beach Litter Sampling Strategies: is there a ‘Best’ Method? Mar Pollut Bull. 1999;38(12):1134–40.
- 66. Hall TA. BioEdit: a user-friendly biological sequence alignment editor and analysis program for Windows 95/98/NT. Nucl Acids Symp Ser. 1999;41:95–8.
- 67. Altschul SF, Gish W, Miller W, Myers EW, Lipman DJ. Basic Local Alignment Search Tool. J Mol Biol. 1990;215:403–10. pmid:2231712
- 68. Kumar S, Stecher G, Tamura K. MEGA7: Molecular Evolutionary Genetics Analysis version 7.0 for bigger datasets. Mol Biol Evol. 2016;33(7):1870–4. pmid:27004904
- 69. Anderson M, Gorley R, Clarke K. PERMANOVA+ for PRIMER: guide to software and statistical methods. PRIMER-E Ltd.; 2008.
- 70. Clarke K, Gorley R. PRIMER v6: User Manual/Tutorial. PRIMER-E, Plymouth; 2006.
- 71. Carlton JT, Chapman JW, Geller JB, Miller JA, Carlton DA, McCuller MI, et al. Tsunami-driven rafting: Transoceanic species dispersal and implications for marine biogeography. Science (80-). 2017;357(6358):1402–6.
- 72. Rees EIS, Southward AJ. Plastic flotsam as an agent for dispersal of Perforatus perforatus (Cirripedia: Balanidae). Mar Biodivers Rec. 2009;2:1–3.
- 73. Vegter AC, Barletta M, Beck C, Borrero J, Burton H, Campbell ML, et al. Global research priorities to mitigate plastic pollution impacts on marine wildlife. Endanger Species Res. 2014;25(3):225–47.
- 74. Fazey FMC, Ryan PG. Debris size and buoyancy influence the dispersal distance of stranded litter. Mar Pollut Bull. 2016;110(1):371–7. pmid:27389460
- 75. Fazey FMC, Ryan PG. Biofouling on buoyant marine plastics: An experimental study into the effect of size on surface longevity. Environ Pollut. 2016;210:354–60. pmid:26803792
- 76. Kerckhof F, Cattrijsse A. Exotic Cirripedia (Balanomorpha) from Buoys off the Belgian Coast. Senckenbergiana maritima. 2001;31(2):245–54.
- 77. Ebbesmeyer CC, Ingraham WJ. Shoe spill in the North Pacific. Eos, Trans Am Geophys Union. 1992;73(34):361–5.
- 78. Thiel M, Gutow L. the Ecology of Rafting in the Marine Environment I. The Floating Substrata. Oceanogr Mar Biol Annu Rev. 2005;42:181–264.
- 79. Calder DR. Hydroid assemblages on holopelagic Sargassum from the Sargasso Sea at Bermuda. Bull Mar Sci. 1995;56(2):537–46.
- 80. Debrot AO, Tiel AB, Bradshaw JE. Beach debris in Curacao. Mar Pollut Bull. 1999;38(9):795–801.
- 81. Lavers JL, Oppel S, Bond AL. Factors influencing the detection of beach plastic debris. Mar Environ Res. 2016;119:245–51. pmid:27363010
- 82. Woodall LC, Robinson LF, Rogers AD, Narayanaswamy BE, Paterson GLJ. Deep-sea litter: a comparison of seamounts, banks and a ridge in the Atlantic and Indian Oceans reveals both environmental and anthropogenic factors impact accumulation and composition. Front Mar Sci. 2015;2:1–10.
- 83. Macfadyen G, Huntington T, Cappell R. Abandoned, lost or otherwise discarded fishing gear. Vol. 523, UNEP Regional seas reports and studies, 185: FAO Fisheries and Aquaculture Technical Paper, 523. Rome, UNEP/FAO. 2009.
- 84. Ebbesmeyer CC, Ingraham WJ, Jones JA, Donohue MJ. Marine debris from the oregon dungeness crab fishery recovered in the Northwestern Hawaiian Islands: Identification and oceanic drift paths. Mar Pollut Bull. 2012;65:69–75. pmid:22014917
- 85. Flor G. Relación entre la distribución de sedimentos y la circulación costera en la región del Cabo Penas. Vol. 10, Trabajos de Geología. Universidad de Oviedo; 1978. p. 183–94.