key: cord-1009961-1j1madof
authors: Lin, Chun-Ting; Chiu, Ming-Chih; Kuo, Mei-Hwa
title: A Mini-Review of Strategies for Quantifying Anthropogenic Activities in Microplastic Studies in Aquatic Environments
date: 2022-01-04
journal: Polymers (Basel)
DOI: 10.3390/polym14010198
sha: 930f7aa4334671059f923189c03e6dd6c28982f9
doc_id: 1009961
cord_uid: 1j1madof

Microplastic pollution is no longer neglected worldwide, as recent studies have unveiled its potential harm to ecosystems and, even worse, to human health. Numerous studies have documented the ubiquity of microplastics, reflecting the necessity of formulating corresponding policies to mitigate the accumulation of microplastics in natural environments. Although anthropogenic activities are generally acknowledged as the primary source of microplastics, a robust approach to identify sources of microplastics is needed to provide scientific suggestions for practical policymaking. This review elucidates recent microplastic studies on various approaches for quantifying or reflecting the degree to which anthropogenic activities contribute to microplastic pollution. Population density (i.e., often used to quantify anthropogenic activities) was not always significantly correlated with microplastic abundance. Furthermore, this review argues that considering potential sources near sample sites as characteristics that may serve to predict the spatial distribution of microplastics in aquatic environments is equivocal. In this vein, a watershed-scale measure that uses land-cover datasets to calculate different percentages of land use in the watershed margins delineated by using Geographic Information System (GIS) software is discussed and suggested. Progress in strategies for quantifying anthropogenic activities is important for guiding future microplastic research and developing effective management policies to prevent microplastic contamination in aquatic ecosystems.

The term "microplastic", which refers to tiny debris of plastics normally defined to be smaller than 5 mm [1] , was not widely used until 2004 [2] . Approximately 10% of municipal waste globally comprises plastics [3] . The vast use of plastic in human life has resulted in the ubiquity of microplastics in the environment, as they can be degraded into small, persistent, and therefore easy-to-transport plastic debris [4] . For example, microplastics have been detected in a variety of environments, such as beaches, bays, estuaries [5] , ocean surfaces [6] , deep-sea sediments [7] , rivers [8] , lakes [9] , raindrop [10] , the Alps and the Arctic [11] , and polar waters [12] . Microplastics have also been documented in biota, including riverine macroinvertebrates [13] , marine fish [14] , and birds [15] . The accumulation of microplastic pollution is considered an environmental hazard that has attracted global concern. Generally, microplastics originating from terrestrial environments are either retained in freshwater systems or eventually enter the ocean [16] . In this context, this review mainly focuses on aquatic environments.

Many studies have discussed the impact of microplastics on organisms [17] , and these impacts can be categorized into two types: physical and chemical [18] . Physical impacts can then be categorized as being either direct or indirect. The direct impacts of microplastics have been observed in numerous studies [17] , as ecotoxicological assessments of microplastic pollution are frequently conducted on different species in the laboratory. Generally, the detrimental consequence of microplastic ingestion results from the blockage of the digestive system, which reduces nutrition intake, inhibits food assimilation [19] , and causes inflammation [20] , resulting in the reduction of growth, reproduction, fitness, mortality, emergence delay, and immune-system weakening [18, 21] . Furthermore, indirect impacts of microplastic pollution on organisms also occur. These detrimental effects are not caused by the ingestion of microplastics per se but include the alteration of gut microbiota [22] , induction of microbiota dysbiosis [23] , ecosystem functioning change [24] , behavioral change [25] , and locomotion interruption [26] . Plastisphere, a term denoting the microbiome of microplastics, has raised global concern because its community structures are distinct from the natural environment. Vibrio, a genus of bacteria, is represented in the plastisphere of the North and Baltic Sea [27] , and can have harmful effects on the human body [28] .

Chemical impacts are caused by chemical additive consumptions, which are added to plastics during their production, and organic pollutants, which tend to attach to microplastics because of their large surface area to volume ratio [29] . These chemical substances can be easily exposed [30] , especially under ultraviolet radiation and extreme heat [31, 32] . For example, plasticizers added to plastic products for flexibility and malleability enhancement are not stable and can leach into the environment [33] . Additives such as bisphenol A (BPA), polybrominated diphenyl ethers (PBDEs), and phthalates are also known as endocrinedisrupting compounds (EDCs) and are harmful to the endocrine system [31] ; these directly (reception of plasticizers by hormone receptors on microbes [34] ), and indirectly (interruption of host hormone signaling) influence gut microbes, as gut microbes are mediated by hormones secreted by their hosts [29] .

In summary, microplastics or substances attached to them can induce immediate and chronic mechanical and chemical disruptions in organisms. Preventing microplastic pollution of natural habitats is necessary to overcome these problems. Therefore, identifying microplastic sources is imperative to mitigating this damage. However, most review articles mainly focus on the risks of microplastics to organisms; the methodological progress of microplastic extraction and identification; and the comparison of microplastic occurrence, size, shape, type, color, and abundance between publications [35] [36] [37] . Discussions on how these reports attributed microplastic pollution to various anthropogenic factors have been limited. This review aims to elucidate the current advancements in the strategies used to analyze the relationship between anthropogenic activities and microplastic pollution.

The major sources of microplastics are anthropogenic activities, such as human manufacturing and plastic-product usage. Humans are a major source of microplastics. The increasing world population size is a possible reason for the increasing plastic waste [2, 38, 39] , owing to the short lifetime that these plastics are actually in use [40] . In 2019, while the world population reached 7700 million [41] , the enormous demand for plastic drove the world plastic production up to 370 million metric tons a year [42] , which has attracted attention as the growing rate of plastic recycling is overtaken by the growing rate of plastic production. Although the recycling rate of plastic waste from 2006 to 2018 has doubled, 25% of plastic waste is still sent to landfills [42] . Furthermore, since the COVID-19 pandemic happened, the relationship between anthropogenic activities and microplastics has become clearer. The plastic demand decreased tremendously during the pandemic in Europe in 2020, due to the quarantine, indicating less human activity, and therefore less plastic production [42] . However, the subsequent lifting of the lockdown restriction implies a resumption of plastic demand, and thus the microplastic problem remains to be solved. In this section, we introduce global publications (n = 34) that have linked microplastic abundance to potential anthropogenic factors ( Figure 1 ), with Europe, India, and China being the top three most studied regions. Indeed, studies on the relationship between human activities and microplastic pollution in many densely populated areas are still in the developing stage, and providing in-depth focus on the link between these variables is necessary for studies that examine microplastic pollution as a function of spatial factors. Therefore, this review aims to not only amplify the importance of defining the relationships between variables, but also to explain why a better measure than population density for quantifying anthropogenic activities is needed and why statistical analysis is essential. Figure 1 . Distribution of the sampling sites of studies that linked microplastic pollution to anthropogenic activities. Densely populated area data were retrieved from Natural Earth (http: //www.naturalearthdata.com (accessed on 20 December 2021) [43] . The Antarctica region was excluded as it is an area with limited human activities. Coordinate reference system: WGS 84, EPSG: 4326.

Numerous studies have shown that areas with intensive anthropogenic activities tend to have higher microplastic pollution levels [17, [44] [45] [46] [47] [48] [49] [50] . Previous reports related to aquatic environments (n = 34) are listed in Table 1 , showing that 64.7% of studies sampled microplastics from water surface/column, 61.8% sampled microplastics from sediments, and only 29.4% sampled microplastics from organisms. Above all, only 50% of studies have conducted statistical analyses to investigate the relationship between anthropogenic factors and microplastic abundance, while 45, 50 and 50% of studies made statistical conclusions regarding the relationship between the two in water surfaces/columns, sediments, and organisms, respectively. Such paucity underlines the pressing need to conduct more statistics-based research in this field, and only half of the studies addressing the relationship between microplastic and anthropogenic activities is insufficient to formulate reliable microplastic control policies. Indeed, because of the heterogeneity of anthropogenic activities, previous studies have usually treated anthropogenic activities as a point source of microplastics. Those studies reflected the degree to which anthropogenic activities were responsible, mainly with regards to population density and proximity to city centers, wastewater treatment plants (WWTPs), harbors, and highly urbanized areas [5, 9, 44, 45, 51] .

Browne et al. [45] , for example, investigated microplastic pollution in sediments sampled from 18 sandy beaches worldwide, with microplastic abundance ranging from 2 to 31 particles in 250 mL sediment, suggesting that population density is significantly positively correlated with level of microplastic pollution (p < 0.05, r 2 = 0.34). However, it was difficult to compare this study with other sediment-focused microplastic studies on the coastline, as most relevant studies used weight/area rather than volume as the sampling unit. Yonkos et al. [52] supported this conclusion, demonstrating that variation in microplastic abundance on sampling dates (5534 to 297,927 particles km −2 ) at the water surface of a bay was significantly correlated with population density (p < 0.05, r 2 = 0.33). In addition, Tang et al. [53] also suggested that, when their observations (514 particles m −3 on average) were integrated with other studies that took place in coastal areas of China, microplastic abundance at the water surface was significantly correlated with population size (p < 0.05, r 2 = 0.99) and urbanization rate (p < 0.05, r 2 = 0.98). Compared with not only a bay in South Korea, where the abundance at the water surface was 770 particles m −3 on average [47] , but also other reports in China (see Reference [53] ), the abundance observed by Tang et al. [53] was lower. This was possibly due to (1) different sampling methodologies, (2) different degrees of population density in sampling sites, and (3) samples being collected during the rainy season. More importantly, microplastic abundance in urban areas was not significantly different from that in rural areas with low population density (ANOVA, p > 0.05) in a bay in South Korea [47] . Furthermore, Wang et al. [51] found that, in China, distance from Wuhan City Center was significantly negatively correlated with microplastic abundance (p < 0.05, r 2 = 0.90), indicating a close relationship between human activities and microplastic pollution. Similarly, microplastic abundance in sediment (11 to 234.6 particles kg −1 ) in heavily polluted areas in Taihu Lake, based on the index of eutrophication that generally reflects the degree of anthropogenic activities, was significantly higher than it was in clean areas (ANOVA, p < 0.05) [9] .

In contrast, many studies provided no evidence of a relationship between population density and microplastics, as population density was not significantly associated with microplastic concentration [38, 50, 54] . For example, no significant relationship was found between the local municipal population and the level of microplastic abundance in water (p > 0.05) and sediment (p > 0.05) in the South African coastline, although some harbors had significantly higher microplastic loads (up to 1200 particles m −3 ) in the water column (ANOVA, p < 0.05) [38] . Furthermore, Townsend et al. [50] investigated microplastic abundance in the wetlands in Australia (2 to 147 particles kg −1 ), suggesting that neither population size (p > 0.05) nor population density (p > 0.05) was significantly correlated with microplastic abundance. Klein et al. [55] analyzed microplastics in river-shore sediments in Germany (228 to 3763 particles kg −1 ), suggesting that population density was not significantly correlated with microplastic abundance (p > 0.05), and similarly microplastic abundance did not vary as a function of proximity to industrial areas or wastewater treatment plants. This disparity indicates that neither population density, a measure to quantify anthropogenic activities as a point source of microplastics, nor the characteristics of sample sites and their surroundings can fully explain the spatial variability of microplastics, with the latter measure being common in previous reports (see next section). 

It is very common to relate the effects of human activities to microplastic abundance without clear statistical analyses [5, 55, 56] . Previous studies tended to attribute the elevated microplastic abundance to the surrounding possible point source of microplastics, probably because it is straightforward and intuitive to infer the relationship between anthropogenic factors and microplastic abundance by associating the spatial distribution of microplastic abundance with general characterization around sample locations.

For example, although Klein et al. [55] suggested that, as mentioned above, it was difficult to visualize the relationship between microplastic abundance and proximity to industrial areas or wastewater treatment plants on a map; sample sites that were close to nature reserves had low microplastic abundance, which probably could be explained by the fewer human activities in nature reserves. In contrast, areas exhibiting high microplastic abundance on the water surface probably resulted from the proximity to marinas, military, and commercial harbors, as well as effluent from wastewater treatment plants that process sewage from more than 134,377 people [5] . In addition, we must acknowledge that those areas are located in the most densely urbanized area in the monitored region (Bay of Brest, France) [5] .

Furthermore, sample sites located on the cruise route had higher microplastic abundance, supporting the inference that vessel activities produce microplastic pollution [56, 76] . In addition, since certain sample sites located downstream of wastewater treatment plants showed high microplastic abundance, especially at the right river bank, and that the outlets of wastewater treatment plants entered the Rhine River from the right river bank, it can be inferred that the elevated microplastic concentration on the river surface probably resulted from the outlets of the wastewater treatment plant [60] . Additionally, consistently high microplastic abundance on the surface of Lake Erie of the Laurentian Great Lakes might be due to anthropogenic activities, as Lake Erie was the most populated lake in the monitored region [64] .

In summary, reports regarding anthropogenic activities and microplastics in the field can generally be presented in two ways, depending on whether the discussion is based on statistical analyses. If yes, there were usually two kinds of mathematical results: microplastic abundance in densely urbanized areas was significantly different from that in less developed areas (reference area) [9, 46, 47] , and there was a correlation between population density and microplastic abundance in sample sites [52, 53, 55] . If not, the discussion was usually made by visual inspection of anthropogenic factors surrounding the sample sites, and this can be problematic.

Microplastic distribution and abundance in monitored regions do not always depend on surrounding anthropogenic activities (e.g., location of WWTPs and harbors). According to Klein et al. [55] , the four sample sites with the highest microplastic abundance, regardless of count (particles kg −1 ) or mass (mg kg −1 ), were also categorized as the four most populated sites in the research area; therefore, there is a trend indicating that population density can explain the high level of microplastic pollution at these sites. However, statistical analysis revealed no significant correlation between microplastic abundance and population density when all sample sites were considered. This highlights the potential scale-dependent effect on the results and the necessity of conducting appropriate statistical analyses to account for this. Linking these variables based on visual inspection of spatial distribution may lead to problematic conclusions. Therefore, in order to apply statistical analysis and produce practical results, two questions remain to be answered: (1) How can anthropogenic factors be quantified? (2) Are there other quantification strategies more appropriate than population density?

Quantifying the level of human activity by population density is simple. As mentioned above, previous studies revealed that the correlation between human activities and the level of microplastic pollution is mostly significant; on the other hand, remote and/or less developed areas showed significantly lower microplastic abundance than urbanized areas. These results, however, oversimplified anthropogenic activities and thus cannot help governments construct effective policies for controlling microplastic pollution. In other words, the anthropogenic activities that contribute microplastics to the environment predominantly remain unknown, leading to a difficult situation in which controlling microplastics from the source is the most effective way to reduce microplastics [77] . While it is no secret that human activities are the biggest source of microplastics, we still have no clue what the exact source is. There is an urgent need for detailed information on human activities.

Therefore, in addition to population density, recent studies have used other urban attributes to quantify different human activities, i.e., different land uses within the catchment of the sample location ( Figure 2 ). Figure 2 visualizes the quantification strategy of different anthropogenic factors: delineation of the catchment margins of sample sites and calculation of the percentages of different upstream land covers (e.g., industrial area, residential area, and agricultural area) in the watershed. These percentages of land cover were used to reflect the magnitude of different anthropogenic activities. For example, Yonkos et al. [52] extrapolated not only the population density in catchments of sample locations from the 2010 US census data, but also the percentages of urban (industrial), suburban (residential), agricultural, and forested areas in catchments of sample sites from the 2006 National Land Cover Database. The study estimated the correlation between different land covers and microplastic abundance and concluded that the microplastic abundance on the water surface was significantly associated with population density, percentage of urban (industrial) area, and percentage of total developed (industrial and residential) areas. Correspondingly, Baldwin et al. [66] analyzed the correlation between the microplastic abundance on the lake surface and different watershed characteristics, including percentages of impervious areas (e.g., roads, parking lots, and buildings), urban area, agricultural areas (total, crops, pasture, and hay), and forested area in catchments of sample sites. Land-cover datasets were retrieved from the National Land Cover Database (NLCD) Land Cover and Percent Developed Imperviousness datasets, and watershed margins were derived from the US Geological Survey Watershed Boundary Dataset (USGC-WBD). The results suggested that microplastic abundance was positively correlated with the percentage of urban area and percentage of impervious areas, and negatively correlated with the percentage of agricultural area (total and crops) [66] , in line with the results of Yonkos et al. [52] . Although agricultural activities were not addressed too much in the study by Baldwin et al. [66] , Yonkos et al. [52] found a similar but insignificant trend in the percentage of agricultural area, which was also dominated by crop agriculture; it was negatively associated with microplastic abundance. This can probably be explained by the lower development and lesser amount of human activities in areas with high agricultural activity.

A similar approach for the quantification of human activities was conducted in the urban wetlands of Melbourne, Australia. Briefly, the study calculated the catchment margins of sample sites with certain digital elevation models, using ArcGIS 10.3 [50] . Detailed land-use data were retrieved from the 2011 Australian Population Census, including the percentages of the following: commercial area, industrial area, undeveloped area, road/rail, residential area, percentage of rural area, and semi-rural area. Additionally, urban growth and dwelling density were also included in the analyses to reflect the different magnitudes of anthropogenic activities.

However, in contrast with the study by Yonkos et al. [52] , Townsend et al. [50] indicated that only the percentage of undeveloped areas within the catchment was significantly negatively correlated with microplastic abundance in sediment. No significant correlation between the percentage of industrial area and microplastic abundance in the catchment was observed. More interestingly, if not using the percentage of land use, no significant correlation was found between microplastic abundance and the absolute area of different land use, presumably resulting from the effect of catchment size. Lin et al. [49] supported this result, as the percentage of the industrial area model was better than its logarithmic model. To elaborate further, Lin et al. [49] constructed several general linear mixed-effect models and conducted model selection to investigate the effects of different land uses (industrial and residential) on microplastic concentration found in chironomid larvae. The results showed that the percentage of industrial area in catchments contributes more to microplastic concentration, a finding that is in line with previous studies that showed that the percentage of industrial (urban) areas in catchments was a potential predictor of microplastic pollution [52, 66] .

To make progress in mitigating environmental microplastics, the source of microplastics needs to be identified. While anthropogenic activities are the most well-known source of microplastics, one should keep in mind that quantifying parameters, such as population density, might not be detailed enough to offer practical suggestions on formulating policies for microplastic pollution management. In fact, due to the environmental risks of microplastics, government agencies and environmental protection organizations have actively advocated policies and regulations to protect aquatic organisms from the detrimental effects of microplastics [78, 79] . Regulation that bans plastic/microplastic production and consumption has been articulated globally in the past few years [80] . For instance, since 2003, the government of South Africa has charged for the use of thick plastic bags, and plastic-bag use has been decreased by 90%. Since 2007, Kenya has banned the manufacture and import of thin plastic bags; however, the ban was not enforced. Since 2008, Rwanda has become the first plastic-free country by banning non-biodegradable plastics. In the same year in China, while the Beijing Olympics were in full swing, plastic bags under a certain thickness were banned, and citizens were charged for the use of others, leading to effective results in mitigating damage caused by plastic bags. In 2013, Pucón was the first city in Chili to ban plastic bags. In 2014, California, USA, banned plastic shopping bags and plastic bottles, and France implemented a tax on non-biodegradable plastic bags. In 2015, an amendment bill in the United States against personal-care products containing microbeads was passed. Similar acts have been adopted in Canada [81] and Taiwan [49] . In addition, plastic regulation in India, the most populated country and the largest plastic consumers in the world, was not successful, due to poor enforcement and pressure from the rapidly growing plastic industry until 2016, when plastic bags with the thickness below 50 µm were banned [82] .

It is recommended that policies focus on secondary microplastics, such as microfibers, because the major source of microfibers is the washing of clothes [45] . Policies should be developed to improve domestic wastewater treatment processes to filter out microfibers, as waste management policies directly influence microplastic abundance in the environment [83] . Furthermore, policies for regular monitoring of microplastic abundance in various ecosystems have been suggested [82] . In addition to reducing plastics from consumption or import, and capturing microplastics before they contaminate the natural environment, more studies are required to further discuss the heterogeneity of human activities and how to effectively control microplastic pollution. Recently, a few studies have attempted to further discuss different kinds of human activities based on land-use-survey data. They have delineated watershed margins, presuming that microplastics released from sources are mainly transported by rain runoff to rivers or lakes (freshwater systems), and incorporated a land-cover dataset to represent distinctive human activities. These studies have shown that industrial/urban areas within catchments are potential sources of microplastics. However, future challenges in this context will be to answer the following questions: (1) Can the resolution of land-cover data increase so that we can identify the exact industry producing the largest amount of microplastics in industrial areas, and can the resolution of microplastic properties increase (with better microplastic identification efficiency) so that we can identify a specific "marker" substance of microplastics that may be representative of a certain type of industry? (2) Because watershed margin delineation has a huge influence on the results, is the watershed margin reliable if river channels are artificially manipulated in urban river systems, and should the sewer system be considered? (3) Are there better approaches to quantifying anthropogenic activities that can help the government build related policies?

In conclusion, these challenges can be tackled by the construction of accessible and reliable land-cover surveillance data from government agencies, the development of better microplastic-substance-identification techniques and protocols, and the available data on artificial river channels and sewer systems in urban areas. Although the relationship between anthropogenic activities and microplastics is yet to be comprehensively studied, this review has observed positive and consistent progress on this issue, showing that these problems are expected to be addressed in the near future. This review integrates the global literature on environmental microplastics and anthropogenic activities, highlighting the necessity of summarizing results with statistical analyses. It is imperative to quantify anthropogenic factors by using indices other than population density, which creates equivocal results whose use by policymakers is difficult. At present, this review suggests that using watershed-scale attributes derived from land-use datasets might produce a more in-depth scientific basis for government authorities and environmental protection organizations and institutions to articulate efficient policies to reduce microplastic pollution. 

The authors declare no conflict of interest.

Proceedings of the International Research Workshop on the Occurrence, Effects, and Fate of Microplastic Marine Debris

Lost at Sea: Where Is All the Plastic? Science

Accumulation and fragmentation of plastic debris in global environments

Mechanistic implications of plastic degradation

Influence of environmental and anthropogenic factors on the composition, concentration and spatial distribution of microplastics: A case study of the Bay of Brest

Plastic Pollution in the World's Oceans: More than 5 Trillion Plastic Pieces Weighing over 250,000 Tons Afloat at Sea

Microplastic pollution in deep-sea sediments

Microplastics in freshwater systems: A review on occurrence, environmental effects, and methods for microplastics detection

It Is Raining Plastic

White and wonderful? Microplastics prevail in snow from the Alps to the

Observations of floating anthropogenic litter in the Barents Sea and Fram Strait

Microplastic ingestion by riverine macroinvertebrates

Microplastic and mesoplastic contamination in canned sardines and sprats

Microplastic accumulation in the gastrointestinal tracts in birds of prey in central Florida

High-levels of microplastic pollution in a large, remote, mountain lake

Microplastics in the freshwater and terrestrial environments: Prevalence, fates, impacts and sustainable solutions

The physical impacts of microplastics on marine organisms: A review

Biodegradable and Petroleum-Based Microplastics Do Not Differ in Their Ingestion and Excretion but in Their Biological Effects in a Freshwater Invertebrate Gammarus fossarum

Uptake and Accumulation of Polystyrene Microplastics in Zebrafish (Danio rerio) and Toxic Effects in Liver

Immune response triggered by the ingestion of polyethylene microplastics in the dipteran larvae Chironomus riparius

Gut microbiota protects honey bees (Apis mellifera L.) against polystyrene microplastics exposure risks

Polystyrene microplastics induce microbiota dysbiosis and inflammation in the gut of adult zebrafish

Effect of microplastics on ecosystem functioning: Microbial nitrogen removal mediated by benthic invertebrates

Effects of large nongrazable particles on clearance and swimming behaviour of zooplankton

Microplastic Ingestion by Zooplankton

Dangerous hitchhikers? Evidence for potentially pathogenic Vibrio spp. on microplastic particles

Wound infections caused by Vibrio vulnificus and other marine bacteria

Microplastics and the gut microbiome: How chronically exposed species may suffer from gut dysbiosis

Transport and release of chemicals from plastics to the environment and to wildlife

Components of plastic: Experimental studies in animals and relevance for human health

Microplastics in the marine environment

A critical analysis of the biological impacts of plasticizers on wildlife

Microbial endocrinology: The interplay between the microbiota and the endocrine system

Microplastics in freshwater systems: A review of the emerging threats, identification of knowledge gaps and prioritisation of research needs

Microplastics in the Marine Environment: A Review of the Methods Used for Identification and Quantification

Microplastics in freshwater sediment: A review on methods, occurrence, and sources

Do microplastic loads reflect the population demographics along the southern African coastline?

Plastic waste inputs from land into the ocean

Production, use, and fate of all plastics ever made

A/423

Plastics-The Facts. An Analysis of European Plastics Production, Demand and Waste Data

World Urban Areas, LandScan, 1:10 Million

Plastic debris and microplastics along the beaches of the Strait of Hormuz, Persian Gulf

Accumulation of Microplastic on Shorelines Woldwide: Sources and Sinks

Microplastic pollution in water and sediment in a textile industrial area

A close relationship between microplastic contamination and coastal area use pattern

Insights into the horizontal and vertical profiles of microplastics in a river emptying into the sea affected by intensive anthropogenic activities in Northern China

Effects of anthropogenic activities on microplastics in deposit-feeders (Diptera: Chironomidae) in an urban river of Taiwan

Associations between microplastic pollution and land use in urban wetland sediments

Microplastics pollution in inland freshwaters of China: A case study in urban surface waters of Wuhan

Microplastics in Four Estuarine Rivers in the Chesapeake Bay

Microplastics and polycyclic aromatic hydrocarbons (PAHs) in Xiamen coastal areas: Implications for anthropogenic impacts

The occurrence of microplastics in farmland and grassland soils in the Qinghai-Tibet plateau: Different land use and mulching time in facility agriculture

Occurrence and Spatial Distribution of Microplastics in River Shore Sediments of the Rhine-Main Area in Germany

Occurrence of microplastics in the water column and sediment in an inland sea affected by intensive anthropogenic activities

Spatio-temporal evaluation of macro, meso and microplastics in surface waters, bottom and beach sediments of two embayments in Niterói, RJ, Brazil

Microplastic ingestion by the sandfish Holothuria scabra in Lampung and Sumbawa, Indonesia

Sinks and sources: Assessing microplastic abundance in river sediment and deposit feeders in an Austral temperate urban river system

Microplastics profile along the Rhine River

Microplastics in sediments from Amazon rivers

Microplastic distribution in surface water and sediment river around slum and industrial area (case study: Ciwalengke River, Majalaya district, Indonesia)

Microplastics ingestion by blue panchax fish (Aplocheilus sp.) from Ciliwung Estuary

Microplastic pollution in the surface waters of the Laurentian Great Lakes

First evidence of microplastic contamination in the freshwater of Lake Guaíba

Plastic Debris in 29 Great Lakes Tributaries: Relations to Watershed Attributes and Hydrology

Abundance, characteristics and surface degradation features of microplastics in beach sediments of five coastal areas in Tamil Nadu

Occurrence and characteristics of microplastics in the coral reef, sea grass and near shore habitats of Rameswaram Island

Occurrence of microplastics in epipelagic and mesopelagic fishes from Tuticorin, Southeast coast of India

Holistic assessment of microplastics in various coastal environmental matrices, southwest coast of India

Evidence of microplastics in samples of zooplankton from Portuguese coastal waters

Estimation of microplastics in sediments at the southernmost coast of India (Kanyakumari)

Microplastics along the beaches of southeast coast of India

Analysis of small microplastics in coastal surface water samples of the subtropical island of Okinawa

Microplastic pollution in freshwater ecosystems: A case study from Turkey

Microplastics in Arctic polar waters: The first reported values of particles in surface and sub-surface samples

On the quantity and composition of floating plastic debris entering and leaving the Tamar Estuary, Southwest England

Microplastics in cosmetics: Environmental issues and needs for global bans

Abundance, interaction, ingestion, ecological concerns, and mitigation policies of microplastic pollution in riverine ecosystem: A review

The Downfall of the Plastic Bag: A Global Picture

Occurrence of microplastics and its pollution in the environment: A review

Plastics and microplastics: A threat to environment

Microplastics contamination in different trophic state lakes along the middle and lower reaches of Yangtze River Basin