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Review

Global Mangrove Deforestation and Its Interacting Social-Ecological Drivers: A Systematic Review and Synthesis

by
Avit K. Bhowmik
1,2,*,†,
Rajchandar Padmanaban
3,4,†,
Pedro Cabral
3 and
Maria M. Romeiras
5
1
Risk and Environmental Studies, Karlstad University, Universitetsgatan 2, 651 88 Karlstad, Sweden
2
Centre for Research on Sustainable Societal Transformation (CRS), Karlstad University, Universitetsgatan 2, 651 88 Karlstad, Sweden
3
Nova Information Management School, Universidade Nova de Lisboa, 1070-312 Lisbon, Portugal
4
Centro de Estudos Geográficos, Instituto de Geografia e Ordenamento do Território, Edificio I, Universidade de Lisboa, R. Branca Edmée Marques, 1600-276 Lisboa, Portugal
5
LEAF, Linking Landscape, Environment, Agriculture and Food, Instituto Superior de Agronomia (ISA), Universidade de Lisboa, Tapada da Ajuda, 1349-017 Lisbon, Portugal
*
Author to whom correspondence should be addressed.
†
These authors have contributed equally.
Sustainability 2022, 14(8), 4433; https://doi.org/10.3390/su14084433
Submission received: 2 March 2022 / Revised: 4 April 2022 / Accepted: 5 April 2022 / Published: 8 April 2022
(This article belongs to the Special Issue Mangrove Ecosystem Ecology, Conservation and Sustainability)
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Abstract

:
Globally, mangrove forests are substantially declining, and a globally synthesized database containing the drivers of deforestation and drivers’ interactions is scarce. Here, we synthesized the key social-ecological drivers of global mangrove deforestation by reviewing about two hundred published scientific studies over the last four decades (from 1980 to 2021). Our focus was on both natural and anthropogenic drivers with their gradual and abrupt impacts and on their geographic coverage of effects, and how these drivers interact. We also summarized the patterns of global mangrove coverage decline between 1990 and 2020 and identified the threatened mangrove species. Our consolidated studies reported an 8600 km2 decline in the global mangrove coverage between 1990 and 2020, with the highest decline occurring in South and Southeast Asia (3870 km2). We could identify 11 threatened mangrove species, two of which are critically endangered (Sonneratia griffithii and Bruguiera hainseii). Our reviewed studies pointed to aquaculture and agriculture as the predominant driver of global mangrove deforestation though their impacts varied across global regions. Gradual climate variations, i.e., sea-level rise, long-term precipitation, and temperature changes and driven coastline erosion, salinity intrusion and acidity at coasts, constitute the second major group of drivers. Our findings underline a strong interaction across natural and anthropogenic drivers, with the strongest interaction between the driver groups aquaculture and agriculture and industrialization and pollution. Our results suggest prioritizing globally coordinated empirical studies linking drivers and mangrove deforestation and global development of policies for mangrove conservation.

1. Introduction

The tropical, subtropical, and warm temperate climate regions of the world contain intertidal mangrove forests forming a unique interface between terrestrial and marine ecosystems with enriched biodiversity composed of different species of flora and fauna, upon which millions of people depend on [1,2,3]. Mangroves provide unique and valuable ecosystem services, i.e., provisioning (e.g., aquaculture, fisheries, fuel, medicine, textiles), regulating (e.g., shoreline protection, erosion control, climate regulation), intermediate (nutrient cycling, nursery habitat), and cultural (recreation and tourism) [4,5,6,7]. Moreover, about 10–15% of the global coastal sediment retention and carbon storage are managed by mangrove forests [8]. These values are five times greater per hectare (0.01 km2) than those driven by tropical forests and other coastal wetlands together [9]. Mangrove forests also act as an important environmental barrier between shores and lands, protecting the inhabiting ecological and social communities from the adverse impacts of extreme events, such as hurricanes and storms worldwide [5,10].
In spite of their critical contribution to human and ecosystem welfare, mangrove forests have been declining globally at an alarming rate during the past 40 years [11,12,13]. The severity of the mangrove deforestation has also been manifested in the substantial loss of mangrove habitats, species, and ecosystem services [14]. For example, during the last 75 years, the Philippines lost more than 75% of its mangrove forests, with more than 66% lost only since 1990 [15]. In Africa, which accounts for about 20% of the global mangrove forests, 63 km2 were lost during 2005, dominantly in West Africa, e.g., in Gabon, Sierra Leone, Guinea-Bissau, and Senegal [16]. Approximately 70 plant species that comprise global mangrove forests and are frequently used as indicators for coastal changes due to their specialized adaptation and minor variation across hydrological and tidal regimes, are on a noticeable decay [17]. Several mangrove species in Southeast Asia, e.g., Aegiceras floridum (with a native range from Malesia to New Guinea) [18], Camptostemon philippinensis (native range in Philippines) [19], Heritiera globose (native to Borneo) [20], and Kandelia candel (native to Asia-Tropical) [21] are now threatened with extinction.
Mangrove deforestation is subject to a multitude of social-ecological drivers, ranging from climate change and natural perturbations to pollution and anthropogenic exploitation of mangrove resources [22,23,24]. Two main groups of drivers emerged in recent studies:
  • Environmental drivers, such as climatic and associated geological changes [10], e.g., increased salinity driven by increasing temperatures [25], and natural disasters, e.g., tropical cyclones [26] and tsunamis [27], and
  • Anthropogenic activities, e.g., aquaculture and agriculture, in situ encroachment [28], exploitation of forest resources [29], water withdrawal [30], urbanization [31], and upstream pollution [32].
Among these, tropical cyclones entail disruptive temporary damages from which mangrove forests may or may not recover, whereas climatic changes and anthropogenic activities cause gradual and largely irreversible loss of mangrove forests [33]. Climate and related changes, e.g., changes in thermal regimes and sea-level rise, emerged as a dominant environmental driver of mangrove deforestation [34]. Sea level has been indicated as the most important factor influencing the future distribution of mangroves, while the mangrove ranges may shift further Northward and Southward as an effect of global warming and shift in the thermal regimes [34]. As the frequency of the occurrences of tropical cyclones increased with global warming and resulting climate change, mangrove responses to tropical cyclones and their regeneration patterns also altered [35,36,37]. The availability of sediments was identified as a crucial supporting factor for the regeneration of minerogenic mangroves from the cyclone aftermaths [6]. Among the anthropogenic drivers, land changes and encroachments were augmented in Southeast Asia as a result of aquaculture and agriculture expansions, e.g., shrimp aquaculture and palm plantation [38,39]. Coastal development and urbanizations also drove a major decline in mangrove coverage, particularly in the Asian, Caribbean, and Sub-Saharan regions [39,40,41].
The environmental and anthropogenic drivers may interact in a complex web and may exacerbate the rate of mangrove deforestation [42,43]. For example, salinity intrusion, which has been identified as an environmental driver of mangrove deforestation in several regions, may be mediated and amplified by the complex interaction among geographical location, flow modifications in upstream, coastal embankments, sea-level rise, cyclone and storm surge, brackish water effect, precipitation and shrimp aquaculture [17,44,45,46,47]. Global conservation and management efforts like “Global Mangrove Alliance” [11] require a global level synthesis and consolidation of these drivers of mangrove deforestation as well as an in-depth understanding of their complex interactions.
Recently published articles studying global mangrove deforestation and drivers either focused on a subset of global mangrove areas [48] or a subset of drivers [1,31] and did not study the interaction among drivers [13,49]. In this review, we draw on scientific literature and synthesize the social-ecological drivers of mangrove deforestation at a global level. Mangrove deforestation covers both total and permanent deforestation, such as loss in the mangrove coverage, as well as partial and temporary deforestation, such as defoliation and damages caused by cyclones. We start by analyzing the changes in the global coverage of mangrove forests and subsequently assess the current status of the mangrove species. The drivers of mangrove deforestation are then identified along with their geographic coverage of effects. Our review ends with an analysis of the interaction among the drivers and a discussion on the challenges involved in mangrove forest conservation.

2. Methods

We conducted a systematic literature review following the Preferred Reporting Items for Systematic Reviews and Meta-analyses (PRISMA) framework [50] (see Figure A1 in Appendix A for details). Two electronic scientific literature sources, i.e., Web of Science (webofknowledge.com) and Scopus (www.scopus.com), were accessed between 2 September 2017 and 31 December 2021 to search for original articles, commentaries, books, letters, and reports related to mangrove deforestation. We searched across all studies that were published between 1 January 1980 and 28 February 2021 using the initial keywords: “mangrove distribution”, “mangrove biomass”, “mangrove species”, and “mangrove ecosystems” to identify the literature that studied mangrove forests in general (Table 1). We then excluded the literature that either did not study changes and deforestation of mangroves or did not address the drivers of changes. A total of 250 scientific literature sources were found, which were further filtered using three sets of keywords based on a priori knowledge of the drivers of global mangrove deforestation (Table 1). The first keyword set “Climate” included drivers related to the long-term gradual changes in temperature, precipitation, and sea-level rise. The keyword set “Extreme events” involved extreme events like cyclones and tsunamis. “Land changes” indicated a set of anthropogenic drivers and included search terms related to agriculture and aquaculture expansion and urbanization, while pollution aspects, such as heavy metal contamination, were included in the “Pollution” set. Finally, the “Flow modification” set included drivers related to the diversion of surface water flow and their impacts on the mangrove forests. The returned search records included at least one entry from each of the four keyword sets. We obtained further inputs from subject experts to revise the search strategy and also to locate additional literature. Thus, we arrived at a final set of 201 scientific studies for the analyses and synthesis of this review.
To assess the change in mangrove forest coverage and the current status of the mangrove species, we linked the consolidated literature with four online databases on mangrove forests distribution and species: (a) Global Mangrove Watch (GMW: https://www.globalmangrovewatch.org/), (b) the mangrove species occurrence dataset of Global Biodiversity Information Facility (GBIF: https://www.gbif.org), (c) the native distribution dataset of Plants of the World Online (POWO: www.plantsoftheworldonline.org), and (d) International Union for Conservation of Nature (IUCN) Red List of Threatened Species (www.iucnredlist.org) (all accessed between 2 September 2017 and 31 December 2021).
We first examined the changes in the global mangrove forests coverage during the period represented by the consolidated literature. We found 36 studies that consistently reported mangrove forest coverage across five global mangrove regions and three decades between 1990 and 2020 (see Table 2 for details). The reported area coverage values for mangrove forests were checked against the GMW datasets and compared to calculate the changes in the coverage of global mangrove forests. Note that these studies and databases reported both gains and losses of mangrove forests, from which we calculated the net change. Subsequently, we identified the vulnerable and endangered mangrove species from the IUCN database and their occurrence and native distribution from the GBIF and POWO databases. This information was again cross-checked using the consolidated literature. We mapped the status of the mangrove species across the United Nations Food and Agriculture Organization (FAO) delineated marine fishing areas [51] using QGIS v.3.4.4 (see Figure 1), as these provide the most detailed account of the coastal wetlands and mangrove species. In the third step, we identified and grouped the drivers of mangrove deforestation and identified their impacts on mangrove habitats, species, ecosystems, and societies in general, and also examined their geographic coverage of effects (Figure 2, Table 3). The number of studies reporting each identified driver and driver group for 32 countries across five global mangrove regions were documented (Table 3), and their driven mangrove coverage losses were identified at the country, region, and global levels. For each driver and driver group, interacting drivers and driver groups were also identified when reported by the consolidated literature. Finally, the interactions among the drivers were mapped at a global level using a Chord-Dependency Diagram (Figure 3).

3. Decline in the Mangrove Forests Coverage

Our consolidated literature (total 36) that reported changes in the mangrove forests coverage covered three decades, i.e., between 1990 and 2020 and about all of the global mangrove forests [49,52] (see Table 2 for details). The mangrove belts are largely found in the equatorial coastal regions with the tropical, sub-tropical, and warm temperate climates between 30° N and 30° S [11,53]. Mangroves typically grow in harsh environments with moderate to high temperatures, tidal fluctuations, and high salinity in groundwater [54,55]. These conditions nourish canopies of mangrove growth up to 30–40 m in height [56]. The majority of mangrove forests (about 40%) covers only four countries, i.e., Indonesia, Australia, Brazil, and Mexico with the Asian region holding the largest (around 42%) and most diverse mangrove areas [12,39]. About 15% of the mangrove forests are situated in Africa, while Oceania and South America cover 12% and 11% of the global mangrove forests, respectively [57,58]. Ramsar wetlands (the Sundarbans in Bangladesh and India, Garig Gunak Barlu in Australia, Cayapas-Mataje in Ecuador, Everglades in the United States, and Douala Edea in Cameroon) had a mangrove coverage of about 378,960 km2 in 2020 [11,13,59].
The studied mangrove forests by our consolidated literature exhibited an overall decline (net loss) of more than 5% in global coverage between 1990 and 2020 [11,39,49,60] (Table 2). Globally, the mangrove cover declined by 8600 km2 between 1990 and 2020 (Table 2) at a rate of 287 km2 per year [61,62]. Sixty percent of the literature that reported changes in the mangrove forests distribution studied countries in the South and Southeast Asian region, which experienced the highest mangrove loss (3870 km2 and more than 6% decline in the global coverage) between 1990 and 2020 [11,62,63,64]. The mangrove habitat loss in South and Southeast Asia was recorded at an average rate of 0.34% and 0.33% per year between 2000 and 2010 and between 2010 and 2020, respectively, which is also the highest among the mangrove regions globally [12,31,38]. The mangrove habitat loss in South America followed a similar average rate of 0.30% and 0.31% per year between 2000 and 2010 and between 2010 and 2020, respectively [11,12,65]. The total areal loss of mangrove forests in South America is 1360 km2 between 1990 and 2020 (Table 2). Among the Asian countries, Indonesia encountered the highest areal loss (more than 700 km2) [38], while Malaysia experienced the highest loss in percentage (more than 3%) [66] between 2000 and 2010. Mangrove forests in Ramsar sites also encountered a substantial loss (5% of the global coverage) between 2000 and 2010 [59].

4. Status of the Mangrove Species

Our consolidated literature reported the status of 69 mangrove plant species [67,68], 35 of which have their native coverage in the Philippines [69,70]. Among the reported mangrove plant species, 11 are listed as threatened (two as Critically Endangered “CR”, three as Endangered “EN” and six as Vulnerable “VU”) (Figure 1). The geographic coverage of the five CR and EN mangrove species are dominantly Southeast Asia (Figure 1). Among the CR species, Sonneratia griffithii (Lythraceae) has a restricted distribution in South Asia, and is considered very rare or locally extinct in many parts of its range [71]. Bruguiera hainesii (Rhizophoraceae), the other CR species, is very rare and has a limited and patchy distribution in Singapore, Malaysia, and Papua New Guinea [71]. The three EN species (i.e., Camptostemon philippinense, Heritiera fomes, and Heritiera globose, all from Malvaceae family) are very rare, showing a patchy distribution in South Asia, particularly in areas impacted by ongoing coastal developments [70,71,72].
The VU mangrove plant species group includes genera Avicennia and Rhizophora, which protect coastal areas from erosion, salt water intrusion, storms, high tides, and floods [54,73,74]. The three VU Avicennia species (i.e., Avicennia bicolor, Avicennia rumphiana, and Avicennia integra) have experienced severe decline during 1980–2005 in Central America [68]. Avicennia bicolor, and three other VU mangrove species, i.e., Mora oleifera, Tabebuia palustris, and Pelliciera rhizophorae, have their native distribution in the Eastern Tropical Pacific region ranging from Mexico to Colombia [68,71,75] (Figure 1).
Several terrestrial animal species, like the yellow-shouldered blackbird (Agelaius xanthomus) and the Philippine cockatoo (Cacatua haematuropygia), which used many of the threatened mangroves species as the last refuge, have now gone extinct [63,76,77].

5. Drivers of Mangrove Deforestation

Figure 2 provides a representation of the drivers and driver groups of global mangrove deforestation identified by our consolidated literature. We identified two major groups of environmental drivers: Climate change and extreme events, and four groups of anthropogenic drivers: Aquaculture and agriculture, settlements and urbanization, industrialization and pollution, and flow modification. The driver groups and drivers’ distribution among the groups are drawn from the keyword sets used for the literature search and the returned literature results (Table 1). The environmental driver group referred to the drivers that originate from the environment, although they can be influenced by anthropogenic activities. By contrast, anthropogenic drivers originate from human and socio-economic activities, which might be triggered by available environmental (and mangrove) resources. The driver sub-group of climate change included gradual changes related to the global sea level, global and regional temperature and precipitation patterns, and associated geological changes, e.g., salinity intrusions. The subgroup of extreme events involved abrupt natural perturbations like cyclones and Tsunamis. Two driver subgroups emerged from the keyword “Land changes”: (1) Aquaculture and agriculture and (2) settlements and urbanization. The aquaculture and agriculture group referred to aquaculture- and agriculture-related activities that directly replaced mangrove forests, while settlements and urbanization included settlement expansions and urbanization processes that directly replaced or indirectly degraded mangrove forests, e.g., timber extraction for furniture and charcoal production and encroachments. The industrialization and pollution subgroup included drivers related to industrial and commercial activities and associated discharges and pollution. The final subgroup flow modification included drivers related to the diversion and withdrawal of upstream surface water and associated geological changes, e.g., subsidence and sedimentation. In Table 3, the environmental and anthropogenic drivers of mangrove deforestation and their geographic coverage of effects are presented. We explain the drivers and their impacts in Section 6 and Section 7.
Our reviewed studies pointed to aquaculture and agriculture, and related anthropogenic activities as the predominant driver of global mangrove deforestation, although the geographic coverage of their effects varied (Table 3). Gradual climate variations, i.e., sea-level rise, precipitation, and temperature changes, constitute the second major group of drivers of deforestation of the global mangrove forest with visible direct impacts on the equatorial regions, e.g., Central America and Asia. Settlements and urbanization constitute the third major group of drivers and were indicated as the main drivers of mangrove deforestation in Asia and Africa, including India, Bangladesh, Thailand, Vietnam, Mauritania, Comoros, Djibouti, and Somalia, by the majority of our consolidated literature (Table 3).

6. Environmental Drivers

6.1. Climate Change

Seventy-nine (39%) of our consolidated studies indicated climate-change-driven coastline erosion, salinity intrusion, and acidity as a dominant environmental driver of mangrove deforestation (Table 3). Climate change and impacts studied included alternations and variations in sea levels, temperature regimes, and precipitation patterns. These alternations were shown to impact the growth, recovery, and spatial distribution patterns of the mangrove forests as well as to change the composition of mangrove species [78]. The geographic coverage of climate change impacts covered almost all mangrove-containing countries (Table 3).

6.1.1. Sea-Level Rise

A review of published literature on the impacts of global climate change revealed sea-level rise as a major driver for mangrove loss [44,79,80]. Global-warming-driven melting of polar ice caps is projected to increase the global sea level by 0.18–0.59 m between 2090 and 2099 [81]. This may lead to a retreat of the mangrove forest belts in low-lying coastal regions and small islands, e.g., Palembang (Indonesia), Sagar Island (India), Sundarbans (Bangladesh), Shenzhen (China), and Small Island States, such as Solomon and Nuatambu [82,83,84,85,86]. For example, sea level is rising at a rate of 3.14 mm per year (which may increase up to 3.5 mm per year) at the coast of Sagar Island, India, which has led to an approximate 0.4 km2 areal loss of mangrove forests between 2000 and 2015 [87].
The increase in sea level can be coupled with extreme high water occurrences as a consequence of the fluctuations in oceanic circulations, such as El Nino Southern Oscillation (ENSO)’ [88] and ‘Northern Atlantic Oscillation (NAO)’ [89] and temperature regimes [90]. Such an increase in the high water occurrences may further increase the mean tidal level and impose coastal sediments to sulfide toxicity [5,35].

6.1.2. Changes in Temperature Regimes

There has been an increase in global temperature by 0.74 °C between 1906 and 2005, with a doubled warming rate (0.13 °C per decade) during the past five decades compared to the last 100 years average [91]. The warming could further accelerate, ranging from about 0.2 °C per decade to 0.4–0.8 °C per decade if emissions reduction strategies fail and aerosols were to be rapidly removed [92].
Increased temperature affects mangrove forests by changing the ecosystem configuration and the species distribution as well as by reducing mangrove productivity rate and changing their phenological patterns [53]. For example, the mangrove canopy heights and biomass depend on the temperature regimes. An exceedance of the temperature regime threshold may decrease canopy growth by 1–2 m [93]. Global warming caused an increase in the frequency and intensity of heat waves drive habitat losses in the mangrove forests through defoliation and intense herbivory. For example, Hong Kong lost 22% of the mangrove coverage due to summer heat-wave-driven defoliation in the flowering seasons leading to low reproductivity and fewer seedlings [94]. Exceedance of the temperature regimes may also drive the extinction of mangrove species, as dominantly for the cases of Sonneratia griffithii and Bruguiera hainesii in Southeast Asia [71].
“Hard freeze” (sudden temperature drop below −3 °C) is a natural phenomenon in winter in Southwest Florida, to which the local mangrove forests have adapted [65]. With the decreasing hard freeze events due to global warming, invasive plant species are advantaged and replacing local mangrove species in this region [95]. Moreover, the sudden high temperature occurrences before and after the hard freeze events slowed down the mangrove recovery preparations and follow-up processes [96]. However, the decreasing hard freeze events due to global warming coupled with sea-level rise may also expand the mangrove belts towards the higher altitudes and thus entail a northward shift in the global mangrove belt [97].

6.1.3. Changes in Precipitation Patterns

Global warming may cause a 25% increase in the global average precipitation by 2050 [98], although the regional patterns will vary, i.e., precipitation will increase in high latitudes, whereas it will decrease in most subtropical countries that contains mangrove forests [99,100]. The decreased precipitation with amplified evaporation can lead to high salinity in the coastal wetland zones, which, in turn, may adversely affect mangrove productivity, development, sapling, and seedling. Consequently, the coverage of mangrove forests may shrink, particularly where mangroves are already at their precipitation limits, e.g., in the arid zones of Africa and Central and South America [54,100,101]. The decreased precipitation may also drive groundwater depletion and reduce freshwater supply to mangrove forests, which further exacerbate salinity intrusion in coastal wetlands and mangrove forests [100,102,103].
The increased precipitation in high latitudes coupled with the increasing sea level may increase productivity and expand mangrove coverage towards the landward fringe of the tidal wetland zones [53]. The diversity of mangrove species may also increase as a result of increased fluvial sand deposits and nutrients, as well as abridged sulfate levels and decreased salinity in the high latitudinal regions, e.g., South Florida [33]. However, heavy and flash precipitation events can cause an overflow of coastal water bodies and introduce freshwater channels through the coastal uplands, which can transport sediments accumulated downstream back to upstream coastal areas. Such sediments overflow occurred in the Choluteca River on the Pacific coast of Honduras during Hurricane Mitch in 1998 [104] and in the Tijuana River in Southern California during the El Niño storm of 1993 [105], causing severe damage to the mangrove forests in these areas [105].

6.2. Extreme Events

The geographic location of the mangrove forests makes them particularly vulnerable to two groups of extreme events: (i) Cyclones and hurricanes and (ii) tsunamis [37]. According to the Intergovernmental Panel on Climate Change (IPCC), global warming resulted in the intensification of peak wind strength, tidal surge, and precipitation resulted from tropical cyclones and hurricanes, along with an increase in their frequency of occurrences [92]. These impact mangrove forests temporarily through three primary means: Sediment deposition, wind damage, and submersion [35]. The intense winds lead to sudden gusts and consequently topple stems, causing defoliation of the canopies and damage of the mangrove tree branches [106]. Cyclones and hurricanes may also uproot mangrove trees through strong wind flow [107]. This may also affect soil stability and lead to soil erosion in mangrove forests [105]. The long-term impacts of cyclones on the mangrove forests are the decreased fertility rate, delayed seedling seasons, and changes in the coastal hydrology, causing permanent ecosystem conversion [108]. Moreover, with the increased cyclone and hurricane occurrences, mangrove forests may lack the time required for recovery from the temporary damages and hence, may encounter permanent loss [64].
Damage to several mangrove regions by cyclones and hurricanes was noted in 47 (23%) of our consolidated studies (Table 3). For example, the Caribbean hurricane ‘Joan’ in 1988 caused 11% areal damage to the mangrove forests in the Caribbean and Central America with reduced soil stability, permanent loss of several mangrove species, and loss of forest density [109]. Sundarbans in Bangladesh and India, the world’s largest mangrove forest region, has encountered a high frequency of tropical cyclones and tidal surge since the 1960s [110]. The Sundarbans encountered areal damage of 2500 km2 by the tropical cyclone Sidr in 2007 [26]. Mangrove regions in Orissa and Tamilnadu in India experienced severe damage by several cyclones, e.g., the Super cyclone in 1999 [111], Vardah cyclone in 2016 [112], Ockhi cyclone in 2017 [113], and Gaja cyclone in 2018 [114].
Tsunamis have emerged as an environmental driver of mangrove deforestation, leaving permanent damage to coastal mangrove ecosystems [115]. Particularly, the Great Tsunami of 2004, which was originated in the Indian Ocean by an earthquake with the epicenter in Sumatra, Indonesia, on the Richter magnitude scale of 9.1–9.3, led to a major 300 km2 areal loss of mangrove forests in 14 countries [116,117]. Indonesia encountered the largest loss (35%), followed by India, Sri Lanka, and Thailand. Andaman Island, India, Aceh Province, Sumatra and Andaman coast, Thailand lost approximately 38 km2, 7.5 km2 and 3 km2 of mangrove forest coverage as a result of this tsunami, respectively [118,119,120]. Tsunami-driven mangrove cover and habitat losses were also observed later in Japan in 2011 and Papua New Guinea in 1999 [115,121,122].

7. Anthropogenic Drivers

7.1. Aquaculture and Agriculture

Aquaculture and agriculture were identified as the most dominant driver of global mangrove deforestation in our consolidated literature, accounting for approximately 47% loss of the global mangrove coverage [3,31,66]. Besides conversion of mangrove forests for fisheries and plantations, aquaculture and agriculture were associated with reduced ground water levels, and soil and water pollution from the effluents, which further intensified mangrove deforestation [123]. For example, the mangrove habitat loss in Kenya during 2000–2010 was associated with soil and water pollution [124], caused by agricultural and aquacultural intensification [66,125]. Aquaculture and agriculture were also shown to be the main driver of loss for the CR and EN mangrove species [71,72].
Globally, shrimp and other forms of aquaculture drove the conversion of 38% and 14% of the mangrove forest areas, respectively, between 1990 and 2020 [42]. Several Southeast Asian countries (Myanmar, Borneo, Malaysia, and Sumatra Island) have undergone a total 10% areal loss of mangroves between 2000 and 2012 due to aquaculture [38,126]. Thailand and Vietnam are the hotspots of mangrove deforestation by aquaculture that encountered mangrove forests loss at an average rate of 0.09 km2 per year between 1990 and 2020 [39]. In Vietnam, 1020 km2 of mangrove areas were converted into aquaculture between 1990 and 2019, followed by 694 km2 in Thailand and 65 km2 in Bangladesh. In India, about 40% of mangrove habitats on the western coastline have been transformed for aquaculture [127]. About 2055 km2 and 2110 km2 of mangrove marshlands have been transformed into shrimp and other fish farms in the Philippines and Indonesia, respectively [128]. A major decline of mangrove forests in Latin America, such as mangrove losses of 216 km2 in Ecuador, and 115 km2 in Honduras [108], is also associated with large scale shrimp farms and agricultural development [129],
Intensification of agriculture is another dominant driver of deforestation in all mangrove regions, particularly in South Asia and Latin America. For example, the majority of mangrove areas in the Philippines and Indonesia were replaced by agriculture [123]. The recent growth of oil palm plantations in Thailand, Malaysia, Sumatra, Colombia, and Indonesia is the main driver of mangrove forests loss in these areas [38,130]. The increasing demand for palm oil in Indonesia drove an areal expansion of palm plantations by 30% between 2012 and 2019 by replacing mangrove forests [131]. Mangroves in Central America have been mostly cleared for cattle grazing and industrial farming [132].

7.2. Settlements and Urbanization

The majority of our consolidated literature (98 studies) suggests human settlements and urbanization as an important anthropogenic driver of global mangrove deforestation [31,39] (see Table 3). Urbanization-related activities, such as clearing for urban infrastructures and timber extraction, have led to the destruction of significant mangrove areas in Asia and Africa during the past 20 years [38,133]. Human settlements occupy 150 km along the global coastal belt that previously contained mangrove forests, among other coastal wetlands [32,134]. The human population density in coastal regions is around 80 people per sq km [135], and urbanization in coastal areas is expanding, particularly in low-lying areas in developing countries [136]. For example, nearly 50% of the population in African countries and Bangladesh lives at the coastline, which affects the adjacent mangrove ecosystems [137].
The geographic coverage of the effect of settlements and urbanization is predominantly Asia and Africa [138]. Particularly, the Indian Ocean coastline, which contains mangrove forests with rich biodiversity expanding over several countries, such as Sri Lanka, Myanmar, Bangladesh, Singapore, Indonesia, and Australia, has been encountering mangrove coverage loss during the last three decades due to urban encroachment [139]. Sub-Saharan countries, such as Mauritania, Comoros, Djibouti, and Somalia, encountered rapid urban development and associated mangrove loss [140]. In Indonesia, the Philippines, Guinea, and Guinea-Bissau, mangrove forests have been heavily exploited for wood harvesting and timber extraction [64,141,142]. The VU species Avicennia rumphiana that dominantly occurs in Southeast Asia is threatened by the expansion of human settlements [19].

7.3. Industrialization and Pollution

Industrialization and pollution represent an emerging group of drivers of mangrove deforestation, as reported by 15% of our consolidated literature (Table 3) [142]. The Caribbean mangrove zone, which encountered the second-highest areal loss after Asia over the past three decades, was impacted by sewage, oil spill, solid wastes, and conversion to landfills, mainly driven by rapid industrialization [7,143,144]. In India, a considerable amount of stress on mangroves has been caused by domestic and industrial wastes, heavy metals, and other toxic discharges, for example, discharges from thermal power stations in Ennore and Tuticorin [145], Vedanta Sterlite Copper industry in Tuticorin, nuclear power plants in Kudankulam, and dye factories in Kalpakkam [146]. A recent project of the Indian Government for drilling in the Cauvery delta region for hydrocarbon and methane exploration threatened Pichavaram mangrove forest, Tamilnadu, which lies only 490 meters away from the exploration zone sheltering the inhabitants of Tamilnadu coast from natural calamities such as the 2004 tsunami [147].
Petroleum explorations, for example, in the Persian Gulf zone, resulted in oil spills from oil wells, oil refiners, and oil transports, which, in turn, led to pollution, driving substantial mangrove habitat loss [148]. These activities can also lead to accidents, for example, the Gulf of Mexico oil spill in 2010 affected 10% of the mangrove forests in the region, with a residue impact lasting for 10 years [149]. In January 2017, the toxic bunker oil spill along the coast of Chennai, India, spread 34 km across the Ennore coast and reached Pichavaram and Pulicat mangrove forests, affecting several native mangrove species [150].
Immobilization of heavy metals, such as copper, iron, magnesium, manganese, zinc, mercury, lead, and tin, has emerged as a driver of mangrove deforestation globally [151,152]. At a low level of heavy metal contamination, mangrove forests may act as biological pollution sinks [153]. Depending on the nutrients cycles and sediment characteristics, mangroves can dissolve metals in the deposits by exuding oxygen into the anoxic soil sediment through aerial roots [32,142,154,155]. However, the increasing contamination and discharges of heavy metals can exceed mangrove sink capacity and cause damage [152].

7.4. Flow Modification

Flow modification by diverting upland water flows diminishes mangrove productivity, as identified by 20 (8%) of our consolidated literature [133]. In Asia, the construction of upstream reservoirs and dams reduced the supply of sediments to several deltaic mangrove regions, including the Ganges and Cauvery in India, the Sundarbans deltas of India and Bangladesh, and the Indus river delta of Pakistan, leading to a decrease in sediment deficit in coastal wetlands of these regions [156]. Likewise, the annual sediment flow to the deltaic regions of China decreased from 1.1 billion metric tons in 1994 to 0.4 billion metric tons in 2009 [87,140].
Coastal erosion prevention structures and seawalls lead to the modification of surface run-off by obstructing downwards currents and inundation in the mangrove forests during flash flood events [64,150,157]. In the Mississippi Delta, the construction of flood control walls led to hydrological disturbances in the deltaic plain and isolation of the river from the Delta, affecting the mangrove zone [158,159]. The conversion of mangrove areas into salt pans and the construction of river dams are the major causes of mangrove deforestation in Brazil [160].

8. Interactions among Drivers

Mangrove deforestation is the outcome of complex interactions among the interconnected environmental and anthropogenic drivers [161]. Our consolidated literature suggests that the drivers may interact within and across their groups and may thus amplify their impacts on mangroves [116,140,162] (Figure 3). For example, climate-change-induced decreased precipitation and drought events lead to an increase in groundwater extraction and thus, flow modification [30]. The increase in the upstream groundwater extraction in turn exacerbate the salinity intrusion induced by climate change in the downstream coastal mangrove zones [163]. Moreover, expansion of aquaculture and agriculture also leads to an increase in groundwater extraction and flow modification in the coastal zones, which also, in turn, leads to an increased salinity intrusion [40].
Settlements and urbanization in the coastal wetland zones directly lead to interruptions and alternations in the hydrological and sedimentation processes [164]. Settlements and urbanization are also major sources of pollution and nutrient overload [12]. The urbanization processes also lead to an expansion of aquaculture and agriculture in the vicinity, which may also be sources of pollution in the mangroves [165]. In fact, the driver groups aquaculture and agriculture and industrialization and pollution exhibited the strongest interaction in our consolidated literature (Figure 3).
A considerable dieback of mangrove forests that occurred between 2015 and 2016 in the Northwest Australian coastline is an example of the interaction among driver groups regarding climate changes, extreme events, and flow modification [166,167]. The dieback is driven by a complex interaction among long-term temperature and precipitation anomalies, El Niño Southern Oscillation (ENSO) related variation in sea level, particularly a 20–30 cm decline in sea level during the immediate pre-dieback period and a 20–30% increase in soil salinization above the pre-dieback level [167]. The interaction among these drivers led to mangrove canopy loss, degraded vegetation health, and reduced recruitment, which in combination, led to an irreversible dieback event.
Climate change can amplify and widen the coverage of plant diseases and insect pests, such as fungal fruit and leaf diseases and wood-boring and leaf-feeding beetles, by spreading their habitats and creating favorable conditions for reproduction [18,168]. These diseases and pests can lead to mangrove deforestation through branch and stem cankers, dieback, and leaf galls [18]. Several mangrove species were shown to be vulnerable to these climate-change-led diseases and pests, such as Barringtonia racemosa is vulnerable to fruit and leaf diseases, and Hibiscus tiliaceus is vulnerable to herbivory beetles [168]. The dieback and canker levels observed in A. marina are also associated with these diseases and pests.
The effects of sea-level rise on the minerogenic mangroves are often mediated by the availability of coastal sediments [169,170]. The availability of sediments often depends on the local tectonic progressions, erosion, and other geological processes [171]. When the coastal sediment level and the accretion rates are exceeded by the mean tidal levels as a result of sea-level rise, the minerogenic mangrove forests may encounter areal loss or even collapse [105].
The impacts of sea-level rise (climate changes) have been exacerbated by coastal subsidence in several regions [172]. Coastal subsidence results from excessive extraction of subsurface ground water (flow modification) and variations in the thermal expansion across geographies, which lead to the vertical motion of the landform during the tectonic movement [173]. Coastal erosion and sediment deposition from the banks of large rivers have further increased subsidence levels through silt depositions [103]. The subsidence is particularly evident along the shorelines where mangrove forests area are located [10,173]. Several deltaic regions, including Changjiang river delta (China), Chao phraya delta (Thailand), and Mississippi river delta (Gulf of Mexico), were identified as extremely sensitive to sea-level fluctuations due to subsidence [159,174,175]. Most of the mangrove forests in the Ganges–Brahmaputra–Meghna delta in India and Bangladesh are affected simultaneously by subsidence due to ground water extraction (flow modification) and erosion from the monsoons rains, and accelerated sea-level-rise (climate changes), which has led to substantial habitat loss of the Sundarbans mangroves [176].
The aftermaths of extreme events may create opportunities for several anthropogenic drivers, such as aquaculture and agriculture [79,177,178]. For example, the South and North provinces in Thailand have converted the tsunami-damaged mangrove areas into aquaculture and agricultural lands [79]. Some mangrove species can withstand or recover and regenerate from the impacts of strong cyclones and typhoons [26,179,180]. However, a net decline in the overall mangrove forests coverage has been reported for many global regions as a result of the interactions with anthropogenic drivers. For example, around 1000 km2 of the degraded mangrove forests in Asia were converted to other land forms (e.g., for agriculture and aquaculture) between 1990 and 2020, largely triggered by the development policies for cyclone-damaged lands [29,35,178,181].
The drivers and their interactions may go beyond the specific driver groups of mangrove deforestation. Several coastal ecosystems, such as ocean algae, coral reefs, and seagrasses, are closely associated with adjacent mangrove forests [54,182]. For example, coral reefs supply nutrition to the downstream mangrove forests, shaping overall mangrove health and seedling rates [183]. Drivers affecting these adjacent coastal ecosystems also passively affect mangrove forests, e.g., bleaching of coral reefs will decrease nutrition flows and, in turn, lower the productivity of mangrove forests [54,184].
Mitigating drivers of mangrove deforestation may have co-benefits for other ecosystems. For example, bad shrimp farming practices and produced pollution degrade mangroves but also adjacent freshwater and coastal ecosystems [185]. Investments in proper shrimp farming infrastructure and development of sewage treatment plants will thus benefit both mangrove forests and those adjacent ecosystems [42]. The consequent increase in the availability of usable freshwater may, in turn, decrease the pressure on groundwater extraction and thus reduce salinity intrusion to mangroves.

9. Conclusions and Outlook

This review contributes to the global synthesis of mangrove deforestation scenarios over three decades, i.e., between 1990 and 2020. Our global level synthesis indicates the Southeast Asian region is particularly vulnerable to mangrove deforestation, with the highest loss of mangrove coverage between 1990 and 2020 (Table 2). Consequently, we urge for strong mangrove monitoring and conservation measures in the Asian region, particularly in countries like Indonesia, Malaysia, and Bangladesh.
Several technical difficulties have been reported by our consolidated studies regarding the monitoring of mangrove regions. For example, most of the deforested mangrove areas replaced with agriculture or other plantations have been misclassified as mangrove forests, particularly in Indonesia [126]. This is because oil palm plantations and palm orchards that replace mangrove forests may reflect the same color bands in satellite images [131]. Moreover, even though the mangrove forests in Brazil have been substantially affected by human settlements, aquaculture and water pollution, little mangrove area loss has been documented since 1980 [68].
Technical difficulties also remain in quantifying anthropogenic drivers’ impacts, for example, quantification of the impacts of population increase and urbanization on mangrove forests coverage in Asia [39,64,66]. The advent of satellite imageries and sophisticated image classification and detection techniques have advanced quantification and trend analyses for anthropogenic activities [31]. Future research should focus on advancing the quantification of the association between anthropogenic drivers and mangrove coverage changes in under studied regions.
Local extinction of threatened mangrove species may infer global loss. According to IUCN, there are no conservation measures specific to most of the threatened mangrove species. We, therefore, recommend continued monitoring and research on these species, as well as the inclusion of these species in the marine and coastal area protection programs [68]. Although mangroves are protected and marginally restored during the last decades in several regions (for example, Avicennia integra [73] has been conserved in a remote area of northern Australia [186,187] and mangrove deforestation has been reversed in Costa Rica [188]), little is known about the achievements of these local conservation efforts while mangrove areas globally continue to decline. Hence, global coordination of these in-situ conservation actions is required with correct management of the Protected Areas Network to fully protect species and the entire mangrove ecosystems [189,190].
The data for drivers available from certain areas needed to be consolidated to arrive at our global driver database, and therefore, a robust global drivers database for mangrove deforestation requires a precise global assessment, e.g., regular updates of Global Mangrove Watch [11]. Our review results can contribute to updating the datasets for assisting the development of policies for mangrove conservation. Such global level assessments will also be helpful for disentangling and quantifying the associations of climatic changes and anthropogenic activities with mangrove cover changes globally and also for predicting future mangrove patterns and provision of ecosystem services.

Author Contributions

A.K.B. and P.C. conceived the study. R.P. conducted the review under the supervision of A.K.B., P.C. and M.M.R. A.K.B. and R.P. wrote the article and all reviewed and revised the article. M.M.R. provided information and input regarding mangrove species. All authors have read and agreed to the published version of the manuscript.

Funding

This study was supported through the FCT (Fundação para a Ciência e a Tecnologia) under the projects PTDC/CTA-AMB/28438/2017—ASEBIO, UIDB/04152/2020—Centro de Investigação em Gestão de Informação (MagIC), UIDB/04152/2020 Centro de Investigação em Gestão de Informação (MagIC) and UID/AGR/04129/2020 (LEAF/ISA).

Conflicts of Interest

The authors declare no conflict of interest.

Appendix A

Sustainability 14 04433 g0a1 550
Figure A1. The schema for this review following the PRISMA framework [50].
Figure A1. The schema for this review following the PRISMA framework [50].
Sustainability 14 04433 g0a1

References

  1. Friess, D.A.; Rogers, K.; Lovelock, C.E.; Krauss, K.W.; Hamilton, S.E.; Lee, S.Y.; Lucas, R.; Primavera, J.; Rajkaran, A.; Shi, S. The State of the World’s Mangrove Forests: Past, Present, and Future. Annu. Rev. Environ. Resour. 2019, 44, 89–115. [Google Scholar] [CrossRef] [Green Version]
  2. Romañach, S.S.; DeAngelis, D.L.; Koh, H.L.; Li, Y.; Teh, S.Y.; Raja Barizan, R.S.; Zhai, L. Conservation and Restoration of Mangroves: Global Status, Perspectives, and Prognosis. Ocean Coast. Manag. 2018, 154, 72–82. [Google Scholar] [CrossRef]
  3. Worthington, T.; Spalding, M. Mangrove Restoration Potential. A Global Map Highlighting a Critical Opportunity; The Nature Conservancy: Arlington, VA, USA, 2018; p. 36. [Google Scholar]
  4. Rivera-Monroy, V.H.; Lee, S.Y.; Kristensen, E.; Twilley, R.R. Mangrove Ecosystems: A Global Biogeographic Perspective; Springer: Cham, The Netherlands, 2017. [Google Scholar]
  5. Barbier, E.B. The Protective Service of Mangrove Ecosystems: A Review of Valuation Methods. Mar. Pollut. Bull. 2016, 109, 676–681. [Google Scholar] [CrossRef] [PubMed]
  6. Carugati, L.; Gatto, B.; Rastelli, E.; Lo Martire, M.; Coral, C.; Greco, S.; Danovaro, R. Impact of Mangrove Forests Degradation on Biodiversity and Ecosystem Functioning. Sci. Rep. 2018, 8, 13298. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  7. Kristensen, E.; Bouillon, S.; Dittmar, T.; Marchand, C. Organic Carbon Dynamics in Mangrove Ecosystems: A Review. Mangrove Ecol. Appl. For. Costal Zone Manag. 2008, 89, 201–219. [Google Scholar] [CrossRef] [Green Version]
  8. Alongi, D.M. Carbon Cycling and Storage in Mangrove Forests. Annu. Rev. Mar. Sci. 2014, 6, 195–219. [Google Scholar] [CrossRef]
  9. Spalding, M. The Global Distribution and Status of Mangrove Ecosystems. Int. NewsLett. Coast. Manag. 1997, 1, 20–21. [Google Scholar]
  10. Alongi, D.M. Mangrove Forests: Resilience, Protection from Tsunamis, and Responses to Global Climate Change. Estuar. Coast. Shelf Sci. 2008, 78, 1–13. [Google Scholar] [CrossRef]
  11. Spalding, M.D.; Leal, M. The State of the World’s Mangroves; Global Mangrove Alliance. 2021, p. 41. Available online: https://www.mangrovealliance.org/mangrove-forests/ (accessed on 7 February 2022).
  12. Worthington, T.A.; Andradi-Brown, D.A.; Bhargava, R.; Buelow, C.; Bunting, P.; Duncan, C.; Fatoyinbo, L.; Friess, D.A.; Goldberg, L.; Hilarides, L.; et al. Harnessing Big Data to Support the Conservation and Rehabilitation of Mangrove Forests Globally. One Earth 2020, 2, 429–443. [Google Scholar] [CrossRef]
  13. Bunting, P.; Rosenqvist, A.; Lucas, R.; Rebelo, L.-M.; Hilarides, L.; Thomas, N.; Hardy, A.; Itoh, T.; Shimada, M.; Finlayson, C. The Global Mangrove Watch—A New 2010 Global Baseline of Mangrove Extent. Remote Sens. 2018, 10, 1669. [Google Scholar] [CrossRef] [Green Version]
  14. Feller, I.C.; Friess, D.A.; Krauss, K.W.; Lewis, R.R. The State of the World’s Mangroves in the 21st Century under Climate Change. Hydrobiologia 2017, 803, 1–12. [Google Scholar] [CrossRef] [Green Version]
  15. Primavera, J.H.; Esteban, J.M.A. A Review of Mangrove Rehabilitation in the Philippines: Successes, Failures and Future Prospects. Wetl. Ecol. Manag. 2008, 16, 345–358. [Google Scholar] [CrossRef]
  16. Cormier-Salem, M.C.; Bernatets, C.; Sarr, O. Mangrove System Sustainability: Public Incentives and Local Strategies in West Africa. In Tropical Deltas and Coastal Zones: Food Production, Communities and Environment at the Land-Water Interface; CABI Publishing: Bonn, Germany, 2010. [Google Scholar]
  17. Asbridge, E.; Lucas, R.; Accad, A.; Dowling, R. Mangrove Response to Environmental Changes Predicted under Varying Climates: Case Studies from Australia. Curr. For. Rep. 2015, 1, 178–194. [Google Scholar] [CrossRef] [Green Version]
  18. Giesen, W.; Wulffraat, S.; Zieren, M.; Scholten, L. Mangrove Guidebook for Southeast Asia; UN Food and Agricultural Organization: Phnom Penh, Combodi, 2007. [Google Scholar]
  19. Mangaoang, C.; Flores, A. Inventory of Mangroves in Katunggan Coastal Eco-Park, Sultan Kudarat Province, the Philippines. Bonorowo Wetl. 2019, 9. [Google Scholar] [CrossRef]
  20. Ragavan, P.; Saxena, M.; Saxena, A.; Mohan, P.M.; Sachithanandam, V.; Coomar, T. Floral Composition and Taxonomy of Mangroves of Andaman and Nicobar Islands. Indian J. Geo. Mar. Sci. 2014, 43, 1031–1044. [Google Scholar]
  21. Sheue, C.R.; Liu, H.Y.; Yong, J.W.H. Kandelia Obovata (Rhizophoraceae), a New Mangrove Species from Eastern Asia. Taxon 2003, 52, 287–294. [Google Scholar] [CrossRef]
  22. Dahdouh-Guebas, F.; Van Pottelbergh, I.; Kairo, J.G.; Cannicci, S.; Koedam, N. Human-Impacted Mangroves in Gazi (Kenya): Predicting Future Vegetation Based on Retrospective Remote Sensing, Social Surveys, and Tree Distribution. Mar. Ecol. Prog. Ser. 2004, 272, 77–92. [Google Scholar] [CrossRef] [Green Version]
  23. Fromard, F.; Vega, C.; Proisy, C. Half a Century of Dynamic Coastal Change Affecting Mangrove Shorelines of French Guiana. A Case Study Based on Remote Sensing Data Analyses and Field Surveys. Mar. Geol. 2004, 208, 265–280. [Google Scholar] [CrossRef]
  24. López-Angarita, J.; Roberts, C.M.; Tilley, A.; Hawkins, J.P.; Cooke, R.G. Mangroves and People: Lessons from a History of Use and Abuse in Four Latin American Countries. For. Ecol. Manag. 2016, 368, 151–162. [Google Scholar] [CrossRef] [Green Version]
  25. Djamaluddin, R.; Brown, B.; Lewis, R.R. The Practice of Hydrological Restoration to Rehabilitate Abandoned Shrimp Ponds in Bunaken National Park, North Sulawesi, Indonesia. Biodiversitas 2019, 20, 160–170. [Google Scholar] [CrossRef] [Green Version]
  26. Bhowmik, A.K.; Cabral, P. Cyclone Sidr Impacts on the Sundarbans Floristic Diversity. Earth Sci. Res. 2013, 2, 62–79. [Google Scholar] [CrossRef] [Green Version]
  27. Williams, N. Tsunami Insight to Mangrove Value. Curr. Biol. 2005, 15, R73. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  28. Primavera, J.H. Development and Conservation of Philippine Mangroves: Institutional Issues. Ecol. Econ. 2000, 35, 91–106. [Google Scholar] [CrossRef]
  29. Maung, W.S.; Sasaki, J. Assessing the Natural Recovery of Mangroves after Human Disturbance Using Neural Network Classification and Sentinel-2 Imagery in Wunbaik Mangrove Forest, Myanmar. Remote Sens. 2021, 13, 52. [Google Scholar] [CrossRef]
  30. Islam, S.; Gnauck, A. Water Shortage in the Gorai River Basin and Damage of Mangrove Wetland Ecosystems in Sundarbans, Bangladesh. In Proceedings of the 3rd International Conference on Water & Flood Management (ICWFM-2011), Dhaka, Bangladesh, 8–10 January 2011. [Google Scholar]
  31. Goldberg, L.; Lagomasino, D.; Thomas, N.; Fatoyinbo, T. Global Declines in Human-driven Mangrove Loss. Glob. Chang. Biol. 2020, 26, 5844–5855. [Google Scholar] [CrossRef]
  32. Tam, N.F.Y. Pollution Studies on Mangroves in Hong Kong and Mainland China. In The Environment in Asia Pacific Harbours; Springer: Dordrecht, The Netherlands, 2006; ISBN 140203654X. [Google Scholar]
  33. Baldwin, A.; Egnotovich, M.; Ford, M.; Platt, W. Regeneration in Fringe Mangrove Forests Damaged by Hurricane Andrew. Plant Ecol. 2001, 157, 151–164. [Google Scholar] [CrossRef]
  34. Godoy, M.D.P.; De Lacerda, L.D. Mangroves Response to Climate Change: A Review of Recent Findings on Mangrove Extension and Distribution. An. Acad. Bras. Cienc. 2015, 87, 651–667. [Google Scholar] [CrossRef] [Green Version]
  35. Krauss, K.W.; Osland, M.J. Tropical Cyclones and the Organization of Mangrove Forests: A Review. Ann. Bot. 2020, 125, 213–234. [Google Scholar] [CrossRef]
  36. Charrua, A.B.; Padmanaban, R.; Cabral, P.; Bandeira, S.; Romeiras, M.M. Impacts of the Tropical Cyclone Idai in Mozambique: A Multi-Temporal Landsat Satellite Imagery Analysis. Remote Sens. 2021, 13, 201. [Google Scholar] [CrossRef]
  37. Das, S. Can Mangroves Minimize Property Loss during Big Storms? An Analysis of House Damages Due to the Super Cyclone in Orissa; The South Asian Network for Development and Environmental Economics: Colombo, Sri Lanka, 2009; ISBN 978-9937-8218-1-0. [Google Scholar]
  38. Richards, D.R.; Friess, D.A. Rates and Drivers of Mangrove Deforestation in Southeast Asia, 2000–2012. Proc. Natl. Acad. Sci. USA 2016, 113, 344–349. [Google Scholar] [CrossRef] [Green Version]
  39. Gandhi, S.; Jones, T.G. Identifying Mangrove Deforestation Hotspots in South Asia, Southeast Asia and Asia-Pacific. Remote Sens. 2019, 11, 728. [Google Scholar] [CrossRef] [Green Version]
  40. Charrua, A.B.; Bandeira, S.O.; Catarino, S.; Cabral, P.; Romeiras, M.M. Assessment of the Vulnerability of Coastal Mangrove Ecosystems in Mozambique. Ocean Coast. Manag. 2020, 189, 105145. [Google Scholar] [CrossRef]
  41. Neumann, B.; Vafeidis, A.T.; Zimmermann, J.; Nicholls, R.J. Future Coastal Population Growth and Exposure to Sea-Level Rise and Coastal Flooding—A Global Assessment. PLoS ONE 2015, 10, e0118571. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  42. Jayanthi, M.; Thirumurthy, S.; Muralidhar, M.; Ravichandran, P. Impact of Shrimp Aquaculture Development on Important Ecosystems in India. Glob. Environ. Chang. 2018, 52, 10–21. [Google Scholar] [CrossRef]
  43. Sherrod, C.L.; McMillan, C. Black Mangrove, Avicennia Germinans, in Texas: Past and Present Distribution. Contrib. Mar. Sci. 1981, 24, 115–131. [Google Scholar]
  44. Fakhruddin, B.; Mahalingam, R.; Padmanaban, R. Sustainable Development Goals for Reducing the Impact of Sea Level Rise on Mangrove Forests. Indian J. Geo. Mar. Sci. 2018, 47, 1947–1958. [Google Scholar]
  45. Madhu, N.V.; Maheswaran, P.A.; Jyothibabu, R.; Sunil, V.; Revichandran, C.; Balasubramanian, T.; Gopalakrishnan, T.C.; Nair, K.K.C. Enhanced Biological Production off Chennai Triggered by October 1999 Super Cyclone (Orissa). Curr. Sci. 2002, 82, 1472–1479. [Google Scholar]
  46. Das, S.; Crépin, A.-S. Mangroves Can Provide Protection against Wind Damage during Storms. Estuar. Coast. Shelf Sci. 2013, 134, 98–107. [Google Scholar] [CrossRef]
  47. Valiela, I.; Bowen, J.L.; Yotk, J.K. Mangrove Forests: One of the World’s Threatened Major Tropical Environments. BioScience 2001, 51, 807. [Google Scholar] [CrossRef] [Green Version]
  48. Maina, J.M.; Bosire, J.O.; Kairo, J.G.; Bandeira, S.O.; Mangora, M.M.; Macamo, C.; Ralison, H.; Majambo, G.; Poulter, B. Identifying Global and Local Drivers of Change in Mangrove Cover and the Implications for Management. Glob. Ecol. Biogeogr. 2021, 30, 2057–2069. [Google Scholar] [CrossRef]
  49. Thomas, N.; Lucas, R.; Bunting, P.; Hardy, A.; Rosenqvist, A.; Simard, M. Distribution and Drivers of Global Mangrove Forest Change, 1996–2010. PLoS ONE 2017, 12, e0179302. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  50. Moher, D.; Liberati, A.; Tetzlaff, J.; Altman, D.G. Prisma Group Preferred Reporting Items for Systematic Reviews and Meta-Analyses: The PRISMA Statement. PLoS Med. 2009, 6, e1000097. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  51. UN Food and Agricultural Organization. Coordinating Working Party on Fishery Statistics (CWP). 2019. Available online: https://www.fao.org/fishery/cwp/en (accessed on 7 February 2022).
  52. Hamilton, S.E.; Casey, D. Creation of a High Spatio-Temporal Resolution Global Database of Continuous Mangrove Forest Cover for the 21st Century (CGMFC-21). Glob. Ecol. Biogeogr. 2016, 25, 729–738. [Google Scholar] [CrossRef]
  53. Ward, R.D.; Friess, D.A.; Day, R.H.; Mackenzie, R.A. Impacts of Climate Change on Mangrove Ecosystems: A Region by Region Overview. Ecosyst. Health Sustain. 2016, 2, e01211. [Google Scholar] [CrossRef] [Green Version]
  54. Kodikara, K.A.S.; Jayatissa, L.P.; Huxham, M.; Dahdouh-Guebas, F.; Koedam, N. The Effects of Salinity on Growth and Survival of Mangrove Seedlings Changes with Age. Acta Bot. Bras. 2018, 32, 37–46. [Google Scholar] [CrossRef] [Green Version]
  55. Bjorkman, O.; Demmig, B.; Andrews, T.J. Mangrove Photosynthesis: Response to High-Irradiance Stress. Aust. J. Plant Physiol. 1988, 15, 43–61. [Google Scholar] [CrossRef]
  56. Hamilton, S.E. Botany of Mangroves. In Coastal Research Library; Springer: Cham, The Netherlands, 2020; Volume 33, pp. 1–40. [Google Scholar]
  57. Mitsch, W.J.; Wu, X.; Nairn, R.W.; Weihe, P.E.; Wang, N.; Deal, R.; Boucher, C.E. Creating and Restoring Wetlands. BioScience 1998, 48, 1019–1030. [Google Scholar] [CrossRef]
  58. Giri, C.; Ochieng, E.; Tieszen, L.L.; Zhu, Z.; Singh, A.; Loveland, T.; Masek, J.; Duke, N. Status and Distribution of Mangrove Forests of the World Using Earth Observation Satellite Data. Glob. Ecol. Biogeogr. 2011, 20, 154–159. [Google Scholar] [CrossRef]
  59. Asante, W.A.; Acheampong, E.; Boateng, K.; Adda, J. The Implications of Land Tenure and Ownership Regimes on Sustainable Mangrove Management and Conservation in Two Ramsar Sites in Ghana. For. Policy Econ. 2017, 85, 65–75. [Google Scholar] [CrossRef]
  60. UN Food and Agricultural Organization (FAO). Global Forest Resources Assessment 2020—Key Findings. Rome. 2020. Available online: https://doi.org/10.4060/ca8753en (accessed on 7 February 2022).
  61. Global Mangrove Alliance. FAO Reviews 30 Years of Global Forest Data. 2020. Available online: https://www.mangrovealliance.org/news/30-years-of-global-forest-data/ (accessed on 7 February 2022).
  62. Bunting, P.; Rosenqvist, A.; Hilarides, L.; Lucas, R.M.; Thomas, N. Global Mangrove Watch: Updated 2010 Mangrove Forest Extent (v2.5). Remote Sens. 2022, 14, 1034. [Google Scholar] [CrossRef]
  63. Luther, D.A.; Greenberg, R. Mangroves: A Global Perspective on the Evolution and Conservation of Their Terrestrial Vertebrates. BioScience 2009, 59, 602–612. [Google Scholar] [CrossRef] [Green Version]
  64. Giri, C.; Long, J.; Abbas, S.; Mani Murali, R.; Qamer, F.M.; Pengra, B.; Thau, D. Distribution and Dynamics of Mangrove Forests of South Asia. J. Environ. Manag. 2015, 48, 101–111. [Google Scholar] [CrossRef] [PubMed]
  65. Ximenes, A.C.; Ponsoni, L.; Lira, C.F.; Koedam, N.; Dahdouh-Guebas, F. Does Sea Surface Temperature Contribute to Determining Range Limits and Expansion of Mangroves in Eastern South America (Brazil)? Remote Sens. 2018, 10, 1787. [Google Scholar] [CrossRef] [Green Version]
  66. Latiff, A.A.; Faridah-Hanum, I.B. Mangrove Ecosystem of Malaysia: Status, Challenges and Management Strategies. In Mangrove Ecosystems of Asia; Springer: New York, NY, USA, 2014; pp. 1–22. ISBN 978-1-4614-8581-0. [Google Scholar]
  67. Hutchison, J.; Manica, A.; Swetnam, R.; Balmford, A.; Spalding, M. Predicting Global Patterns in Mangrove Forest Biomass. Conserv. Lett. 2014, 7, 233–240. [Google Scholar] [CrossRef] [Green Version]
  68. Polidoro, B.A.; Carpenter, K.E.; Collins, L.; Duke, N.C.; Ellison, A.M.; Ellison, J.C.; Farnsworth, E.J.; Fernando, E.S.; Kathiresan, K.; Koedam, N.E.; et al. The Loss of Species: Mangrove Extinction Risk and Geographic Areas of Global Concern. PLoS ONE 2010, 5, e10095. [Google Scholar] [CrossRef] [PubMed]
  69. Long, J.; Napton, D.; Giri, C.; Graesser, J. A Mapping and Monitoring Assessment of the Philippines’ Mangrove Forests from 1990 to 2010. J. Coast. Res. 2014, 294, 260–271. [Google Scholar] [CrossRef]
  70. Duke, N.; Kathiresan, K.; Salmo, S.G., III; Fernando, E.S.; Peras, J.R.; Sukardjo, S.; Miyagi, T.; Ellison, J.; Koedam, N.E.; Wang, Y.; et al. Camptostemon philippinense. The IUCN Red List of Threatened Species. Available online: https://www.iucnredlist.org/species/178808/7612909 (accessed on 7 February 2022).
  71. Duke, N.; Kathiresan, K.; Salmo, S.G., III; Fernando, E.S.; Peras, J.R.; Sukardjo, S.; Miyagi, T. Sonneratia griffithii. The IUCN Red List of Threatened Species. Available online: https://www.iucnredlist.org/species/178799/7609832 (accessed on 7 February 2022).
  72. Duke, N.; Kathiresan, K.; Salmo, S.G., III; Fernando, E.S.; Peras, J.R.; Sukardjo, S.; Miyagi, T.; Ellison, J.; Koedam, N.E.; Wang, Y.; et al. Bruguiera hainesii. The IUCN Red List of Threatened Species. 2010. Available online: https://www.iucnredlist.org/species/178834/7621565 (accessed on 7 February 2022).
  73. Huang, X.; Zhang, L.; Wang, L. Evaluation of Morphological Texture Features for Mangrove Forest Mapping and Species Discrimination Using Multispectral IKONOS Imagery. IEEE Geosci. Remote Sens. Lett. 2009, 6, 393–397. [Google Scholar] [CrossRef] [Green Version]
  74. Pin, T.G.; Supriatna, J.; Takarina, N.D.; Tambunan, R.P. Mangrove Diversity and Suitability Assessments for Ecotourism in Cimalaya Wetan Coast, Karawang District, Indonesia. Biodiversitas 2021, 22. [Google Scholar] [CrossRef]
  75. Day, J.W.; Conner, W.H.; Ley-Lou, F.; Day, R.H.; Navarro, A.M. The Productivity and Composition of Mangrove Forests, Laguna de Términos, Mexico. Aquat. Bot. 1987, 27, 267–284. [Google Scholar] [CrossRef]
  76. Rowley, I.; Kirwan, G.M. Philippine Cockatoo (Cacatua haematuropygia). Birds of the World. 2020. Available online: https://birdsoftheworld.org/bow/species/phicoc1/cur/introduction (accessed on 6 February 2022).
  77. Liu, I.A. Conservation Genetics and Genetic Mating System of the Yellow-Shouldered Blackbird (Agelaius xanthomus), an Endangered Island Endemic. Conserv. Genet. 2015, 16, 1041–1053. [Google Scholar] [CrossRef]
  78. Field, C.D. Impact of Expected Climate Change on Mangroves. Hydrobiologia 1995, 295, 75–81. [Google Scholar] [CrossRef]
  79. Cochard, R.; Ranamukhaarachchi, S.L.; Shivakoti, G.P.; Shipin, O.V.; Edwards, P.J.; Seeland, K.T. The 2004 Tsunami in Aceh and Southern Thailand: A Review on Coastal Ecosystems, Wave Hazards and Vulnerability. Perspect. Plant Ecol. Evol. Syst. 2008, 10, 3–40. [Google Scholar] [CrossRef]
  80. Woodroffe, C.D. The Impact of Sea-Level Rise on Mangrove Shorelines. Prog. Phys. Geogr. 1990, 14, 483–520. [Google Scholar] [CrossRef]
  81. Saintilan, N.; Khan, N.S.; Ashe, E.; Kelleway, J.J.; Rogers, K.; Woodroffe, C.D.; Horton, B.P. Thresholds of Mangrove Survival under Rapid Sea Level Rise. Science 2020, 368, 1118–1121. [Google Scholar] [CrossRef]
  82. Andriyono, S.; Masithah, E.D.; Pramono, H.; Suciyono, S. First Record of The Burrowing Goby Trypuchen Vagina from Pangpang Bay, Indonesia. ILMU Kelaut. Indones. J. Mar. Sci. 2019, 24, 127–131. [Google Scholar] [CrossRef]
  83. Mantri, V.A.; Mishra, A.K. On Monitoring Mangrove Vegetation of Sagar Island by Remote Sensing. Natl. Acad. Sci. Lett.-India 2006, 29, 45–48. [Google Scholar]
  84. Hoque, A.K.F.; Datta, D.K. The Mangroves of Bangladesh. Int. J. Ecol. Environ. Sci. 2005, 31, 245–253. [Google Scholar]
  85. Feng, Z.; Tan, G.; Xia, J.; Shu, C.; Chen, P.; Wu, M.; Wu, X. Dynamics of Mangrove Forests in Shenzhen Bay in Response to Natural and Anthropogenic Factors from 1988 to 2017. J. Hydrol. 2020, 591, 125271. [Google Scholar] [CrossRef]
  86. Albert, S.; Saunders, M.I.; Roelfsema, C.M.; Leon, J.X.; Johnstone, E.; Mackenzie, J.R.; Hoegh-Guldberg, O.; Grinham, A.R.; Phinn, S.R.; Duke, N.C.; et al. Winners and Losers as Mangrove, Coral and Seagrass Ecosystems Respond to Sea-Level Rise in Solomon Islands. Environ. Res. Lett. 2017, 12, 94009. [Google Scholar] [CrossRef]
  87. Li, S.; Meng, X.; Ge, Z.; Zhang, L. Evaluation of the Threat from Sea-Level Rise to the Mangrove Ecosystems in Tieshangang Bay, Southern China. Ocean Coast. Manag. 2015, 109, 1–8. [Google Scholar] [CrossRef]
  88. Schultz, K.A. El Niño/Southern Oscillation and the Seasonal Predictability of Tropical Cyclones. In El Nino and the Southern Oscillation; Cambridge University Press: Cambridge, UK, 2001; Volume 76, pp. 149–182. ISBN 9780511573125. [Google Scholar]
  89. Chen, S.; Wu, R.; Chen, W. The Changing Relationship between Interannual Variations of the North Atlantic Oscillation and Northern Tropical Atlantic SST. J. Clim. 2015, 28, 485–504. [Google Scholar] [CrossRef]
  90. Jevrejeva, S.; Jackson, L.P.; Riva, R.E.M.; Grinsted, A.; Moore, J.C. Coastal Sea Level Rise with Warming above 2 °C. Proc. Natl. Acad. Sci. USA 2016, 113, 13342–13347. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  91. Trenberth, K.E. Observations: Surface and Atmospheric Climate Change. Changes 2007, 164. [Google Scholar] [CrossRef] [Green Version]
  92. Meehl, G.A.; Stocker, T.F. Chapter 10. Global Climate Projections. In Climate Change 2007: The Physical Science Basis; 2007. Available online: https://www.ipcc.ch/report/ar4/wg1/ (accessed on 1 August 2017).
  93. Hu, T.; Zhang, Y.Y.; Su, Y.; Zheng, Y.; Lin, G.; Guo, Q. Mapping the Global Mangrove Forest Aboveground Biomass Using Multisource Remote Sensing Data. Remote Sens. 2020, 12, 1690. [Google Scholar] [CrossRef]
  94. Liu, M.; Zhang, H.; Lin, G.; Lin, H.; Tang, D. Zonation and Directional Dynamics of Mangrove Forests Derived from Time-Series Satellite Imagery in Mai Po, Hong Kong. Sustainability 2018, 10, 1913. [Google Scholar] [CrossRef] [Green Version]
  95. Cavanaugh, K.C.; Parker, J.D.; Cook-Patton, S.C.; Feller, I.C.; Williams, A.P.; Kellner, J.R. Integrating Physiological Threshold Experiments with Climate Modeling to Project Mangrove Species’ Range Expansion. Glob. Chang. Biol. 2015, 21, 1928–1938. [Google Scholar] [CrossRef] [Green Version]
  96. Stevens, P.W.; Fox, S.L.; Montague, C.L. The Interplay between Mangroves and Saltmarshes at the Transition between Temperate and Subtropical Climate in Florida. Wetl. Ecol. Manag. 2006, 14, 435–444. [Google Scholar] [CrossRef]
  97. Cavanaugh, K.C.; Dangremond, E.M.; Doughty, C.L.; Williams, A.P.; Parker, J.D.; Hayes, M.A.; Rodriguez, W.; Feller, I.C. Climate-Driven Regime Shifts in a Mangrove–Salt Marsh Ecotone over the Past 250 Years. Proc. Natl. Acad. Sci. USA 2019, 116, 21602–21608. [Google Scholar] [CrossRef] [Green Version]
  98. McCarthy, M.P.; Best, M.J.; Betts, R.A. Climate Change in Cities due to Global Warming and Urban Effects. Geophys. Res. Lett. 2010, 37, 415. [Google Scholar] [CrossRef] [Green Version]
  99. Hoegh-Guldberg, O.; Jacob, D.; Taylor, M.; Bindi, M.; Brown, S.; Camilloni, I.; Diedhiou, A.; Djalante, R.; Ebi, K.L.; Engelbrecht, F.; et al. Chapter 3: Impacts of 1.5 °C Global Warming on Natural and Human Systems. In Global Warming of 1.5 °C an IPCC Special Report on the Impacts of Global Warming of 1.5 °C above Pre-Industrial Levels and Related Global Greenhouse Gas Emission Pathways, in the Context of Strengthening the Global Response to the Threat of Climate Change. 2018. Available online: https://www.ipcc.ch/sr15/ (accessed on 1 August 2017).
  100. Chen, Y.; Ye, Y. Effects of Salinity and Nutrient Addition on Mangrove Excoecaria Agallocha. PLoS ONE 2014, 9, e93337. [Google Scholar] [CrossRef]
  101. Bunt, J.S.; Williams, W.T.; Clay, H.J. River Water Salinity and the Distribution of Mangrove Species along Several Rivers in North Queensland. Aust. J. Bot. 1982, 30, 401–412. [Google Scholar] [CrossRef]
  102. Manna, S.; Chaudhuri, K.; Bhattacharyya, S.; Bhattacharyya, M. Dynamics of Sundarban Estuarine Ecosystem: Eutrophication Induced Threat to Mangroves. Saline Syst. 2010, 6, 8. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  103. Krauss, K.W.; Lovelock, C.E.; McKee, K.L.; López-Hoffman, L.; Ewe, S.M.L.; Sousa, W.P. Environmental Drivers in Mangrove Establishment and Early Development: A Review. Aquat. Bot. 2008, 89, 105–127. [Google Scholar] [CrossRef]
  104. Fickert, T. Better Resilient than Resistant-Regeneration Dynamics of Storm-Disturbed Mangrove Forests on the Bay Island of Guanaja (Honduras) during the First Two Decades after Hurricane Mitch (October 1998). Diversity 2018, 10, 8. [Google Scholar] [CrossRef] [Green Version]
  105. Cahoon, D.R. A Review of Major Storm Impacts on Coastal Wetland Elevations. Estuaries Coasts 2006, 29, 889–898. [Google Scholar] [CrossRef]
  106. Granek, E.F.; Ruttenberg, B.I. Protective Capacity of Mangroves during Tropical Storms: A Case Study from “Wilma” and “Gamma” in Belize. Mar. Ecol. Prog. Ser. 2007, 343, 101–105. [Google Scholar] [CrossRef] [Green Version]
  107. Rivera-Monroy, V.H.; Danielson, T.M.; Castañeda-Moya, E.; Marx, B.D.; Travieso, R.; Zhao, X.; Gaiser, E.E.; Farfan, L.M. Long-Term Demography and Stem Productivity of Everglades Mangrove Forests (Florida, USA): Resistance to Hurricane Disturbance. For. Ecol. Manag. 2019, 440, 79–91. [Google Scholar] [CrossRef]
  108. Cahoon, D.R.; Hensel, P.; Rybczyk, J.; McKee, K.L.; Proffitt, C.E.; Perez, B.C. Mass Tree Mortality Leads to Mangrove Peat Collapse at Bay Islands, Honduras after Hurricane Mitch. J. Ecol. 2003, 91, 1093–1105. [Google Scholar] [CrossRef]
  109. Roth, L.C. Hurricanes and Mangrove Regeneration: Effects of Hurricane Joan, October 1988, on the Vegetation of Isla Del Venado, Bluefields, Nicaragua. Biotropica 1992, 24, 375. [Google Scholar] [CrossRef] [Green Version]
  110. Ahmed, A.; Aziz, A.; Khan, A.N.A.; Islam, M.N.; Iqubal, K.F.; Nazma, M.; Islam, M.S. Tree Diversity as Affected by Salinity in the Sundarban Mangrove Forests, Bangladesh. Bangladesh J. Bot. 2011, 40, 197–202. [Google Scholar] [CrossRef] [Green Version]
  111. Das, S.; Vincent, J.R. Mangroves Protected Villages and Reduced Death Toll during Indian Super Cyclone. Proc. Natl. Acad. Sci. USA 2009, 106, 7357–7360. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  112. Ayyappan, K.; Thiruvenkatasamy, K.; Arumugam, T. Impact Assessment Study of Cyclone Vardah on Chennai, On East Coast of Tamil Nadu, India. TERI Inf. Dig. Energy Environ. 2017, 16, 13–20. [Google Scholar]
  113. Muthusamy, S.; Sivakumar, K.; Durai, A.; Sheriff, M. Ockhi Cyclone and Its Impact in the Kanyakumari District of Southern Tamilnadu, India: An Aftermath Analysis. Int. J. Recent Res. Asp. 2018, 1, 466–469. [Google Scholar]
  114. Nivedita Priyadarshini, K.; Sivashankari, V.; Shekhar, S. An Assessment of Land Cover Change Dynamics of Gaja Cyclone in Coastal Tamil Nadu, India Using Sentinel 1 SAR Dataset. In Proceedings of the International Archives of the Photogrammetry, Remote Sensing and Spatial Information Sciences—ISPRS Archives, Dhulikhel, Nepal, 10–11 December 2019; Volume 42. [Google Scholar]
  115. Meyers, R.A. Extreme Environmental Events; Springer: New York, NY, USA, 2011; ISBN 978-1-4419-7694-9. [Google Scholar]
  116. Danielsen, F.; Sørensen, M.K.; Olwig, M.F.; Selvam, V.; Parish, F.; Burgess, N.D.; Hiraishi, T.; Karunagaran, V.M.; Rasmussen, M.S.; Hansen, L.B.; et al. The Asian Tsunami: A Protective Role for Coastal Vegetation. Science 2005, 310, 643. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  117. FAO. FAO Fisheries and Aquaculture Department. Mangrove Forest Management Guidelines; FAO Forestry Paper, FAO Fisheries and Aquaculture Department: Rome, Italy, 2004. [Google Scholar]
  118. Kusmana, C. Distribution and Current Status of Mangrove Forests in Indonesia. In Mangrove Ecosystems of Asia: Status, Challenges and Management Strategies; Springer: New York, NY, USA, 2014; pp. 37–60. ISBN 9781461485827. [Google Scholar]
  119. Prasad, P.R.C.; Reddy, C.S.; Rajan, K.S.; Raza, S.H.; Dutt, C.B.S. Assessment of Tsunami and Anthropogenic Impacts on the Forest of the North Andaman Islands, India. Int. J. Remote Sens. 2009, 30, 1235–1249. [Google Scholar] [CrossRef]
  120. Barbier, E.B. Natural Barriers to Natural Disasters: Replanting Mangroves after the Tsunami. Front. Ecol. Environ. 2006, 4, 124–131. [Google Scholar] [CrossRef]
  121. Dharanirajan, K.; Kasinatha Pandian, P.; Gurugnanam, B.; Narayanan, R.M.; Ramachandran, S. An Integrated Study for the Assessment of Tsunami Impacts: A Case Study of South Andaman Island, India Using Remote Sensing and GIS. Coast. Eng. J. 2007, 49, 229–266. [Google Scholar] [CrossRef]
  122. Tappin, D.R.; Watts, P.; Grilli, S.T. The Papua New Guinea Tsunami of 17 July 1998: Anatomy of a Catastrophic Event. Nat. Hazards Earth Syst. Sci. 2008, 8, 243–266. [Google Scholar] [CrossRef] [Green Version]
  123. Primavera, J.H. Socio-Economic Impacts of Shrimp Culture. Aquac. Res. 1997, 28, 815–827. [Google Scholar] [CrossRef]
  124. Bosire, J.O.; Kaino, J.J.; Olagoke, A.O.; Mwihaki, L.M.; Ogendi, G.M.; Kairo, J.G.; Berger, U.; Macharia, D. Mangroves in Peril: Unprecedented Degradation Rates of Peri-Urban Mangroves in Kenya. Biogeosciences 2014, 11, 2623–2634. [Google Scholar] [CrossRef] [Green Version]
  125. Murdiyarso, D.; Purbopuspito, J.; Kauffman, J.B.; Warren, M.W.; Sasmito, S.D.; Donato, D.C.; Manuri, S.; Krisnawati, H.; Taberima, S.; Kurnianto, S. The Potential of Indonesian Mangrove Forests for Global Climate Change Mitigation. Nat. Clim. Chang. 2015, 5, 1089–1092. [Google Scholar] [CrossRef]
  126. Hamilton, S. Assessing the Role of Commercial Aquaculture in Displacing Mangrove Forest. BMS 2013, 89, 585–601. [Google Scholar] [CrossRef]
  127. Quimby, B. Emerging Customs: Small-Scale Fishing Practices in Aceh, Indonesia. Appl. Geogr. 2015, 59, 125–130. [Google Scholar] [CrossRef] [Green Version]
  128. Ahmed, N.; Thompson, S.; Glaser, M. Integrated Mangrove-Shrimp Cultivation: Potential for Blue Carbon Sequestration. Ambio 2018, 47, 441–452. [Google Scholar] [CrossRef]
  129. Lacerda, L.D. Conservation and Sustainable Utilization of Mangrove Forests in Latin America and Africa Regions. America 1992, 114190, 44. [Google Scholar]
  130. Kadarsah, A.; Salim, D.; Husain, S.; Dinata, M. Species Density and Lead (Pb) Pollution in Mangrove Ecosystem, South Kalimantan. J. Biodjati 2020, 5, 70–81. [Google Scholar] [CrossRef]
  131. Euler, M.; Schwarze, S.; Siregar, H.; Qaim, M. Oil Palm Expansion among Smallholder Farmers in Sumatra, Indonesia. J. Agric. Econ. 2016, 67, 658–676. [Google Scholar] [CrossRef]
  132. Son, N.T.; Chen, C.F.; Chen, C.R. Mapping Mangrove Density from Rapideye Data in Central America. Open Geosci. 2017, 9, 211–220. [Google Scholar] [CrossRef] [Green Version]
  133. Alongi, D.M.D.M. Present State and Future of the World’s Mangrove Forests. Environ. Conserv. 2002, 29, 331–349. [Google Scholar] [CrossRef] [Green Version]
  134. Small, C.; Gornitz, V.; Cohen, J.E. Coastal Hazards and the Global Distribution of Human Population. Environ. Geosci. 2000, 7, 3–12. [Google Scholar] [CrossRef]
  135. United Nations. World Urbanization Prospects—Population Division; United Nations: New York, NY, USA, 2019. [Google Scholar]
  136. Padmanaban, R.; Bhowmik, A.K.; Cabral, P.; Zamyatin, A.; Almegdadi, O.; Shuangao, W. Modelling Urban Sprawl Using Remotely Sensed Data: A Case Study of Chennai City, Tamilnadu. Entropy 2017, 19, 163. [Google Scholar] [CrossRef] [Green Version]
  137. Simard, M.; Grandi, G.D.E.; Saatchi, S.; Mayaux, P. Mapping Tropical Coastal Vegetation Using JERS-1 and ERS-1 Radar Data with a Decision Tree Classifier. Int. J. Remote Sens. 2002, 23, 1461–1474. [Google Scholar] [CrossRef]
  138. Whitehead, P.G.; Barbour, E.; Futter, M.N.; Sarkar, S.; Rodda, H.; Caesar, J.; Butterfield, D.; Jin, L.; Sinha, R.; Nicholls, R.; et al. Impacts of Climate Change and Socio-Economic Scenarios on Flow and Water Quality of the Ganges, Brahmaputra and Meghna (GBM) River Systems: Low Flow and Flood Statistics. Environ. Sci. Processes Impacts 2015, 17, 1057–1069. [Google Scholar] [CrossRef] [PubMed]
  139. Kathiresan, K.; Rajendran, N. Mangrove Ecosystems of the Indian Ocean Region. Indian J. Mar. Sci. 2005, 34, 104–113. [Google Scholar]
  140. Myers, S.S. Global Environmental Change: The Threat to Human Health; Worldwatch Paper; Worldwatch Institute: Washington, DC, USA, 2009. [Google Scholar]
  141. Farley, J.; Batker, D.; De La Torre, I.; Hudspeth, T. Conserving Mangrove Ecosystems in the Philippines: Transcending Disciplinary and Institutional Borders. Environ. Manag. 2010, 45, 39–51. [Google Scholar] [CrossRef] [PubMed]
  142. Zhang, Z.W.; Xu, X.R.; Sun, Y.X.; Yu, S.; Chen, Y.S.; Peng, J.X. Heavy Metal and Organic Contaminants in Mangrove Ecosystems of China: A Review. Environ. Sci. Pollut. Res. 2014, 21, 11938–11950. [Google Scholar] [CrossRef]
  143. Barbosa, F.M.A.; Cuambe, C.C.; Bandeira, S.O. Status and Distribution of Mangroves in Mozambique. S. Afr. J. Bot. 2001, 67, 393–398. [Google Scholar] [CrossRef] [Green Version]
  144. Hendy, I.W.; Michie, L.; Taylor, B.W. Habitat Creation and Biodiversity Maintenance in Mangrove Forests: Teredinid Bivalves as Ecosystemengineers. PeerJ 2014, 2014, e591. [Google Scholar] [CrossRef] [Green Version]
  145. Selvam, S.; Venkatramanan, S.; Singaraja, C. A GIS-Based Assessment of Water Quality Pollution Indices for Heavy Metal Contamination in Tuticorin Corporation, Tamilnadu, India. Arab. J. Geosci. 2015, 8, 10611–10623. [Google Scholar] [CrossRef]
  146. Chidambaram, S.; Karmegam, U.; Prasanna, M.V.; Sasidhar, P. A Study on Evaluation of Probable Sources of Heavy Metal Pollution in Groundwater of Kalpakkam Region, South India. Environmentalist 2012, 32, 371–382. [Google Scholar] [CrossRef]
  147. Ganesan, S. One hydrocarbon Project, Many Fault Lines. The Hindu. Chennai, 2017. Available online: https://www.thehindu.com/news/national/tamil-nadu/one-hydrocarbon-project-many-fault-lines/article61808511.ece (accessed on 6 February 2022).
  148. Duke, N.C. Oil Spill Impacts on Mangroves: Recommendations for Operational Planning and Action Based on a Global Review. Mar. Pollut. Bull. 2016, 109, 700–715. [Google Scholar] [CrossRef] [PubMed]
  149. Goldstein, B.D.; Osofsky, H.J.; Lichtveld, M.Y. The Gulf Oil Spill. N. Engl. J. Med. 2011, 364, 1334–1348. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  150. Han, Y.; Nambi, I.M.; Prabhakar Clement, T. Environmental Impacts of the Chennai Oil Spill Accident—A Case Study. Sci. Total Environ. 2018, 626, 795–806. [Google Scholar] [CrossRef] [PubMed]
  151. Sruthi, P.; Shackira, A.M.; Puthur, J.T. Heavy Metal Detoxification Mechanisms in Halophytes: An Overview. Wetl. Ecol. Manag. 2017, 25, 129–148. [Google Scholar] [CrossRef]
  152. Mandura, A.S. A Mangrove Stand under Sewage Pollution Stress: Red Sea. Mangroves Salt Marshes 1997, 1, 255–262. [Google Scholar] [CrossRef]
  153. Maiti, S.K.; Chowdhury, A. Effects of Anthropogenic Pollution on Mangrove Biodiversity: A Review. J. Environ. Prot. 2013, 4, 1428–1434. [Google Scholar] [CrossRef] [Green Version]
  154. Ellison, A.M.; Farnsworth, E.J. Anthropogenic Disturbance of Caribbean Mangrove Ecosystems: Past Impacts, Present Trends, and Future Predictions. Biotropica 1996, 28, 549. [Google Scholar] [CrossRef]
  155. Hemminga, M.A.; Slim, F.J.; Kazungu, J.; Ganssen, G.M.; Nieuwenhuize, J.; Kruyt, N.M. Carbon Outwelling from a Mangrove Forest with Adjacent Seagrass Beds and Coral Reefs (Gazi Bay, Kenya). Mar. Ecol. Prog. Ser. 1994, 106, 291–301. [Google Scholar] [CrossRef]
  156. Rudra, K. Rivers of the Ganga–Brahmaputra–Meghna Delta: An Overview; Springer: Cham, The Netherlands, 2018. [Google Scholar]
  157. Khare, D.; Patra, D.; Mondal, A.; Kundu, S. Impact of Landuse/Land Cover Change on Run-off in a Catchment of Narmada River in India. Appl. Geomat. 2015, 7, 23–35. [Google Scholar] [CrossRef]
  158. Day, J.W.; Conner, W.H.; Costanza, R.; Kemp, G.P.; Mendelssohn, I.A. Impacts of Sea Level Rise on Coastal Systems with Special Emphasis on the Mississippi River Deltaic Plain. In Climate and Sea Level Change: Observations, Projections and Implications; Cambridge University Press: Cambridge, UK, 1994; pp. 276–296. [Google Scholar]
  159. McKee, K.L.; Vervaeke, W.C. Will Fluctuations in Salt Marsh–Mangrove Dominance Alter Vulnerability of a Subtropical Wetland to Sea-Level Rise? Glob. Chang. Biol. 2018, 24, 1224–1238. [Google Scholar] [CrossRef]
  160. Ferreira, A.C.; Lacerda, L.D. Degradation and Conservation of Brazilian Mangroves, Status and Perspectives. Ocean Coast. Manag. 2016, 125, 38–46. [Google Scholar] [CrossRef]
  161. Adame, M.F.; Hermoso, V.; Perhans, K.; Lovelock, C.E.; Herrera-Silveira, J.A. Selecting Cost-Effective Areas for Restoration of Ecosystem Services. Conserv. Biol. 2015, 29, 493–502. [Google Scholar] [CrossRef] [PubMed] [Green Version]
  162. Fadzil, M.F.; Yun, P.S.; Razal, A.R.; Chee, P.S.; Suratman, S.; Dagang, N.S.; Tahir, N.M. Oil and Grease and Total Petroleum Hydrocarbons in the Waters of Ramsar Gazetted Mangrove Area, Johor. J. Sustain. Sci. Manag. 2017, 12, 30–39. [Google Scholar]
  163. Committee, A.T.; Rise, S.; Effects, I. Effects of Sea-Level Rise on Bays and Estuaries. J. Hydraul. Eng. 1992, 118. [Google Scholar] [CrossRef]
  164. Lee, S.Y.; Dunn, R.J.K.; Young, R.A.; Connolly, R.M.; Dale, P.E.R.; Dehayr, R.; Lemckert, C.J.; McKinnon, S.; Powell, B.; Teasdale, P.R.; et al. Impact of Urbanization on Coastal Wetland Structure and Function. Austral Ecol. 2006, 31, 149–163. [Google Scholar] [CrossRef]
  165. Rosasco, P.; Sdino, L.; Magoni, S. Reclamation Costs and Their Weight in the Economic Sustainability of a Project. Procedia Soc. Behav. Sci. 2016, 223, 209–216. [Google Scholar] [CrossRef] [Green Version]
  166. Asbridge, E.F.; Bartolo, R.; Finlayson, C.M.; Lucas, R.M.; Rogers, K.; Woodroffe, C.D. Assessing the Distribution and Drivers of Mangrove Dieback in Kakadu National Park, Northern Australia. Estuar. Coast. Shelf Sci. 2019, 228, 106353. [Google Scholar] [CrossRef]
  167. Lovelock, C.E.; Feller, I.C.; Reef, R.; Hickey, S.; Ball, M.C. Mangrove Dieback during Fluctuating Sea Levels. Sci. Rep. 2017, 7, 1680. [Google Scholar] [CrossRef]
  168. Osorio, J.A.; Crous, C.J.; Wingfield, M.J.; de Beer, Z.W.; Roux, J. An Assessment of Mangrove Diseases and Pests in South Africa. Forestry 2017, 90, 343–358. [Google Scholar] [CrossRef] [Green Version]
  169. Blasco, F.; Saenger, P.; Janodet, E. Mangroves as Indicator of Coastal Change. Catena 1996, 27, 167–178. [Google Scholar] [CrossRef] [Green Version]
  170. Ellison, J.C.; Stoddart, D.R. Mangrove Ecosystem Collapse during Predicted Sea-Level Rise: Holocene Analogues and Implications. J. Coast. Res. 1991, 7, 151–165. [Google Scholar]
  171. Bourne, J. Louisiana’s Vanishing Wetlands: Going, Going. Science 2000, 289, 1860–1863. [Google Scholar] [CrossRef] [PubMed]
  172. Syvitski, J.P.M.; Kettner, A.J.; Overeem, I.; Hutton, E.W.H.; Hannon, M.T.; Brakenridge, G.R.; Day, J.; Vörösmarty, C.; Saito, Y.; Giosan, L.; et al. Sinking Deltas Due to Human Activities. Nat. Geosci. 2009, 2, 681–686. [Google Scholar] [CrossRef]
  173. Gornitz, V. Sea-level Rise: A Review of Recent Past and Near-future Trends. Earth Surf. Processes Landf. 1995, 20, 7–20. [Google Scholar] [CrossRef]
  174. Shi-lun, Y.; Ji-yu, C. Coatal Salt Marshes and Mangrove Swamps in China. Chin. J. Oceanol. Limnol. 1995, 13, 318–324. [Google Scholar] [CrossRef]
  175. Bidorn, B.; Sok, K.; Bidorn, K.; Burnett, W.C. An Analysis of the Factors Responsible for the Shoreline Retreat of the Chao Phraya Delta (Thailand). Sci. Total Environ. 2021, 769, 145253. [Google Scholar] [CrossRef]
  176. Hale, R.P.; Wilson, C.A.; Bomer, E.J. Seasonal Variability of Forces Controlling Sedimentation in the Sundarbans National Forest, Bangladesh. Front. Earth Sci. 2019, 7, 211. [Google Scholar] [CrossRef] [Green Version]
  177. Kanaya, G.; Suzuki, T.; Kikuchi, E. Impacts of the 2011 Tsunami on Sediment Characteristics and Macrozoobenthic Assemblages in a Shallow Eutrophic Lagoon, Sendai Bay, Japan. PLoS ONE 2015, 10, e0135125. [Google Scholar] [CrossRef]
  178. Sandilyan, S.; Kathiresan, K. Mangrove Conservation: A Global Perspective. Biodivers. Conserv. 2012, 21, 3523–3542. [Google Scholar] [CrossRef]
  179. Hoque, M.A.-A.; Phinn, S.; Roelfsema, C.; Childs, I. Assessing Tropical Cyclone Impacts Using Object-Based Moderate Spatial Resolution Image Analysis: A Case Study in Bangladesh. Int. J. Remote Sens. 2016, 37, 5320–5343. [Google Scholar] [CrossRef]
  180. Macamo, C.; Massuanganhe, E.; Nicolau, D.; Bandeira, S.; Adams, J. Mangrove’s Response to Cyclone Eline (2000): What’s Happening 14 Years Late. Aquat. Bot. 2016, 134, 10–17. [Google Scholar] [CrossRef]
  181. FAO (Food and Agriculture Organization) The State of the World’s Land and Water Resources for Food and Agriculture (SOLAW)–Managing Systems at Risk; 2011. FAO, Earthscan Publications. Available online: https://www.fao.org/3/a-i1688e.pdf (accessed on 1 August 2017).
  182. Smith, S.V.; Buddemeier, R.W. Global Change and Coral Reef Ecosystems. Annu. Rev. Ecol. Syst. 1992, 23, 89–118. [Google Scholar] [CrossRef]
  183. Ellison, J.C. How South Pacific Mangroves May Respond to Predicted Climate Change and Sea-Level Rise. In Climate Change in the South Pacific: Impacts and Responses in Australia, New Zealand, and Small Island States; Springer: Berlin/Heidelberg, Germany, 2000. [Google Scholar]
  184. Ilman, M.; Dargusch, P.; Dart, P. Onrizal A Historical Analysis of the Drivers of Loss and Degradation of Indonesia’s Mangroves. Land Use Policy 2016, 54, 448–459. [Google Scholar] [CrossRef]
  185. Thu, P.M.; Populus, J. Status and Changes of Mangrove Forest in Mekong Delta: Case Study in Tra Vinh, Vietnam. Estuar. Coast. Shelf Sci. 2007, 71, 98–109. [Google Scholar] [CrossRef]
  186. Lymburner, L.; Bunting, P.; Lucas, R.; Scarth, P.; Alam, I.; Phillips, C.; Ticehurst, C.; Held, A. Mapping the Multi-Decadal Mangrove Dynamics of the Australian Coastline. Remote Sens. Environ. 2020, 238, 111185. [Google Scholar] [CrossRef]
  187. Woodroffe, C.D.; Thom, B.G.; Chappell, J. Development of Widespread Mangrove Swamps in Mid-Holocene Times in Northern Australia. Nature 1985, 317, 711–713. [Google Scholar] [CrossRef]
  188. Acuña-Piedra, J.F.; Quesada-Román, A. Multidecadal Biogeomorphic Dynamics of a Deltaic Mangrove Forest in Costa Rica. Ocean Coast. Manag. 2021, 211, 105770. [Google Scholar] [CrossRef]
  189. Gilman, E.L.; Ellison, J.; Duke, N.C.; Field, C. Threats to Mangroves from Climate Change and Adaptation Options. Aquat. Bot. 2008, 89, 237–250. [Google Scholar] [CrossRef]
  190. Hamilton, L.S.; Snedaker, S.C. Handbook for Mangrove Area Management; United Nations Environment Programme and International Union for Conservation of Nature, 1984. Available online: https://wedocs.unep.org/handle/20.500.11822/29409 (accessed on 1 August 2017).
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Figure 1. (A) Status of the global mangrove species and (B) geographic coverage of the threatened mangrove species (LC: Least Concern; VU: Vulnerable; CR: Critically Endangered; NT: Not Threatened; EN: Endangered; DD: Data Deficient).
Figure 1. (A) Status of the global mangrove species and (B) geographic coverage of the threatened mangrove species (LC: Least Concern; VU: Vulnerable; CR: Critically Endangered; NT: Not Threatened; EN: Endangered; DD: Data Deficient).
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Figure 2. (a) Current global mangrove distribution (green stripe) and associated consolidated studies at the country level and (b) identified drivers and driver groups of mangrove deforestation.
Figure 2. (a) Current global mangrove distribution (green stripe) and associated consolidated studies at the country level and (b) identified drivers and driver groups of mangrove deforestation.
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Figure 3. Interactions among the identified drivers and driver groups of mangrove deforestation. The scale indicates the number of consolidated studies indicating such interactions.
Figure 3. Interactions among the identified drivers and driver groups of mangrove deforestation. The scale indicates the number of consolidated studies indicating such interactions.
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Table
Table 1. List of the combination of keywords and keyword sets, and the number of the literature obtained.
Table 1. List of the combination of keywords and keyword sets, and the number of the literature obtained.
Initial KeywordsDriver Related Keyword SetsNumber of Literature
WOSScopusTotal
{mangrove distribution, mangrove biomass, mangrove species, mangrove ecosystems}Climate 151429
Extreme events202545
Land changes29 25 54
Pollution 121527
Flow modification163046
Total92109201
Table
Table 2. Mangrove forests coverage across five global regions and the decline in the coverage between 1990 and 2020.
Table 2. Mangrove forests coverage across five global regions and the decline in the coverage between 1990 and 2020.
Global RegionsMangrove Coverage
km2		Rate of Decline
%/year
19902000201020201990–20002000–20102010–2020
Western and Central Africa24,36024,20023,89023,8400.070.130.02
Eastern and Southern Africa92909050902088300.260.030.21
Total Africa33,65033,25032,91032,6700.120.100.07
East Asia3202502402202.190.400.83
South and Southeast Asia57,17057,08055,13053,3000.020.340.33
Western and Central Asia19001900190018400.000.000.32
Total Asia59,39059,23057,27055,3600.030.330.33
Caribbean79107890787077400.030.030.17
Central America49204830482046600.180.020.33
North America11,95011,90011,67011,5200.040.190.13
Total Caribbean, Central, and North America24,78024,62024,36023,9200.060.110.18
Total Oceania12,47012,14011,55011,5000.260.490.04
Total South America21,52021,24020,50019,7600.130.350.36
World151,810150,480146,590143,2100.090.260.23
Table
Table 3. Environmental and anthropogenic drivers of mangrove deforestation and their geographic coverage of effects. The values refer to the number of corresponding literature reviewed. N/A—Not available. Note that the numbers of literature are absolute and are not weighted by the mangrove coverages of the corresponding countries.
Table 3. Environmental and anthropogenic drivers of mangrove deforestation and their geographic coverage of effects. The values refer to the number of corresponding literature reviewed. N/A—Not available. Note that the numbers of literature are absolute and are not weighted by the mangrove coverages of the corresponding countries.
CountriesEnvironmental DriversAnthropogenic Drivers
Climate Change (Sea-Level Rise, Temperature, and Precipitation Changes)Extreme EventsAquaculture and AgricultureSettlements and UrbanizationIndustrialization and PollutionFlow Modification
Mexico5N/A351N/A
CubaN/AN/A121N/A
Brazil3N/A3633
Guinea Bissau11N/A2N/AN/A
GuyanaN/AN/A221N/A
Saudi Arabia1114N/AN/A
Ethiopia2143N/AN/A
Mozambique 1N/A221N/A
Madagascar 42N/A2N/AN/A
India 9461174
Bangladesh 646823
Myanmar12N/AN/AN/AN/A
Malaysia3N/A32N/AN/A
Philippines626111
Indonesia728211
Australia34162N/A
Papua New Guinea1111N/AN/A
New Zealand 2211N/AN/A
Thailand426N/A1N/A
Colombia3211N/AN/A
Nigeria2212N/A1
Vietnam1231N/AN/A
China2N/A1921
South Africa1N/AN/A421
Ecuador N/AN/A2N/A1N/A
Pakistan122413
Venezuela2N/AN/A111
United States 24N/A3N/AN/A
Mauritius 11N/A121
Sri Lanka2216N/AN/A
Kenya11N/A21N/A
Japan23N/A4N/AN/A
Total794765983120
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Bhowmik, A.K.; Padmanaban, R.; Cabral, P.; Romeiras, M.M. Global Mangrove Deforestation and Its Interacting Social-Ecological Drivers: A Systematic Review and Synthesis. Sustainability 2022, 14, 4433. https://doi.org/10.3390/su14084433

AMA Style

Bhowmik AK, Padmanaban R, Cabral P, Romeiras MM. Global Mangrove Deforestation and Its Interacting Social-Ecological Drivers: A Systematic Review and Synthesis. Sustainability. 2022; 14(8):4433. https://doi.org/10.3390/su14084433

Chicago/Turabian Style

Bhowmik, Avit K., Rajchandar Padmanaban, Pedro Cabral, and Maria M. Romeiras. 2022. "Global Mangrove Deforestation and Its Interacting Social-Ecological Drivers: A Systematic Review and Synthesis" Sustainability 14, no. 8: 4433. https://doi.org/10.3390/su14084433

APA Style

Bhowmik, A. K., Padmanaban, R., Cabral, P., & Romeiras, M. M. (2022). Global Mangrove Deforestation and Its Interacting Social-Ecological Drivers: A Systematic Review and Synthesis. Sustainability, 14(8), 4433. https://doi.org/10.3390/su14084433

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