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Search Results (541)

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Keywords = mangrove forest

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28 pages, 32933 KiB  
Article
The Change Detection of Mangrove Forests Using Deep Learning with Medium-Resolution Satellite Imagery: A Case Study of Wunbaik Mangrove Forest in Myanmar
by Kyaw Soe Win and Jun Sasaki
Remote Sens. 2024, 16(21), 4077; https://doi.org/10.3390/rs16214077 - 31 Oct 2024
Viewed by 782
Abstract
This paper presents the development of a U-Net model using four basic optical bands and SRTM data to analyze changes in mangrove forests from 1990 to 2024, with an emphasis on the impact of restoration programs. The model, which employed supervised learning for [...] Read more.
This paper presents the development of a U-Net model using four basic optical bands and SRTM data to analyze changes in mangrove forests from 1990 to 2024, with an emphasis on the impact of restoration programs. The model, which employed supervised learning for binary classification by fusing multi-temporal Landsat 8 and Sentinel-2 imagery, achieved a superior accuracy of 99.73% for the 2020 image classification. It was applied to predict the long-term mangrove maps in Wunbaik Mangrove Forest (WMF) and to detect the changes at five-year intervals. The change detection results revealed significant changes in the mangrove forests, with 29.3% deforestation, 5.75% reforestation, and −224.52 ha/yr of annual rate of changes over 34 years. The large areas of mangrove forests have increased since 2010, primarily due to naturally recovered and artificially planted mangroves. Approximately 30% of the increased mangroves from 2015 to 2024 were attributed to mangrove plantations implemented by the government. This study contributes to developing a deep learning model with multi-temporal and multi-source imagery for long-term mangrove monitoring by providing accurate performance and valuable information for effective conservation strategies and restoration programs. Full article
(This article belongs to the Special Issue Remote Sensing in Mangroves III)
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Figure 1
<p>The location of the study area: (<b>a</b>) Wunbaik Mangrove Forest (Landsat 8 composite image of 4 bands); (<b>b</b>) Myanmar’s States and Regions (Myanmar Information Management Unit—MIMU); and (<b>c</b>,<b>d</b>) Example patches used in U-Net model training (Landsat 8 composite image).</p>
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<p>Ground truth image used for model training.</p>
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<p>The architecture of the CNN model.</p>
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<p>The architecture of the U-Net model (visualized using visualkeras).</p>
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<p>Evaluation results of example patches shown in <a href="#remotesensing-16-04077-f001" class="html-fig">Figure 1</a>c,d, comparing Landsat 8 and Sentinel-2 images with ground truth: (<b>a</b>) ground truth images; (<b>b</b>) TP, TN, FP, and FN of Landsat 8 images; and (<b>c</b>) TP, TN, FP, and FN of Sentinel-2 images.</p>
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<p>Mangrove maps predicted by the multi-temporal and multi-source model and Google Earth images from 1990 to 2024: (<b>a</b>) the mangrove map of 1990; (<b>b</b>) the Google Earth image of 1990; (<b>c</b>) the mangrove map of 1995; (<b>d</b>) the Google Earth image of 1995; (<b>e</b>) the mangrove map of 2000; (<b>f</b>) the Google Earth image of 2000; (<b>g</b>) the mangrove map of 2005; (<b>h</b>) the Google Earth image of 2005; (<b>i</b>) the mangrove map of 2010; (<b>j</b>) the Google Earth image of 2010; (<b>k</b>) the mangrove map of 2015; (<b>l</b>) the Google Earth image of 2015; (<b>m</b>) the mangrove map of 2020; (<b>n</b>) the Google Earth image of 2020; (<b>o</b>) the mangrove map of 2024; and (<b>p</b>) the Google Earth image of 2024. (The dark green is mangroves, light and dark brown are agricultural and aquacultural areas, and light green is water bodies).</p>
Full article ">Figure 6 Cont.
<p>Mangrove maps predicted by the multi-temporal and multi-source model and Google Earth images from 1990 to 2024: (<b>a</b>) the mangrove map of 1990; (<b>b</b>) the Google Earth image of 1990; (<b>c</b>) the mangrove map of 1995; (<b>d</b>) the Google Earth image of 1995; (<b>e</b>) the mangrove map of 2000; (<b>f</b>) the Google Earth image of 2000; (<b>g</b>) the mangrove map of 2005; (<b>h</b>) the Google Earth image of 2005; (<b>i</b>) the mangrove map of 2010; (<b>j</b>) the Google Earth image of 2010; (<b>k</b>) the mangrove map of 2015; (<b>l</b>) the Google Earth image of 2015; (<b>m</b>) the mangrove map of 2020; (<b>n</b>) the Google Earth image of 2020; (<b>o</b>) the mangrove map of 2024; and (<b>p</b>) the Google Earth image of 2024. (The dark green is mangroves, light and dark brown are agricultural and aquacultural areas, and light green is water bodies).</p>
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<p>The annual changes of mangrove forests in WMF from 1990 to 2024.</p>
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<p>Change detection maps for each period: (<b>a</b>) 1990–1995; (<b>b</b>) 1995–2000; (<b>c</b>) 2000–2005; (<b>d</b>) 2005–2010; (<b>e</b>) 2010–2015; (<b>f</b>) 2015–2020; (<b>g</b>) 2020–2024; and (<b>h</b>) 1990–2024.</p>
Full article ">Figure 8 Cont.
<p>Change detection maps for each period: (<b>a</b>) 1990–1995; (<b>b</b>) 1995–2000; (<b>c</b>) 2000–2005; (<b>d</b>) 2005–2010; (<b>e</b>) 2010–2015; (<b>f</b>) 2015–2020; (<b>g</b>) 2020–2024; and (<b>h</b>) 1990–2024.</p>
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<p>Annual rate of mangrove changes in WMF.</p>
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<p>The training flow of the CNN model with different input features: (<b>a</b>) accuracy flow trained with NDVI, NDWI, SAVI, CMRI, SRTM, and CHM; (<b>b</b>) accuracy flow trained with 4 bands and SRTM.</p>
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<p>Mangrove maps predicted by CNN model trained with three bands and SRTM for 1995: (<b>a</b>) mangrove map predicted using 3 bands and SRTM; (<b>b</b>) mangrove map predicted using 4 bands and SRTM; and (<b>c</b>) Google Earth image for 1995. (The dark green is mangroves, light brown is agricultural and aquacultural areas, and light green is water bodies).</p>
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<p>Different temporal conditions of paddy fields: (<b>a</b>) Landsat composite image of January 2020; (<b>b</b>) Landsat composite image of December 2019; (<b>c</b>) Landsat composite image of November 2019; (<b>d</b>) CNN result for January 2020; (<b>e</b>) CNN result for December 2019; and (<b>f</b>) CNN result for November 2019. (The dark brown is mangroves, light green and white are agricultural and aquacultural areas, and yellow-green is water bodies).</p>
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<p>Area differences between Landsat 8 (30 m), Landsat 8 (10 m), and Sentinel-2 (10 m).</p>
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<p>Model results on satellite images with different spatial resolutions: (<b>a</b>) U-Net result on Landsat 8 (30 m); (<b>b</b>) U-Net result on Landsat 8 (10 m); and (<b>c</b>) U-Net result on Sentinel-2 (10 m).</p>
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<p>Annual area changes of WMF given by GMW data.</p>
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<p>Annual area changes of WMF given by Sentinel-2 data.</p>
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<p>Annual area changes of WMF given by HLS data: (<b>a</b>) HLS L30 data, (<b>b</b>) HLS S30 data.</p>
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<p>Mangrove losses: (<b>a</b>) changes from 2010 to 2024; (<b>b</b>) land use in 2009; (<b>c</b>) land use in 2024; (<b>d</b>) land use in 2009; and (<b>e</b>) land use in 2024. The drivers of losses from (<b>b</b>) to (<b>c</b>) are shrimp ponds and from (<b>d</b>) to (<b>e</b>) are paddy fields due to Google Earth images and the study by Maung et al. (2024) [<a href="#B48-remotesensing-16-04077" class="html-bibr">48</a>].</p>
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<p>Mangrove gains: (<b>a</b>) changes from 2010 to 2024; (<b>b</b>) land use in 2009; (<b>c</b>) land use in 2023; (<b>d</b>) land use in 2009; and (<b>e</b>) land use in 2023. The drivers of gains from (<b>b</b>) to (<b>c</b>) are mangrove plantations and from (<b>d</b>) to (<b>e</b>) are natural mangroves due to Google Earth images and Maung and Sasaki (2021) [<a href="#B23-remotesensing-16-04077" class="html-bibr">23</a>].</p>
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<p>Mangrove losses after recovery: (<b>a</b>) changes from 2010 to 2024; (<b>b</b>) land use in 2015; (<b>c</b>) land use in 2018; (<b>d</b>) land use in 2024; (<b>e</b>) changes from 2010 to 2015; (<b>f</b>) changes from 2015 to 2020; and (<b>g</b>) changes from 2020 to 2024 (Google Earth images for historical land uses).</p>
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<p>Mangrove losses after 2020: (<b>a</b>) changes from 2020 to 2024; (<b>b</b>) Google Earth image of 2023; (<b>c</b>) Sentinel-2 composite image of 2020; (<b>d</b>) Sentinel-2 composite image of 2024; (<b>e</b>) Google Earth image of 2023; (<b>f</b>) Sentinel-2 composite image of 2020; and (<b>g</b>) Sentinel-2 composite image of 2024. (The red line represents the areas of change with dark green for mangroves, light and dark brown indicating newly cut areas for aquaculture).</p>
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21 pages, 7085 KiB  
Article
Space-Based Mapping of Pre- and Post-Hurricane Mangrove Canopy Heights Using Machine Learning with Multi-Sensor Observations
by Boya Zhang, Daniel Gann, Shimon Wdowinski, Chaohao Lin, Erin Hestir, Lukas Lamb-Wotton, Khandker S. Ishtiaq, Kaleb Smith and Yuepeng Li
Remote Sens. 2024, 16(21), 3992; https://doi.org/10.3390/rs16213992 - 28 Oct 2024
Viewed by 733
Abstract
Coastal mangrove forests provide numerous ecosystem services, which can be disrupted by natural disturbances, mainly hurricanes. Canopy height (CH) is a key parameter for estimating carbon storage. Airborne Light Detection and Ranging (LiDAR) is widely viewed as the most accurate method for estimating [...] Read more.
Coastal mangrove forests provide numerous ecosystem services, which can be disrupted by natural disturbances, mainly hurricanes. Canopy height (CH) is a key parameter for estimating carbon storage. Airborne Light Detection and Ranging (LiDAR) is widely viewed as the most accurate method for estimating CH but data are often limited in spatial coverage and are not readily available for rapid impact assessment after hurricane events. Hence, we evaluated the use of systematically acquired space-based Synthetic Aperture Radar (SAR) and optical observations with airborne LiDAR to predict CH across expansive mangrove areas in South Florida that were severely impacted by Category 3 Hurricane Irma in 2017. We used pre- and post-Irma LiDAR-derived canopy height models (CHMs) to train Random Forest regression models that used features of Sentinel-1 SAR time series, Landsat-8 optical, and classified mangrove maps. We evaluated (1) spatial transfer learning to predict regional CH for both time periods and (2) temporal transfer learning coupled with species-specific error correction models to predict post-Irma CH using models trained by pre-Irma data. Model performance of SAR and optical data differed with time period and across height classes. For spatial transfer, SAR data models achieved higher accuracy than optical models for post-Irma, while the opposite was the case for the pre-Irma period. For temporal transfer, SAR models were more accurate for tall trees (>10 m) but optical models were more accurate for short trees. By fusing data of both sensors, spatial and temporal transfer learning achieved the root mean square errors (RMSEs) of 1.9 m and 1.7 m, respectively, for absolute CH. Predicted CH losses were comparable with LiDAR-derived reference values across height and species classes. Spatial and temporal transfer learning techniques applied to readily available spaceborne satellite data can enable conservation managers to assess the impacts of disturbances on regional coastal ecosystems efficiently and within a practical timeframe after a disturbance event. Full article
(This article belongs to the Section Forest Remote Sensing)
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Figure 1
<p>(<b>a</b>) Florida state boundary and Hurricane Irma track. (<b>b</b>) Level 3 mangrove classification map. (<b>c</b>) Level 4 mangrove species classification. (<b>d</b>) The 30 m G-LiHT footprint of pre-Irma CHM. (<b>e</b>–<b>p</b>) Zoom-in views for four representative sites.</p>
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<p>Timeline of pre-Irma (orange lines) and post-Irma (purple lines) observations separated by September 2017 Hurricane Irma (the dark vertical line).</p>
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<p>(<b>a</b>) Flow chart of data filtering. (<b>b</b>) Spatial and temporal transfer learning based on <span class="html-italic">DS2_pre</span> and <span class="html-italic">DS2_post</span> data that are separately used in the spatial transfer but collectively used in the temporal transfer learning. Blue and green rectangles are input variables; white and red rectangles are intermediate products; ovals indicate model processes; pink and orange rectangles are output products.</p>
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<p>(<b>a</b>) Boxplots for the reference pre- and post-Irma CHM from <span class="html-italic">DS2</span> dataset. Red line indicates the median value; the boxes represent the interquartile range between the first quartile (25th percentile) and the third quartile (75th percentile); the whiskers extend from the edges of the box to the smallest and largest values within 1.5 times the interquartile range. (<b>b</b>) Comparison of backscatter time series and optical observations using a representative pixel from each species. For each subplot, darker color represents pre-Irma values and lighter color post-Irma values. CH values are displayed in the last row.</p>
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<p>(<b>a</b>) Scatter plot of predicted and referenced CH for pre- and post-Irma from one of the cross-validation evaluation datasets. The yellow lines mark the least-square linear regression model. “BW” in the legend indicates “buttonwood” species. (<b>b</b>) Mean and standard deviation of variable importance of top ten variables using the mixed feature.</p>
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<p>Scatter plots of prediction error and percentage (Perc) error versus reference CH for both time periods by species. Red lines are the least-squared linear models.</p>
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<p>Predicted CH (<b>a</b>) pre-Irma, (<b>b</b>) post-Irma, and (<b>c</b>) CH loss (positive values indicate losses). (<b>d</b>) Comparison between mean and standard deviation of predicted and reference CH loss from evaluation datasets in cross-validation. Deep color represents predicted values and light color reference values. Missing data are due to no pixel samples. (<b>e</b>) Local maps of CH loss. White circles in (<b>e3</b>) indicate (<b>left</b>) the bank areas and (<b>right</b>) the boundary between white and red mangroves according to <a href="#remotesensing-16-03992-f001" class="html-fig">Figure 1</a>f.</p>
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<p>(<b>a</b>) Scatter plot of predicted and corrected CH versus reference post-Irma CH from a cross-validation dataset. (<b>b</b>) Mean and standard deviation of top ten ranking of variable importance using mixed features.</p>
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<p>(<b>a</b>–<b>l</b>) Local maps of post-Irma CH reference, corrected predictions, and errors. White circle outlines indicate areas with large errors. (<b>m</b>) Comparison of the corrected predictions and reference CH losses across pre-Irma canopy height and species classes. Deep color indicates predicted values and light color reference values.</p>
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<p>(<b>a</b>,<b>b</b>) Pre-Irma CH maps for (<b>a</b>) remake of <a href="#remotesensing-16-03992-f007" class="html-fig">Figure 7</a>a and (<b>b</b>) Figure from Jamaluddin et al. (2024) [<a href="#B32-remotesensing-16-03992" class="html-bibr">32</a>]. (<b>c</b>) Remake of CH loss predictions from <a href="#remotesensing-16-03992-f007" class="html-fig">Figure 7</a>c. (<b>d</b>) CH loss predictions from Lagomasino et al. (2021) [<a href="#B10-remotesensing-16-03992" class="html-bibr">10</a>].</p>
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27 pages, 4549 KiB  
Article
Benthic Community Metrics Track Hydrologically Stressed Mangrove Systems
by Amanda W. J. Demopoulos, Jill R. Bourque, Jennifer P. McClain-Counts, Nicole Cormier and Ken W. Krauss
Diversity 2024, 16(11), 659; https://doi.org/10.3390/d16110659 - 25 Oct 2024
Viewed by 648
Abstract
Mangrove restoration efforts have increased in order to help combat their decline globally. While restoration efforts often focus on planting seedlings, underlying chronic issues, including disrupted hydrological regimes, can hinder restoration success. While improving hydrology may be more cost-effective and have higher success [...] Read more.
Mangrove restoration efforts have increased in order to help combat their decline globally. While restoration efforts often focus on planting seedlings, underlying chronic issues, including disrupted hydrological regimes, can hinder restoration success. While improving hydrology may be more cost-effective and have higher success rates than planting seedlings alone, hydrological restoration success in this form is poorly understood. Restoration assessments can employ a functional equivalency approach, comparing restoration areas over time with natural, reference forests in order to quantify the relative effectiveness of different restoration approaches. Here, we employ the use of baseline community ecology metrics along with stable isotopes to track changes in the community and trophic structure and enable time estimates for establishing mangrove functional equivalency. We examined a mangrove system impacted by road construction and recently targeted for hydrological restoration within the Rookery Bay National Estuarine Research Reserve, Florida, USA. Samples were collected along a gradient of degradation, from a heavily degraded zone, with mostly dead trees, to a transition zone, with a high number of saplings, to a full canopy zone, with mature trees, and into a reference zone with dense, mature mangrove trees. The transition, full canopy, and reference zones were dominated by annelids, gastropods, isopods, and fiddler crabs. Diversity was lower in the dead zone; these taxa were enriched in 13C relative to those found in all the other zones, indicating a shift in the dominant carbon source from mangrove detritus (reference zone) to algae (dead zone). Community-wide isotope niche metrics also distinguished zones, likely reflecting dominant primary food resources (baseline organic matter) present. Our results suggest that stable isotope niche metrics provide a useful tool for tracking mangrove degradation gradients. These baseline data provide critical information on the ecosystem functioning in mangrove habitats following hydrological restoration. Full article
(This article belongs to the Special Issue Mangrove Regeneration and Restoration)
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<p>Conceptual diagram of the hypothesized isotopic niche patterns based on the maturation of detrital pathways and increased diversity of available carbon resources.</p>
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<p>Location of the study area in southwest Florida sampled during winter (January) and summer (August) 2015. (<b>A</b>) Two sites (T1 and T2) were established in an area targeted for hydrological restoration on Marco Island, Florida. The points represent three different zones: dead (red), transitional (green), and full canopy (blue), sampled along each transect in the restoration area. (<b>B</b>) Additional transects were established within a natural mangrove habitat (T5) on Horrs Island. The purple points represent the locations of three reference transects in mature mangroves. (<b>C</b>) Representative habitats in each zone sampled during this study.</p>
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<p>(<b>A</b>) Epifauna and biogenic structure density (individuals m<sup>−2</sup>) ± 1 standard error and (<b>B</b>) taxonomic composition in surface quadrats during winter (January) and summer (August) 2015 from reference, full canopy, transitional, and dead zones. Colors in composition figure (<b>B</b>) represent major taxonomic groups: Mollusca (purple), insects (green), crabs (orange), fish (light blue), and burrows (beige).</p>
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<p>A non-metric multidimensional scaling plot for (<b>A</b>) epifauna and (<b>B</b>) infauna in the surface sediments collected during winter (January, solid symbols) and summer (August, open symbols) of 2015 based on Bray–Curtis similarities of square root-transformed density data. The colors refer to the zones: purple = reference; blue = full canopy; green = transitional; red = dead. The ellipses represent significant clusters with average similarity among the cluster samples indicated.</p>
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<p>(<b>A</b>) Infauna density (individuals m<sup>−2</sup>) ± 1 standard error and (<b>B</b>) taxonomic composition in the upper 2 cm of sediment during winter (January) and summer (August) 2015 from reference, full canopy, transitional, and dead zones. Colors in composition figure (<b>B</b>) represent major taxonomic groups: Polychaeta (dark blue), Oligochaeta (red), Mollusca (purple), insects (green), and other taxa (orange).</p>
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<p>Distance-based redundancy analysis (dbRDA) of the “best” model from the distance-based linear modeling of the sampling locations within the zones based on Bray–Curtis similarities of square root-transformed (<b>A</b>) epifauna and (<b>B</b>) infauna density data.</p>
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<p>Fauna stable isotope data (δ<sup>13</sup>C and δ<sup>15</sup>N, ‰, solid symbols represent centroids) and their corresponding standard ellipse area (SEA<sub>c</sub>) for each habitat zone in (<b>A</b>) winter and (<b>B</b>) summer. Colors refer to zones: purple = reference; blue = full canopy; green = transitional; red = dead.</p>
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25 pages, 26385 KiB  
Article
An Innovative Tool for Monitoring Mangrove Forest Dynamics in Cuba Using Remote Sensing and WebGIS Technologies: SIGMEM
by Alexey Valero-Jorge, Raúl González-Lozano, Roberto González-De Zayas, Felipe Matos-Pupo, Rogert Sorí and Milica Stojanovic
Remote Sens. 2024, 16(20), 3802; https://doi.org/10.3390/rs16203802 - 12 Oct 2024
Viewed by 722
Abstract
The main objective of this work was to develop a viewer with web output, through which the changes experienced by the mangroves of the Gran Humedal del Norte de Ciego de Avila (GHNCA) can be evaluated from remote sensors, contributing to the understanding [...] Read more.
The main objective of this work was to develop a viewer with web output, through which the changes experienced by the mangroves of the Gran Humedal del Norte de Ciego de Avila (GHNCA) can be evaluated from remote sensors, contributing to the understanding of the spatiotemporal variability of their vegetative dynamics. The achievement of this objective is supported by the use of open-source technologies such as MapStore, GeoServer and Django, as well as Google Earth Engine, which combine to offer a robust and technologically independent solution to the problem. In this context, it was decided to adopt an action model aimed at automating the workflow steps related to data preprocessing, downloading, and publishing. A visualizer with web output (Geospatial System for Monitoring Mangrove Ecosystems or SIGMEM) is developed for the first time, evaluating changes in an area of central Cuba from different vegetation indices. The evaluation of the machine learning classifiers Random Forest and Naive Bayes for the automated mapping of mangroves highlighted the ability of Random Forest to discriminate between areas occupied by mangroves and other coverages with an Overall Accuracy (OA) of 94.11%, surpassing the 89.85% of Naive Bayes. The estimated net change based on the year 2020 of the areas determined during the classification process showed a decrease of 5138.17 ha in the year 2023 and 2831.76 ha in the year 2022. This tool will be fundamental for researchers, decision makers, and students, contributing to new research proposals and sustainable management of mangroves in Cuba and the Caribbean. Full article
(This article belongs to the Special Issue Remote Sensing: 15th Anniversary)
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<p>Location of the Gran Humedal del Norte de Ciego de Ávila (GHNCA), Cuba.</p>
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<p>General workflow for the development of the WebGis platform: SIGMEM.</p>
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<p>Spatial distribution of the reference points taken in the GHNCA. Green dots indicate mangrove class and red dots non-mangrove.</p>
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<p>Distribution of predictor variables used in the classification model grouped by classes (mangrove/non-mangrove). Selected Sentinel-2 spectral bands and spectral indices selected by the recursive variable elimination method.</p>
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<p>Diagram of the web architecture used for the development of the GeoServer.</p>
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<p>Estimated mangrove areas in the GHN in Ciego de Avila, Cuba emulating Sentinel-2 images. (<b>A</b>) 2020, (<b>B</b>) 2021, (<b>C</b>) 2022, and (<b>D</b>) 2023. Legend: the areas occupied by mangrove ecosystems in each of the years are shown in red; the limits of the GHN of Ciego de Avila are shown in blue dashed lines.</p>
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<p>Two-dimensional view of the workspace within the MapStore application. The red line represents the limit of the GHNCA.</p>
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<p>Three-dimensional view of the workspace within the MapStore application. The red line represents the limit of the GHNCA.</p>
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<p>Access to the metadata catalog of geospatial resources. The red line represents the limit of the GHNCA.</p>
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<p>Functionality for visual intercomparison of layers. The red line represents the limit of the GHNCA.</p>
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<p>Features for viewing and manipulating layer attributes. The red line represents the limit of the GHNCA.</p>
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<p>Vegetation Indices calculated in the GHN of Ciego de Avila, Cuba during the third quarter of the year 2023 emulating Sentinel-2 images. (<b>A</b>) NDVI, (<b>B</b>) EVI, (<b>C</b>) NDMI, and (<b>D</b>) CCCI.</p>
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16 pages, 9032 KiB  
Article
Assessing Vulnerability to Cyclone Hazards in the World’s Largest Mangrove Forest, The Sundarbans: A Geospatial Analysis
by Mohammed, Fahmida Sultana, Ariful Khan, Sohag Ahammed, Md. Shamim Reza Saimun, Md Saifuzzaman Bhuiyan, Sanjeev K. Srivastava, Sharif A. Mukul and Mohammed A. S. Arfin-Khan
Forests 2024, 15(10), 1722; https://doi.org/10.3390/f15101722 - 29 Sep 2024
Viewed by 1137
Abstract
The Sundarbans is the world’s largest contiguous mangrove forest with an area of about 10,000 square kilometers and shared between Bangladesh and India. This world-renowned mangrove forest, located on the lower Ganges floodplain and facing the Bay of Bengal, has long served as [...] Read more.
The Sundarbans is the world’s largest contiguous mangrove forest with an area of about 10,000 square kilometers and shared between Bangladesh and India. This world-renowned mangrove forest, located on the lower Ganges floodplain and facing the Bay of Bengal, has long served as a crucial barrier, shielding southern coastal Bangladesh from cyclone hazards. However, the Sundarbans mangrove ecosystem is now increasingly threatened by climate-induced hazards, particularly tropical cyclones originating from the Indian Ocean. To assess the cyclone vulnerability of this unique ecosystem, using geospatial techniques, we analyzed the damage caused by past cyclones and the subsequent recovery across three salinity zones, i.e., Oligohaline, Mesohaline, and Polyhaline. Our study also examined the relationship between cyclone intensity with the extent of damage and forest recovery. The findings of our study indicate that the Polyhaline zone, the largest in terms of area and with the lowest elevation, suffered the most significant damage from cyclones in the Sundarbans region, likely due to its proximity to the most cyclone paths. A correlation analysis revealed that cyclone damage positively correlated with wind speed and negatively correlated with the distance of landfall from the center of the Sundarbans. With the expectation of more extreme weather events in the near future, the Sundarbans mangrove forest faces a potentially devastating outlook unless both natural protection processes and human interventions are undertaken to safeguard this critical ecosystem. Full article
(This article belongs to the Special Issue Biodiversity, Health, and Ecosystem Services of Mangroves)
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<p>Path of the studied cyclones in the Bangladesh Sundarbans and the coverage of three saline zones (i.e., Polyhaline, Mesohaline, and Oligohaline) in the area. The red dot mark indicates the center point of the Sundarbans mangrove forest.</p>
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<p>Flowchart of the working procedures of cyclone damage and recovery analysis.</p>
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<p>Transition of the four NDVI classes after the occurrence of cyclones and their transitioned amount in square kilometers (km<sup>2</sup>). C1, C2, C3, and C4 represent Class 1, Class 2, Class 3, and Class 4 of pre-cyclone and post-cyclone NDVI classes, respectively. The total amount of area (in km<sup>2</sup>) of each class of pre-cyclone and post-cyclone NDVI is given under the class identifier (C1, C2, C3, and C4). Gray-colored inset boxes represent the unchanged area of each NDVI class after cyclone occurrence. A distinct colored number at the end of each line illustrates the amount of area (in km<sup>2</sup>) shifted to other classes.</p>
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<p>Transitioned area under different NDVI classes according to salinity zones in Bangladesh Sundarbans after the occurrence of 12 studied cyclones, where (<b>a</b>) represents the extent of the three saline zones.</p>
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<p>Four NDVI classes of both, pre-cyclone NDVI and post-cyclone NDVI, for the three saline zones of Bangladesh Sundarbans, where (<b>a</b>) represents the extent of the three saline zones.</p>
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<p>Cyclone-damaged areas in different saline zones are sorted by the year the cyclone occurred.</p>
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<p>Cyclone-recovered areas in different saline zones sorted by the year of cyclone occurred.</p>
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<p>Mean saline zone-wise values of (<b>a</b>) the damaged area and (<b>b</b>) the recovered area. Here, similar letters were used to represent no significant difference among saline zone-wise damaged and recovered areas, respectively.</p>
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<p>Results of correlation analysis of damage percentage (%) with cyclone variables, distance, and wind speed shown by (<b>a</b>) correlation matrix showing correlation coefficient values among different values; (<b>b</b>) results of Pearson’s correlation among damage percentage and wind speed (<b>c</b>); results of Pearson’s correlation among damage percentage and distance.</p>
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20 pages, 6529 KiB  
Article
Spatial Differentiation of Mangrove Aboveground Biomass and Identification of Its Main Environmental Drivers in Qinglan Harbor Mangrove Nature Reserve
by Kaiyue Wang, Meihuijuan Jiang, Yating Li, Shengnan Kong, Yilun Gao, Yingying Huang, Penghua Qiu, Yanli Yang and Siang Wan
Sustainability 2024, 16(19), 8408; https://doi.org/10.3390/su16198408 - 27 Sep 2024
Viewed by 760
Abstract
In the Bamen Bay area of the Qinglan Harbor Mangrove Provincial Nature Reserve in Wenchang, Hainan Province, China, mangrove aboveground biomass (AGB) was estimated using high-resolution UAV ortho-imagery and UAV LiDAR data. The spatial distribution characteristics of AGB were studied using global Moran’s [...] Read more.
In the Bamen Bay area of the Qinglan Harbor Mangrove Provincial Nature Reserve in Wenchang, Hainan Province, China, mangrove aboveground biomass (AGB) was estimated using high-resolution UAV ortho-imagery and UAV LiDAR data. The spatial distribution characteristics of AGB were studied using global Moran’s I index and hotspot analysis. Optimal geographic detectors and regression models were employed to analyze the relationship between AGB and key environmental factors. The results indicate that (1) the average AGB in the study area was 141.22 Mg/ha, with significant spatial variation. High AGB values were concentrated in the southwestern and northeastern regions, while low values were mainly found in the central and southeastern regions. (2) Plant species, water pH, soil total potassium, salinity, dissolved oxygen, elevation, soil organic matter, soil total phosphorus, and soil total nitrogen were identified as major factors influencing the spatial distribution of AGB. The interaction results indicate either bifactor enhancement or nonlinear enhancement, showing a significantly higher impact compared with single factors. (3) Comprehensive regression model results reveal that soil total nitrogen was the primary factor affecting AGB, followed by soil total potassium, with water pH having the least impact. Factors positively correlated with AGB promoted biomass growth, while elevation negatively affected AGB, inhibiting biomass accumulation. The findings provide critical insights that can guide targeted conservation efforts and management strategies aimed at enhancing mangrove ecosystem health and resilience, particularly by focusing on key areas identified for potential improvement and by addressing the complex interactions among environmental factors. Full article
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<p>Location of the study area and distribution of sampling points. The total area of mangrove habitat in the study area is 210 ha.</p>
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<p>Spatial distribution of mangrove plant species.</p>
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<p>Scatter diagram of verification results of mangrove AGB inversion model.</p>
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<p>Overview of the framework.</p>
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<p>Statistical diagram of AGB grid frequency of mangrove plant grid.</p>
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<p>Spatial distribution of environmental factors.</p>
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<p>Spatial distribution of environmental factors.</p>
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<p>(<b>a</b>) Moran’s I scatter plot; (<b>b</b>) hotspot analysis of aboveground biomass of mangrove plants.</p>
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<p>Two-factor interaction detection. Diagonal entries reflect the correlation between the specified independent and dependent variables.</p>
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<p>Spatial distribution of regression coefficients of influencing factors on mangrove AGB.</p>
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24 pages, 3135 KiB  
Review
Current Status of Remote Sensing for Studying the Impacts of Hurricanes on Mangrove Forests in the Coastal United States
by Abhilash Dutta Roy, Daria Agnieszka Karpowicz, Ian Hendy, Stefanie M. Rog, Michael S. Watt, Ruth Reef, Eben North Broadbent, Emma F. Asbridge, Amare Gebrie, Tarig Ali and Midhun Mohan
Remote Sens. 2024, 16(19), 3596; https://doi.org/10.3390/rs16193596 - 26 Sep 2024
Viewed by 1389
Abstract
Hurricane incidents have become increasingly frequent along the coastal United States and have had a negative impact on the mangrove forests and their ecosystem services across the southeastern region. Mangroves play a key role in providing coastal protection during hurricanes by attenuating storm [...] Read more.
Hurricane incidents have become increasingly frequent along the coastal United States and have had a negative impact on the mangrove forests and their ecosystem services across the southeastern region. Mangroves play a key role in providing coastal protection during hurricanes by attenuating storm surges and reducing erosion. However, their resilience is being increasingly compromised due to climate change through sea level rises and the greater intensity of storms. This article examines the role of remote sensing tools in studying the impacts of hurricanes on mangrove forests in the coastal United States. Our results show that various remote sensing tools including satellite imagery, Light detection and ranging (LiDAR) and unmanned aerial vehicles (UAVs) have been used to detect mangrove damage, monitor their recovery and analyze their 3D structural changes. Landsat 8 OLI (14%) has been particularly useful in long-term assessments, followed by Landsat 5 TM (9%) and NASA G-LiHT LiDAR (8%). Random forest (24%) and linear regression (24%) models were the most common modeling techniques, with the former being the most frequently used method for classifying satellite images. Some studies have shown significant mangrove canopy loss after major hurricanes, and damage was seen to vary spatially based on factors such as proximity to oceans, elevation and canopy structure, with taller mangroves typically experiencing greater damage. Recovery rates after hurricane-induced damage also vary, as some areas were seen to show rapid regrowth within months while others remained impacted after many years. The current challenges include capturing fine-scale changes owing to the dearth of remote sensing data with high temporal and spatial resolution. This review provides insights into the current remote sensing applications used in hurricane-prone mangrove habitats and is intended to guide future research directions, inform coastal management strategies and support conservation efforts. Full article
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<p>PRISMA workflow representing the systematic literature review process.</p>
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<p>Applications of remote sensing for studying impacts of hurricanes on mangroves.</p>
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<p>Coastal southeastern United States showing some locations where studies on hurricane impact on mangroves were carried out, that included (<b>A</b>) Everglades National Park, Florida, (<b>B</b>) Florida Keys, (<b>C</b>) Port Fourchon, Louisiana, (<b>D</b>) (Inset): Puerto Rico.</p>
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<p>The regional frequency of remote sensing based peer-reviewed articles published on studying impacts of hurricanes on mangroves in the United States from January 2010 to September 2024.</p>
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<p>Percentage breakdown of sensors used for studying impacts of hurricanes on mangroves in the United States from January 2010 to September 2024.</p>
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<p>Data analysis methods used to study the impacts of hurricanes on mangroves in the United States from January 2010 to September 2024.</p>
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15 pages, 2732 KiB  
Article
Allometric Models of Aboveground Biomass in Mangroves Compared with Those of the Climate Action Reserve Standard Applied in the Carbon Market
by Carlos Roberto Ávila-Acosta, Marivel Domínguez-Domínguez, César Jesús Vázquez-Navarrete, Rocío Guadalupe Acosta-Pech and Pablo Martínez-Zurimendi
Resources 2024, 13(9), 129; https://doi.org/10.3390/resources13090129 - 17 Sep 2024
Viewed by 1221
Abstract
The standardized methods used in carbon markets require measurement of the biomass and carbon stored in trees, which can be quantified through allometric equations. The objective of this study was to analyze aboveground biomass estimates with allometric models in three mangrove species and [...] Read more.
The standardized methods used in carbon markets require measurement of the biomass and carbon stored in trees, which can be quantified through allometric equations. The objective of this study was to analyze aboveground biomass estimates with allometric models in three mangrove species and compare them with those used by the Climate Action Reserve (CAR) standard. The mangrove forest in Tabasco, Mexico, was certified with the Forest Protocol for Mexico Version 2.0 (FPM) of the CAR standard. Allometric equations for mangrove species were reviewed to determine the most suitable equation for the calculation of biomass. The predictions of the allometric equations of the FPM were analyzed with data from Tabasco from the National Forest and Soil Inventory 2015–2020, and the percentages of trees within the ranges of diameters of the FPM equations were determined. The FPM equations generated higher biomass values for Rhizophora mangle and lower values for Avicennia germinans than the seven equations with which they were compared. In the mangrove swamp of Ejido Úrsulo Galván, Tabasco, 81.8% of the biomass of A. germinans, 34.4% of Laguncularia racemosa and 24.0% of R. mangle were within the diameter range of the FPM equations, and in Tabasco, 28.5% of A. germinans, 16.7% of L. racemosa and 5.7% of R. mangle were within the diameter range. For A. germinans and R. mangle, we recommend using the equation that considers greater maximum diameters. The allometric equations of the FPM do not adequately predict a large percentage of the biomass. Full article
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<p>Predictions of the allometric equation of Smith and Whelan [<a href="#B16-resources-13-00129" class="html-bibr">16</a>] were applied to <span class="html-italic">A. germinans</span> and compared with the predictions of equations developed by other authors. Source of the equations: Smith y Whelan (2006) [<a href="#B16-resources-13-00129" class="html-bibr">16</a>], Day et al. (1987) [<a href="#B9-resources-13-00129" class="html-bibr">9</a>], Fromard et al. (1998) [<a href="#B18-resources-13-00129" class="html-bibr">18</a>], Imbert and Rollet (1989) [<a href="#B17-resources-13-00129" class="html-bibr">17</a>], Yepes et al. (2016) [<a href="#B22-resources-13-00129" class="html-bibr">22</a>], Komiyama et al. (2005) [<a href="#B4-resources-13-00129" class="html-bibr">4</a>], Chave et al. (2005) [<a href="#B20-resources-13-00129" class="html-bibr">20</a>].</p>
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<p>Predictions of the allometric equation of Day et al. [<a href="#B9-resources-13-00129" class="html-bibr">9</a>] were applied to <span class="html-italic">L. racemosa</span> and compared with the predictions of equations developed by other authors. Source of the equations: Day et al. (1987) [<a href="#B9-resources-13-00129" class="html-bibr">9</a>], Smith y Whelan (2006) [<a href="#B16-resources-13-00129" class="html-bibr">16</a>], Fromard et al. (1998) [<a href="#B18-resources-13-00129" class="html-bibr">18</a>], Imbert and Rollet (1989) [<a href="#B17-resources-13-00129" class="html-bibr">17</a>], Medeiros and Sampaio (2008) [<a href="#B21-resources-13-00129" class="html-bibr">21</a>], Komiyama et al. (2005) [<a href="#B4-resources-13-00129" class="html-bibr">4</a>], Chave et al. (2005) [<a href="#B20-resources-13-00129" class="html-bibr">20</a>].</p>
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<p>Predictions of the allometric equation of Day et al. [<a href="#B9-resources-13-00129" class="html-bibr">9</a>] were applied to <span class="html-italic">R. mangle</span> and compared with the predictions of equations developed by other authors. Source of the equations: Day et al. (1987) [<a href="#B9-resources-13-00129" class="html-bibr">9</a>], Smith y Whelan (2006) [<a href="#B16-resources-13-00129" class="html-bibr">16</a>], Fromard et al. (1998) [<a href="#B18-resources-13-00129" class="html-bibr">18</a>], Imbert and Rollet (1989) [<a href="#B17-resources-13-00129" class="html-bibr">17</a>], Gomes and Schaeffer-Novelli (2005) [<a href="#B19-resources-13-00129" class="html-bibr">19</a>], Yepes et al. (2016) [<a href="#B22-resources-13-00129" class="html-bibr">22</a>], Medeiros and Sampaio (2008) [<a href="#B21-resources-13-00129" class="html-bibr">21</a>], Komiyama et al. (2005) [<a href="#B4-resources-13-00129" class="html-bibr">4</a>], Chave et al. (2005) [<a href="#B20-resources-13-00129" class="html-bibr">20</a>].</p>
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<p>Biomass of <span class="html-italic">A. germinans</span> obtained via different allometric equations within the ranges of diameters. The solid line represents the biomass obtained at 21.5 cm in diameter according to the Smith and Whelan equation [<a href="#B16-resources-13-00129" class="html-bibr">16</a>]. Source of the equations: Smith y Whelan (2006) [<a href="#B16-resources-13-00129" class="html-bibr">16</a>], Day et al. (1987) [<a href="#B9-resources-13-00129" class="html-bibr">9</a>], Fromard et al. (1998) [<a href="#B18-resources-13-00129" class="html-bibr">18</a>], Imbert and Rollet (1989) [<a href="#B17-resources-13-00129" class="html-bibr">17</a>], Yepes et al. (2016) [<a href="#B22-resources-13-00129" class="html-bibr">22</a>], Komiyama et al. (2005) [<a href="#B4-resources-13-00129" class="html-bibr">4</a>], Chave et al. (2005) [<a href="#B20-resources-13-00129" class="html-bibr">20</a>].</p>
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<p>Biomass of <span class="html-italic">L. racemosa</span> obtained with various allometric equations within the ranges of diameters. The solid line represents the biomass obtained at a diameter of 10 cm via the equation of Day et al. [<a href="#B9-resources-13-00129" class="html-bibr">9</a>]. Source of the equations: Day et al. (1987) [<a href="#B9-resources-13-00129" class="html-bibr">9</a>], Smith y Whelan (2006) [<a href="#B16-resources-13-00129" class="html-bibr">16</a>], Fromard et al. (1998) [<a href="#B18-resources-13-00129" class="html-bibr">18</a>], Imbert and Rollet (1989) [<a href="#B17-resources-13-00129" class="html-bibr">17</a>], Medeiros and Sampaio (2008) [<a href="#B21-resources-13-00129" class="html-bibr">21</a>], Komiyama et al. (2005) [<a href="#B4-resources-13-00129" class="html-bibr">4</a>], Chave et al. (2005) [<a href="#B20-resources-13-00129" class="html-bibr">20</a>].</p>
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<p>Biomass of <span class="html-italic">R. mangle</span> obtained with various allometric equations within the ranges of diameters. The solid line represents the biomass obtained at a diameter of 10 cm via the equation of Day et al. [<a href="#B9-resources-13-00129" class="html-bibr">9</a>]. Source of the equations: Day et al. (1987) [<a href="#B9-resources-13-00129" class="html-bibr">9</a>], Smith y Whelan (2006) [<a href="#B16-resources-13-00129" class="html-bibr">16</a>], Fromard et al. (1998) [<a href="#B18-resources-13-00129" class="html-bibr">18</a>], Imbert and Rollet (1989) [<a href="#B17-resources-13-00129" class="html-bibr">17</a>], Gomes and Schaeffer-Novelli (2005) [<a href="#B19-resources-13-00129" class="html-bibr">19</a>], Yepes et al. (2016) [<a href="#B22-resources-13-00129" class="html-bibr">22</a>], Medeiros and Sampaio (2008) [<a href="#B21-resources-13-00129" class="html-bibr">21</a>], Komiyama et al. (2005) [<a href="#B4-resources-13-00129" class="html-bibr">4</a>], Chave et al. (2005) [<a href="#B20-resources-13-00129" class="html-bibr">20</a>].</p>
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<p>Average diameters of <span class="html-italic">A. germinans</span>, <span class="html-italic">L. racemosa</span> and <span class="html-italic">R. mangle</span> according to the National Forest and Soil Inventory 2015–2020 CONAFOR for Tabasco.</p>
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43 pages, 24204 KiB  
Article
Support Vector Machine Algorithm for Mapping Land Cover Dynamics in Senegal, West Africa, Using Earth Observation Data
by Polina Lemenkova
Earth 2024, 5(3), 420-462; https://doi.org/10.3390/earth5030024 - 6 Sep 2024
Viewed by 1065
Abstract
This paper addresses the problem of mapping land cover types in Senegal and recognition of vegetation systems in the Saloum River Delta on the satellite images. Multi-seasonal landscape dynamics were analyzed using Landsat 8-9 OLI/TIRS images from 2015 to 2023. Two image classification [...] Read more.
This paper addresses the problem of mapping land cover types in Senegal and recognition of vegetation systems in the Saloum River Delta on the satellite images. Multi-seasonal landscape dynamics were analyzed using Landsat 8-9 OLI/TIRS images from 2015 to 2023. Two image classification methods were compared, and their performance was evaluated in the GRASS GIS software (version 8.4.0, creator: GRASS Development Team, original location: Champaign, Illinois, USA, currently multinational project) by means of unsupervised classification using the k-means clustering algorithm and supervised classification using the Support Vector Machine (SVM) algorithm. The land cover types were identified using machine learning (ML)-based analysis of the spectral reflectance of the multispectral images. The results based on the processed multispectral images indicated a decrease in savannas, an increase in croplands and agricultural lands, a decline in forests, and changes to coastal wetlands, including mangroves with high biodiversity. The practical aim is to describe a novel method of creating land cover maps using RS data for each class and to improve accuracy. We accomplish this by calculating the areas occupied by 10 land cover classes within the target area for six consecutive years. Our results indicate that, in comparing the performance of the algorithms, the SVM classification approach increased the accuracy, with 98% of pixels being stable, which shows qualitative improvements in image classification. This paper contributes to the natural resource management and environmental monitoring of Senegal, West Africa, through advanced cartographic methods applied to remote sensing of Earth observation data. Full article
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<p>Study area with segments of the Landsat images shown on a topographic map of Senegal. Software: GMT. Map source: Author.</p>
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<p>Data capture of Landsat images from the USGS EarthExplorer repository.</p>
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<p>Landsat images in RGB colors covering the Cape Verde Peninsula region and Saloum River Delta, West Senegal, in February: (<b>a</b>) 2015; (<b>b</b>) 2018; (<b>c</b>) 2020; (<b>d</b>) 2021; (<b>e</b>) 2022; (<b>f</b>) 2023.</p>
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<p>Workflow scheme illustrating the data and the main methodological steps. Software: R version 4.3.3, library DiagrammeR version 1.0.11. Diagram source: Author.</p>
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<p>False color composites of the Landsat 8-9 OLI/TIRS images with vegetation colored red, using a combination of spectral bands 5 (Near Infrared (NIR)), 4 (Red), and 3 (Green) of the Landsat OLI sensor covering the study area in the Cape Verde Peninsula region and Saloum River Delta, West Senegal, using February scenes: (<b>a</b>) 2015; (<b>b</b>) 2018; (<b>c</b>) 2020; (<b>d</b>) 2021; (<b>e</b>) 2022; (<b>f</b>) 2023.</p>
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<p>Land cover types in Senegal according to the FAO classification scheme. Software: QGIS v. 3.22. Map source: Author.</p>
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<p>Classification of the Landsat images from 2020 covering the Cape Verde Peninsula region and the Saloum River Delta, West Senegal: (<b>a</b>) 2015; (<b>b</b>) 2018; (<b>c</b>) 2020; (<b>d</b>) 2021; (<b>e</b>) 2022; (<b>f</b>) 2023.</p>
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<p>Results of the Support Vector Machine (SVM)-based classification of the Landsat images covering the Cape Verde Peninsula region and Saloum River Delta, West Senegal: (<b>a</b>) February 2015; (<b>b</b>) February 2018; (<b>c</b>) February 2020; (<b>d</b>) February 2021; (<b>e</b>) February 2022; (<b>f</b>) February 2023.</p>
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<p>Accuracy evaluated based on the pixel confidence levels with rejection probability values for the Landsat images covering the Cape Verde Peninsula region and Saloum River Delta, West Senegal: (<b>a</b>) 2015; (<b>b</b>) 2018; (<b>c</b>) 2020; (<b>d</b>) 2021; (<b>e</b>) 2022;(<b>f</b>) 2023.</p>
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20 pages, 9179 KiB  
Article
EIAGA-S: Rapid Mapping of Mangroves Using Geospatial Data without Ground Truth Samples
by Yuchen Zhao, Shulei Wu, Xianyao Zhang, Hui Luo, Huandong Chen and Chunhui Song
Forests 2024, 15(9), 1512; https://doi.org/10.3390/f15091512 - 29 Aug 2024
Viewed by 606
Abstract
Mangrove forests are essential for coastal protection and carbon sequestration, yet accurately mapping their distribution remains challenging due to spectral similarities with other vegetation. This study introduces a novel unsupervised learning method, the Elite Individual Adaptive Genetic Algorithm-Semantic Inference (EIAGA-S), designed for the [...] Read more.
Mangrove forests are essential for coastal protection and carbon sequestration, yet accurately mapping their distribution remains challenging due to spectral similarities with other vegetation. This study introduces a novel unsupervised learning method, the Elite Individual Adaptive Genetic Algorithm-Semantic Inference (EIAGA-S), designed for the high-precision semantic segmentation of mangrove forests using remote sensing images without the need for ground truth samples. EIAGA-S integrates an adaptive Genetic Algorithm with an elite individual’s evolution strategy, optimizing the segmentation process. A new Mangrove Enhanced Vegetation Index (MEVI) was developed to better distinguish mangroves from other vegetation types within the spectral feature space. EIAGA-S constructs segmentation rules through iterative rule stacking and enhances boundary information using connected component analysis. The method was evaluated using a multi-source remote sensing dataset covering the Hainan Dongzhai Port Mangrove Nature Reserve in China. The experimental results demonstrate that EIAGA-S achieves a superior overall mIoU (mean intersection over union) of 0.92 and an F1 score of 0.923, outperforming traditional models such as K-means and SVM (Support Vector Machine). A detailed boundary analysis confirms EIAGA-S’s ability to extract fine-grained mangrove patches. The segmentation includes five categories: mangrove canopy, other terrestrial vegetation, buildings and streets, bare land, and water bodies. The proposed EIAGA-S model offers a precise and data-efficient solution for mangrove semantic mapping while eliminating the dependency on extensive field sampling and labeled data. Additionally, the MEVI index facilitates large-scale mangrove monitoring. In future work, EIAGA-S can be integrated with long-term remote sensing data to analyze mangrove forest dynamics under climate change conditions. This innovative approach has potential applications in rapid forest change detection, environmental protection, and beyond. Full article
(This article belongs to the Section Forest Inventory, Modeling and Remote Sensing)
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<p>Location of the study. (<b>a</b>) Administrative map of China; (<b>b</b>) distribution of cities and counties on Hainan Island; (<b>c</b>) Dongzhai Port Mangrove Nature Reserve.</p>
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<p>The flowchart of semantic segmentation using EIAGA-S on WorldView-2 data for the study area.</p>
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<p>Flowchart of Elite Individual Adaptive Genetic Algorithm. (<b>a</b>) Improvements to the Crossover module; (<b>b</b>) improvements to the Mutation module; (<b>c</b>) addition of the elite-individual-directed Evolution module.</p>
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<p>Comparison of segmentation results for different algorithms.</p>
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<p>Comparison of experimental segmentation results of different algorithms for mangroves, houses, water pools, rivers, and land areas. (a) Mangroves and water pools area; (b) Mangroves and rivers area; (c) Mangroves and water pools area; (d) Houses and land area; (e) Land areas.</p>
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<p>Comparison of ablation parameters optimized by EIAGA model. (<b>a</b>) Optimization results for different kPc parameters; (<b>b</b>) optimization results for different kPm1 parameters; (<b>c</b>) optimization results for different kPm2 parameters; (<b>d</b>) optimization results for different kGm parameters.</p>
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<p>Comparison of GA and EIAGA models’ effects. (<b>a</b>) The optimization results for the EIAGA model under different iteration rounds; (<b>b</b>) comparison of GA and EIAGA optimization results; (<b>c</b>) optimization results for GA model under different iteration rounds.</p>
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<p>Comparison of GA and EIAGA model effects. (<b>a</b>) 1000 rounds of EIAGA model optimization results; (<b>b</b>) comparison of GA and EIAGA for 1000 rounds of optimization results; (<b>c</b>) 1000 rounds of GA model optimization results; (<b>d</b>) 2000 rounds of EIAGA model optimization results; (<b>e</b>) comparison of GA and EIAGA for 2000 rounds of optimization results; (<b>f</b>) 2000 rounds of GA model optimization results; (<b>g</b>) 3000 rounds of EIAGA model optimization results; (<b>h</b>) comparison of GA and EIAGA for 3000 rounds of optimization results; (<b>i</b>) 3000 rounds of GA model optimization results.</p>
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<p>MEVI thermal maps for various locations. Red and white circles mark the tidal flat areas detected by different algorithms. (<b>a</b>) Dongzhai Port, (<b>b</b>) Dongfang, (<b>c</b>) Maowei Sea.</p>
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<p>Experimental results for the Mangrove Density Vegetation Index (MDVI)’s empirical parameters: (<b>a</b>) Sampling points used for validation; (<b>b</b>) variation in evaluation metrics across different parameter settings.</p>
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15 pages, 297 KiB  
Review
Blue Carbon as a Nature-Based Mitigation Solution in Temperate Zones
by Mine Cinar, Nathalie Hilmi, Gisele Arruda, Laura Elsler, Alain Safa and Jeroen A. J. M. van de Water
Sustainability 2024, 16(17), 7446; https://doi.org/10.3390/su16177446 - 28 Aug 2024
Viewed by 1895
Abstract
Concern for the future requires local steward-led cooperation between natural and social scientists and decision-makers to develop informed and policy-relevant nature-based mitigation solutions, including blue carbon (BC), which can help secure the future. Salt marshes, kelp forests, and seagrass meadows (and to a [...] Read more.
Concern for the future requires local steward-led cooperation between natural and social scientists and decision-makers to develop informed and policy-relevant nature-based mitigation solutions, including blue carbon (BC), which can help secure the future. Salt marshes, kelp forests, and seagrass meadows (and to a lesser extent mangroves) are significant BC ecosystems in temperate areas. We discuss the concept of blue carbon stocks and the scientific approaches to building BC stocks considering the variability in local conditions and the co-benefits of blue carbon ecosystems to improve climate change mitigation and adaptation mechanisms. The study examines (1) methods to assess the potential of BC ecosystems and the impact of disturbances, while (2) building relevant policy based on socio-economic assessments of impacted communities. We highlight economic and social approaches to rebuilding BC using financial tools such as blue bonds, development plans, cost-benefit analyses, cross-ecosystem restoration projects, AI and blockchain, and economic accounts of coastal ecosystems, while emphasizing that cutting carbon emissions is more important than (re)building BC stocks. Full article
(This article belongs to the Section Sustainable Oceans)
22 pages, 7710 KiB  
Review
Review of the Current Status and Development Trend of Global Forest Carbon Storage Research Based on Bibliometrics
by Chenchen Wu, Yang Yang and Tianxiang Yue
Forests 2024, 15(9), 1498; https://doi.org/10.3390/f15091498 - 27 Aug 2024
Viewed by 1676
Abstract
Forests are one of the largest terrestrial ecosystems on Earth, absorbing carbon dioxide from the atmosphere through photosynthesis and storing it as organic carbon, thereby mitigating global warming. Conducting bibliometric analysis of forest carbon storage can identify current research trends and hot issues [...] Read more.
Forests are one of the largest terrestrial ecosystems on Earth, absorbing carbon dioxide from the atmosphere through photosynthesis and storing it as organic carbon, thereby mitigating global warming. Conducting bibliometric analysis of forest carbon storage can identify current research trends and hot issues in this field, providing data support for researchers and policy makers. This review article provides a comprehensive bibliometric analysis of global forest carbon storage research, using databases from the Web of Science Core Collection. CiteSpace software (6.2.6 version) was employed to visualize and analyze the data, focusing on key researchers, institutions, and countries, as well as major research themes and emerging trends. The main findings are as follows: (1) Since the 21st century, the publication volume in this field has been increasing, with the United States and China being the top contributors. (2) There is active collaboration among key authors, institutions, and countries, with a notable close-knit network centered around French author Philippe Ciais. This group includes nearly half of the field’s authors and many of them are crucial for advancing research in this field. (3) Cluster and citation burst analyses suggest that future research will focus more on the impact of forest management policies on carbon stocks, with particular attention to the roles of northern temperate forests and mangroves in global carbon storage. These findings provide valuable insights into the current state and future directions of forest carbon storage research. This article is instrumental in elucidating the role of forest ecosystems within the global carbon cycle, evaluating the impacts of anthropogenic activities on forest carbon stocks, and informing the development of effective climate change mitigation strategies. Full article
(This article belongs to the Special Issue Forest Inventory: The Monitoring of Biomass and Carbon Stocks)
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<p>The overall workflow.</p>
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<p>The global publication trends of the particular study field and all science study fields. The blue line is the annual articles published in the field of forest carbon storage research from 1993 to 2023. The red line is the reference line showing the annual articles published in scientific and technical journals worldwide. The scientific and technical journals include the journals in physics, biology, chemistry, mathematics, clinical medicine, biomedical research, engineering and technology, and earth and space sciences study fields.</p>
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<p>(<b>a</b>) The trend in the annual number of publications from 1993 to 2023 for the five countries with the highest publication counts in the field; (<b>b</b>) the trend of the number of scientific journal articles per million people in these five countries (using the data from “Our World in Data” [<a href="#B15-forests-15-01498" class="html-bibr">15</a>]).</p>
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<p>The percentage stacked area plot considering the five countries with the highest publication counts in the field.</p>
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<p>Author collaboration network.</p>
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<p>Institution collaboration network.</p>
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<p>International collaboration network.</p>
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<p>Co-citation and high centrality article hybrid network.</p>
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<p>Timeline view of co-citation clusters in the literature on forest carbon storage. Note: Two question marks appear in the top left corner of the image, which is due to CiteSpace’s inability to recognise the name of one of the authors. The corresponding content is Pörtner and the corresponding article is [<a href="#B23-forests-15-01498" class="html-bibr">23</a>] of the reference list.</p>
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16 pages, 10234 KiB  
Article
Temporal Variations in Methane Emissions from a Restored Mangrove Ecosystem in Southern China
by Pengpeng Tian, Xianglan Li, Zhe Xu, Liangxu Wu, Yuting Huang, Zhao Zhang, Mengna Chen, Shumin Zhang, Houcai Cai, Minghai Xu and Wei Chen
Forests 2024, 15(9), 1487; https://doi.org/10.3390/f15091487 - 24 Aug 2024
Viewed by 889
Abstract
The role of coastal mangrove wetlands in sequestering atmospheric carbon dioxide has been increasingly investigated in recent years. While studies have shown that mangroves are weak sources of methane (CH4) emissions, measurements of CH4 fluxes from these ecosystems remain scarce. [...] Read more.
The role of coastal mangrove wetlands in sequestering atmospheric carbon dioxide has been increasingly investigated in recent years. While studies have shown that mangroves are weak sources of methane (CH4) emissions, measurements of CH4 fluxes from these ecosystems remain scarce. In this study, we examined the temporal variation and biophysical drivers of ecosystem-scale CH4 fluxes in China’s northernmost mangrove ecosystem based on eddy covariance measurements obtained over a 3-year period. In this mangrove, the annual CH4 emissions ranged from 6.15 to 9.07 g C m−2 year−1. The daily CH4 flux reached a peak of over 0.07 g C m−2 day−1 during the summer, while the winter CH4 flux was negligible. Latent heat, soil temperature, photosynthetically active radiation, and tide water level were the primary factors controlling CH4 emissions. This study not only elucidates the mechanisms influencing CH4 emissions from mangroves, strengthening the understanding of these processes but also provides a valuable benchmark dataset to validate the model-derived carbon budget estimates for these ecosystems. Full article
(This article belongs to the Section Forest Ecology and Management)
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<p>Photograph (<b>a</b>) and location (<b>b</b>) of the eddy covariance flux tower established for measuring net ecosystem exchange of greenhouse gases over a restored mangrove in China (<b>c</b>).</p>
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<p>Time series plots of measured biophysical variables in the restored mangrove between 2020 and 2022, including (<b>a</b>) daily and monthly average air temperature and daily precipitation, (<b>b</b>) daily and monthly average PAR, (<b>c</b>) daily and monthly average VPD, (<b>d</b>) daily and monthly average LE, and (<b>e</b>) daily average, minimum, and maximum as well as monthly average tidal water levels.</p>
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<p>Diurnal patterns of the CH<sub>4</sub> flux in 2020 (<b>a</b>), 2021 (<b>b</b>), and 2022 (<b>c</b>), and average pattern for the 3-year period (2020–2022) (<b>d</b>). The gray area denotes the 95% confidence interval.</p>
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<p>Daily (gray bars) and monthly (red dots) variations in CH<sub>4</sub> flux from March 2020 to December 2020. The lighter gray bars represent daily values filled in using RF model simulations.</p>
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<p>Coefficients of correlation between environmental variables and the CH<sub>4</sub> flux in (<b>a</b>) 2020, (<b>b</b>) 2021, and (<b>c</b>) 2022. The environmental variables included soil water content (SWC), air temperature (Tair), sensible heat (H), photosynthetically active radiation (PAR), vapor pressure deficit (VPD), soil temperature (T<sub>soil</sub>), rainfall, relative humidity (RH), latent heat (LE), and tide water level (TWL). These parameters are expressed as daily averages, except for precipitation, which, here, is indicated as a cumulative value.</p>
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<p>Relationships between the monthly integrated CH<sub>4</sub> flux and (<b>a</b>) latent heat, (<b>b</b>) photosynthetically active radiation, (<b>c</b>) air temperature, and (<b>d</b>) soil temperature. All the relationships shown were significant at <span class="html-italic">p</span> ≤ 0.001. Red area represents the 95% confidence interval of the fitted line.</p>
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<p>Results of path analysis examining the relationships between the CH<sub>4</sub> flux and environmental variables in (<b>a</b>) 2020, (<b>b</b>) 2021, and (<b>c</b>) 2022. The environmental variables included soil water content (SWC), photosynthetically active radiation (PAR), vapor pressure deficit (VPD), sensible heat (H), air temperature (Tair), tide water level (TWL), relative humidity (RH), latent heat (LE), and soil temperature (Tsoil). The values of these parameters are expressed as daily averages. Blue represents a positive effect; orange represents a negative effect. * indicates <span class="html-italic">p</span> &lt; 0.05, ** indicates <span class="html-italic">p</span> &lt; 0.01, and *** indicates <span class="html-italic">p</span> &lt; 0.001.</p>
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<p>Latitudinal patterns of CH<sub>4</sub> fluxes from mangroves measured using chambers (blue points) and EC (green points), and their regression.</p>
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26 pages, 6113 KiB  
Review
Methods Using Marine Aquatic Photoautotrophs along the Qatari Coastline to Remediate Oil and Gas Industrial Water
by Roda F. Al-Thani and Bassam T. Yasseen
Toxics 2024, 12(9), 625; https://doi.org/10.3390/toxics12090625 - 24 Aug 2024
Viewed by 1191
Abstract
Qatar and other Gulf States have a diverse range of marine vegetation that is adapted to the stressful environmental conditions of seawater. The industrial wastewater produced by oil and gas activities adds further detrimental conditions for marine aquatic photosynthetic organisms on the Qatari [...] Read more.
Qatar and other Gulf States have a diverse range of marine vegetation that is adapted to the stressful environmental conditions of seawater. The industrial wastewater produced by oil and gas activities adds further detrimental conditions for marine aquatic photosynthetic organisms on the Qatari coastlines. Thus, these organisms experience severe stress from both seawater and industrial wastewater. This review discusses the biodiversity in seawater around Qatar, as well as remediation methods and metabolic pathways to reduce the negative impacts of heavy metals and petroleum hydrocarbons produced during these activities. The role of microorganisms that are adjacent to or associated with these aquatic marine organisms is discussed. Exudates that are released by plant roots enhance the role of microorganisms to degrade organic pollutants and immobilize heavy metals. Seaweeds may have other roles such as biosorption and nutrient uptake of extra essential elements to avoid or reduce eutrophication in marine environments. Special attention is paid to mangrove forests and their roles in remediating shores polluted by industrial wastewater. Seagrasses (Halodule uninervis, Halophila ovalis, and Thalassia hemprichii) can be used as promising candidates for phytoremediation or bioindicators for pollution status. Some genera among seaweeds that have proven efficient in accumulating the most common heavy metals found in gas activities and biodegradation of petroleum hydrocarbons are discussed. Full article
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<p>Map of Qatar showing the locations of mangrove forests on the eastern coastline.</p>
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<p><span class="html-italic">Avicennia marina</span> is the only species represented in mangroves in Qatar. A part of a mangrove forest showing trees and propagules.</p>
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23 pages, 39394 KiB  
Article
Fine-Scale Mangrove Species Classification Based on UAV Multispectral and Hyperspectral Remote Sensing Using Machine Learning
by Yuanzheng Yang, Zhouju Meng, Jiaxing Zu, Wenhua Cai, Jiali Wang, Hongxin Su and Jian Yang
Remote Sens. 2024, 16(16), 3093; https://doi.org/10.3390/rs16163093 - 22 Aug 2024
Viewed by 1545
Abstract
Mangrove ecosystems play an irreplaceable role in coastal environments by providing essential ecosystem services. Diverse mangrove species have different functions due to their morphological and physiological characteristics. A precise spatial distribution map of mangrove species is therefore crucial for biodiversity maintenance and environmental [...] Read more.
Mangrove ecosystems play an irreplaceable role in coastal environments by providing essential ecosystem services. Diverse mangrove species have different functions due to their morphological and physiological characteristics. A precise spatial distribution map of mangrove species is therefore crucial for biodiversity maintenance and environmental conservation of coastal ecosystems. Traditional satellite data are limited in fine-scale mangrove species classification due to low spatial resolution and less spectral information. This study employed unmanned aerial vehicle (UAV) technology to acquire high-resolution multispectral and hyperspectral mangrove forest imagery in Guangxi, China. We leveraged advanced algorithms, including RFE-RF for feature selection and machine learning models (Adaptive Boosting (AdaBoost), eXtreme Gradient Boosting (XGBoost), Random Forest (RF), and Light Gradient Boosting Machine (LightGBM)), to achieve mangrove species mapping with high classification accuracy. The study assessed the classification performance of these four machine learning models for two types of image data (UAV multispectral and hyperspectral imagery), respectively. The results demonstrated that hyperspectral imagery had superiority over multispectral data by offering enhanced noise reduction and classification performance. Hyperspectral imagery produced mangrove species classification with overall accuracy (OA) higher than 91% across the four machine learning models. LightGBM achieved the highest OA of 97.15% and kappa coefficient (Kappa) of 0.97 based on hyperspectral imagery. Dimensionality reduction and feature extraction techniques were effectively applied to the UAV data, with vegetation indices proving to be particularly valuable for species classification. The present research underscored the effectiveness of UAV hyperspectral images using machine learning models for fine-scale mangrove species classification. This approach has the potential to significantly improve ecological management and conservation strategies, providing a robust framework for monitoring and safeguarding these essential coastal habitats. Full article
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<p>Study area and UAV-based visible image ((<b>A</b>): Yingluo Bay, (<b>B</b>): Pearl Bay).</p>
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<p>Workflow diagram illustrating the methodology of this study.</p>
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<p>Mangrove species classification comparison of user’s and producer’s accuracies obtained by four learning models based on multi- and hyper-spectral images in Yingluo Bay.</p>
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<p>Mangrove species classification comparison of user’s and producer’s accuracies obtained by LightGBM learning model based on the multi- and hyper-spectral image in Pearl Bay.</p>
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<p>The mangrove species classification maps using four learning models (LightGBM, RF, XGBoost, and AdaBoost) based on UAV multispectral image (<b>a</b>–<b>d</b>) and hyperspectral image (<b>e</b>–<b>h</b>), respectively, in Yingluo Bay.</p>
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<p>The UAV visual image covering Yingluo Bay and three subsets (<b>A</b>–<b>C</b>) of the UAV multispectral and hyperspectral image classification results based on the LightGBM learning model.</p>
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<p>The mangrove species classification maps using the LightGBM learning model based on UAV multispectral image (<b>a</b>) and hyperspectral image (<b>b</b>) in Pearl Bay.</p>
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<p>The UAV visual image covering Pearl Bay and three subsets (<b>A</b>–<b>C</b>) of the UAV multispectral and hyperspectral image classification results using LightGBM learning model.</p>
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<p>Normalized confusion matrices of mangrove species classification using four learning models (AdaBoost, XGboost, RF, and LightGBM) based on UAV multi- and hyper-spectral images in Yingluo Bay.</p>
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