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Search Results (562)

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18 pages, 18618 KiB  
Article
Extraction of Mangrove Community of Kandelia obovata in China Based on Google Earth Engine and Dense Sentinel-1/2 Time Series Data
by Chen Lin, Jiali Zheng, Luojia Hu and Luzhen Chen
Remote Sens. 2025, 17(5), 898; https://doi.org/10.3390/rs17050898 - 4 Mar 2025
Viewed by 167
Abstract
Although significant progress has been made in the remote sensing extraction of mangroves, research at the species level remains relatively limited. Kandelia obovata is a dominant mangrove species and is frequently used in ecological restoration projects in China. However, owing to the fragmented [...] Read more.
Although significant progress has been made in the remote sensing extraction of mangroves, research at the species level remains relatively limited. Kandelia obovata is a dominant mangrove species and is frequently used in ecological restoration projects in China. However, owing to the fragmented distribution of K. obovata within mixed mangrove communities and the significant spectral and textural similarities among mangrove species, accurately extracting large-scale K. obovata-based remote sensing data remains a challenging task. In this study, we conducted extensive field surveys and developed a comprehensive sampling database covering K. obovata and other mangrove species across mangrove-distributing areas in China. We identified the optimal bands for extracting K. obovata by utilizing time-series remote sensing data from Sentinel-1 and Sentinel-2, along with the Google Earth Engine (GEE), and proposed a method for extracting K. obovata communities. The main conclusions are as follows: (1) The spectral-temporal variability characteristics of the blue and red-edge bands play a crucial role in the identification of K. obovata communities. The 90th percentile metric of the blue wavelength band ranks first in importance, while the 75th percentile metric of the blue wavelength band ranks second; (2) This method of remote sensing extraction using spectral-temporal variability metrics with time-series optical and radar remote sensing data offers significant advantages in identifying the K. obovata species, achieving a producer’s accuracy of up to 94.6%; (3) In 2018, the total area of pure K. obovata communities in China was 4825.97 ha; (4) In the southern provinces of China, Guangdong Province has the largest K. obovata community area, while Macau has the smallest. This research contributes to the understanding of mangrove ecosystems and provides a methodological framework for monitoring K. obovata and other coastal vegetation using advanced remote sensing technologies. Full article
(This article belongs to the Special Issue Remote Sensing in Mangroves III)
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<p>Location of the study area.</p>
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<p>Experimental Workflow Diagram.</p>
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<p>Sample plot survey purebred location.</p>
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<p>Sample points distribution map. The red boxes in the figure correspond to the plots in <a href="#remotesensing-17-00898-t002" class="html-table">Table 2</a>.</p>
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<p>Quintile plots of spectral characteristics of <span class="html-italic">K. obovata</span> community with other species. The error bars in the figure represent the standard deviation of each species at different percentiles.</p>
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<p>Distribution of <span class="html-italic">K. obovata</span> in China, 2018. (<b>a</b>) shows the distribution of <span class="html-italic">K. obovata</span> in China. (<b>b</b>) presents the extraction results in the Zhangjiang Estuary, Fujian province. (<b>c</b>) displays the extraction results in Futian, Shenzhen. (<b>d</b>) shows the extraction results in Dongzhaigang, Hainan province. In subplots (<b>b</b>–<b>d</b>), the yellow lines represent the distribution range of <span class="html-italic">K. obovata</span>.</p>
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<p>Comparison of <span class="html-italic">K. obovata</span> results. (<b>a-1</b>), (<b>b-1</b>), and (<b>c-1</b>) show the extraction results by Zhao et al. [<a href="#B18-remotesensing-17-00898" class="html-bibr">18</a>] in Estuary of Jiulong River, Quanzhou Bay, and Wenzhou, Zhejiang, respectively. (<b>a-2</b>), (<b>b-2</b>), and (<b>c-2</b>) show the extraction results of this study. (<b>a-3</b>)~(<b>a-5</b>), (<b>b-3</b>)~(<b>b-5</b>), and (<b>c-3</b>)~(<b>c-5</b>) represent the actual remote sensing features of the corresponding regions. The yellow lines indicate the <span class="html-italic">K. obovata</span> boundaries extracted by us, while the red lines represent the boundaries extracted by Zhao et al.</p>
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<p>The performance of research results at a small scale. (<b>a-1</b>) shows the extraction results by Li et al. [<a href="#B21-remotesensing-17-00898" class="html-bibr">21</a>] at Zhangjiangkou, and (<b>a-2</b>) shows the present results. (<b>b-1</b>) shows the results by Wang et al. [<a href="#B24-remotesensing-17-00898" class="html-bibr">24</a>] at Sanjiang, Hainan, and (<b>b-2</b>) shows results of the present study.</p>
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16 pages, 2439 KiB  
Article
Comparative Analysis of Drought-Driven Water-Use Strategies in Mangroves and Forests
by Xin Li, Feng An, You Wang, Manyao Gong, Huiting Xu, Binbin Zheng, Lu Dong and Rui Yu
Forests 2025, 16(3), 396; https://doi.org/10.3390/f16030396 - 23 Feb 2025
Viewed by 289
Abstract
Mangroves grow in high-salinity environments with low soil water potential (Ψs), where high light intensity and strong winds increase the vapor pressure deficit (VPD), causing physiological drought and high transpiration demand (Δw), which limits carbon dioxide (carbon gain) for photosynthesis. This [...] Read more.
Mangroves grow in high-salinity environments with low soil water potential (Ψs), where high light intensity and strong winds increase the vapor pressure deficit (VPD), causing physiological drought and high transpiration demand (Δw), which limits carbon dioxide (carbon gain) for photosynthesis. This study explored how mangroves optimize their carbon-gain-to-water-loss ratio (water-use strategies) to maximize carbon gain during both dry and rainy seasons. We also calculated the relative costs of key leaf traits and compared them with those of terrestrial forests under the carbon gain optimization model. The results revealed that (1) with increasing Δw, terrestrial forests primarily adjusted leaf hydraulic conductance (Kleaf), while mangroves altered the difference in water potential (ΔΨ); (2) as Ψs decreased, πtlp of both terrestrial forests and mangroves increased; (3) terrestrial forests developed a more balanced distribution of leaf trait costs between osmotic pressure (46.7 ± 0.2%) and stomata (43.3 ± 1.2%), whereas mangroves had the highest cost in osmotic pressure (49.04 ± 0.03%) and the lowest cost in stomata (11.08 ± 3.00%) during the rainy season; and (4) although mangroves showed differences in trait values between dry and rainy seasons, their responses to drought stress remained consistent. These findings provided new theoretical insights into how mangroves maintain high carbon gain and water-use efficiency under extreme environmental conditions, which is important to improve mangrove conservation efforts and contribute to climate mitigation policies. Full article
(This article belongs to the Section Forest Ecophysiology and Biology)
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<p>Relationships of leaf photosynthetic traits with stomatal and hydraulic traits: (<b>a</b>) dependence of light-saturated CO<sub>2</sub> assimilation rate (A<sub>sat</sub>) on stomatal conductance (g<sub>sat</sub>); (<b>b</b>) dependence of A<sub>sat</sub> on leaf hydraulic conductance (K<sub>leaf</sub>); (<b>c</b>) dependence of g<sub>sat</sub> on K<sub>leaf</sub>; (<b>d</b>) influence of stem-to-leaf water potential difference (ΔΨ) on A<sub>sat</sub>; (<b>e</b>) influence of turgor loss point osmotic potential (π<sub>tlp</sub>) on A<sub>sat</sub>. Black circles represent species with complete A<sub>sat</sub>, g<sub>sat</sub>, K<sub>leaf</sub>, and π<sub>tlp</sub> data used for model fitting. Red circles represent species missing π<sub>tlp</sub> data. Lines represent predicted model trends. In (<b>d</b>), the solid line represents the linear line of best fit, and the dotted lines encompass the 95% confidence interval of the fit. Black: terrestrial forests; red: mangroves in the dry season; blue: mangroves in the rainy season (same throughout).</p>
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<p>Model-predicted impacts of atmospheric vapor pressure difference and source water potential on leaf-level adaptations for (<b>a</b>,<b>b</b>) light-saturated CO<sub>2</sub> assimilation (A<sub>sat</sub>) and (<b>c</b>,<b>d</b>) stomatal conductance (g<sub>sat</sub>). All of the model predictions used a photosynthetic capacity expected for a plant with an A<sub>sat</sub> of 15 μmol m<sup>−2</sup> s<sup>−1</sup> at Δw = 0.015 and Ψ<sub>s</sub> = 0 MPa. In (<b>a</b>,<b>c</b>), the dashed lines represent relationships predicted by the linearized Cowan–Farquhar stomatal optimization model.</p>
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<p>Model-predicted responses of leaf traits, including (<b>a</b>,<b>b</b>) leaf hydraulic conductance (K<sub>leaf</sub>), (<b>c</b>,<b>d</b>) turgor loss point osmotic potential (π<sub>tlp</sub>), and (<b>e</b>,<b>f</b>) stem-leaf water potential difference (ΔΨ), to (<b>a</b>,<b>c</b>,<b>e</b>) changes in vapor pressure difference (Δw) and (<b>b</b>,<b>d</b>,<b>f</b>) changes in source water potential (Ψ<sub>s</sub>). All of the model predictions used the photosynthetic capacity expected for a plant with an A<sub>sat</sub> of 15 μmol m<sup>−2</sup> s<sup>−1</sup> at Δw = 0.015 and Ψ<sub>s</sub> = 0 MPa.</p>
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<p>Proportions of the total cost for stomatal, hydraulic, and osmotic traits. The center line represents the median, the box represents the 25th–75th percentiles, the whiskers represent non-outlier extremes, and the plus signs represent outliers. The circles show the mean values, and the error bars indicate the standard deviation. Letters indicate significantly different groups based on the Kruskal–Wallis test and two-sided multiple comparisons. (For terrestrial forests, <span class="html-italic">n</span> = 16; hydraulic vs. stomatal: <span class="html-italic">p</span> = 4.5 × 10<sup>−4</sup>; hydraulic vs. osmotic: <span class="html-italic">p</span> = 1.1 × 10<sup>−8</sup>; stomatal vs. osmotic: not significant. For mangroves in the dry season, <span class="html-italic">n</span> = 6; hydraulic vs. stomatal: not significant; hydraulic vs. osmotic: not significant; stomatal vs. osmotic: <span class="html-italic">p</span> = 6.0 × 10<sup>−4</sup>. For mangroves in the rainy season, <span class="html-italic">n</span> = 7; hydraulic vs. stomatal: <span class="html-italic">p</span> = 4.2 × 10<sup>−2</sup>; hydraulic vs. osmotic: not significant; stomatal vs. osmotic: <span class="html-italic">p</span> = 3.0 × 10<sup>−4</sup>).</p>
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25 pages, 7154 KiB  
Article
Tourism-Induced Urbanization in Phuket Island, Thailand (1987–2024): A Spatiotemporal Analysis
by Sitthisak Moukomla and Wijitbusaba Marome
Urban Sci. 2025, 9(3), 55; https://doi.org/10.3390/urbansci9030055 - 20 Feb 2025
Viewed by 324
Abstract
Historically known for its tin mining industry, Phuket Island has undergone significant transformation into a global tourism hub. This study aims at analyzing the evolutionary dynamics of Phuket Island from the years 1987 to 2024. We integrate Landsat satellite images and sophisticated analytical [...] Read more.
Historically known for its tin mining industry, Phuket Island has undergone significant transformation into a global tourism hub. This study aims at analyzing the evolutionary dynamics of Phuket Island from the years 1987 to 2024. We integrate Landsat satellite images and sophisticated analytical methods to assess the effects of tourism and economic policies on changes in land use and land cover using Google Earth Engine (GEE) for cloud-based data processing and Random Forest (RF) models for classification, and the Urban Expansion Intensity Index (UEII) and Shannon Entropy metrics for measuring the intensity of urban expansion and diversity, respectively. The results show that there has been a dynamic change in the patterns of land use which was brought about by the economic and environmental forces. Some of the major events that have had a great effect on Phuket’s landscape include the 1997 Asian Financial Crisis, the 2004 Indian Ocean Tsunami, and the COVID-19 pandemic; this highlights how the island is fragile and can be affected easily by events happening around the world. This work reveals a dramatic reduction in forest and mangrove cover, which calls for increased conservation measures to prevent the loss of biodiversity and to preserve the natural balance. Full article
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<p>Thailand’s tourism industry’s resilience despite recurring disruptions from political, economic, and natural crises.</p>
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<p>Study area of Phuket, Thailand, showing the detailed coastal geography, tourist attractions, and its regional context.</p>
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<p>Number of scenes of Landsat images used in this study.</p>
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<p>General framework of the study illustrating the key methodological steps.</p>
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<p>Phuket LULC changes illustrated in spatial-temporal (<b>a</b>) and the changes in categories in Phuket over a span of years (<b>b</b>) from 1990 to 2024.</p>
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<p>Temporal variation in Phuket’s urban expansion.</p>
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<p>The urban landscape transformation underscores the critical need for strategic planning to address these challenges and ensure sustainable development for Phuket’s future.</p>
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<p>Correlation heatmap, revealing strong links between urban expansion, housing density, and economic indicators. (<b>a</b>) The relationship between urban growth, visitor numbers, and economic activity, highlighting long-term urbanization trends. (<b>b</b>) A strong alignment between actual and predicted urban expansion, confirming the model’s accuracy (<b>c</b>).</p>
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40 pages, 9921 KiB  
Article
Geoinformatics and Machine Learning for Shoreline Change Monitoring: A 35-Year Analysis of Coastal Erosion in the Upper Gulf of Thailand
by Chakrit Chawalit, Wuttichai Boonpook, Asamaporn Sitthi, Kritanai Torsri, Daroonwan Kamthonkiat, Yumin Tan, Apised Suwansaard and Attawut Nardkulpat
ISPRS Int. J. Geo-Inf. 2025, 14(2), 94; https://doi.org/10.3390/ijgi14020094 - 19 Feb 2025
Viewed by 605
Abstract
Coastal erosion is a critical environmental challenge in the Upper Gulf of Thailand, driven by both natural processes and human activities. This study analyzes 35 years (1988–2023) of shoreline changes using geoinformatics, machine learning algorithms (Random Forest, Support Vector Machine, Maximum Likelihood, Minimum [...] Read more.
Coastal erosion is a critical environmental challenge in the Upper Gulf of Thailand, driven by both natural processes and human activities. This study analyzes 35 years (1988–2023) of shoreline changes using geoinformatics, machine learning algorithms (Random Forest, Support Vector Machine, Maximum Likelihood, Minimum Distance), and the Digital Shoreline Analysis System (DSAS). The results show that the Random Forest algorithm, utilizing spectral bands and indices (NDVI, NDWI, MNDWI, SAVI), achieved the highest classification accuracy (98.17%) and a Kappa coefficient of 0.9432, enabling reliable delineation of land and water boundaries. The extracted annual shorelines were validated with high accuracy, yielding RMSE values of 13.59 m (2018) and 8.90 m (2023). The DSAS analysis identified significant spatial and temporal variations in shoreline erosion and accretion. Between 1988 and 2006, the most intense erosion occurred in regions 4 and 5, influenced by sea-level rise, strong monsoonal currents, and human activities. However, from 2006 to 2018, erosion rates declined significantly, attributed to coastal protection structures and mangrove restoration. The period 2018–2023 exhibited a combination of erosion and accretion, reflecting dynamic sediment transport processes and the impact of coastal management measures. Over time, erosion rates declined due to the implementation of protective structures (e.g., bamboo fences, rock revetments) and the natural expansion of mangrove forests. However, localized erosion remains persistent in low-lying, vulnerable areas, exacerbated by tidal forces, rising sea levels, and seasonal monsoons. Anthropogenic activities, including urban development, mangrove deforestation, and aquaculture expansion, continue to destabilize shorelines. The findings underscore the importance of sustainable coastal management strategies, such as mangrove restoration, soft engineering coastal protection, and integrated land-use planning. This study demonstrates the effectiveness of combining machine learning and geoinformatics for shoreline monitoring and provides valuable insights for coastal erosion mitigation and enhancing coastal resilience in the Upper Gulf of Thailand. Full article
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<p>Map of the study area in the Upper Gulf of Thailand which is divided into six regions based on physical characteristics.</p>
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<p>Workflow of the research methodology used for shoreline change analysis in the Upper Gulf of Thailand.</p>
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<p>Compare the performance of classification algorithms including Minimum Distance, Maximum Likelihood Classifier, Support Vector Machine, and Random Forest in overall accuracy and Cohen’s Kappa Coefficient.</p>
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<p>Classification results using four ML methods—Random Forest (<b>a</b>), Support Vector Machine (<b>b</b>), Maximum Likelihood Classifier (<b>c</b>), and Minimum Distance (<b>d</b>), for the Upper Gulf of Thailand. Each classification result illustrates the boundary between land and water in sample areas, including beach (<b>aA</b>,<b>bA</b>,<b>cA</b>,<b>dA</b>), mangrove forest (<b>aB</b>,<b>bB</b>,<b>cB</b>,<b>dB</b>), coastal fishing areas (<b>aC</b>,<b>bC</b>,<b>cC</b>,<b>dC</b>), shoreline protection structures (<b>aD</b>,<b>bD</b>,<b>cD</b>,<b>dD</b>), and steep cliffs (<b>aF</b>,<b>bF</b>,<b>cF</b>,<b>dF</b>).</p>
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<p>Overall accuracy and Cohen’s Kappa Coefficient for the Random Forest classification method applied to 65 satellite images from 1988 to 2023.</p>
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<p>Overlay of the extracted shorelines from seven time periods (1988, 1994, 2000, 2006, 2011, 2018, and 2023) in the Upper Gulf of Thailand. (<b>A</b>) represents shoreline changes at the Klong Yi San Kao estuary, (<b>B</b>) represents shoreline changes at Pak Thalenai, (<b>C</b>) represents shoreline changes at the mangrove area in Bang Krachao, (<b>E</b>) represents shoreline changes at Khun Samut Chin, and (<b>D</b>) represents shoreline changes at Khlong Nang Hong.</p>
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<p>Assessment of annual shoreline extraction compared to the reference shorelines in 2018 (<b>a</b>) and 2023 (<b>b</b>) in the Upper Gulf of Thailand. Shoreline locations in 2018: (<b>aA</b>) Hua Hin Beach, (<b>aB</b>) Chaosamran Beach, (<b>aC</b>) Pak Thale Nok, (<b>aD</b>) Bang Khun Thian, (<b>aE</b>) Bang Pu, (<b>aF</b>) Udom Bay, (<b>aG</b>) Na Chom Thian Beach, and (<b>aH</b>) Bang Sare. Shoreline locations in 2023: (<b>bA</b>) Hua Hin Beach, (<b>bB</b>) Chaosamran Beach, (<b>bC</b>) Bang Tabun estuary, (<b>bD</b>) Bang Khun Thian, (<b>bE</b>) Udom Bay, (<b>bF</b>) Jomtien Beach, (<b>bG</b>) Na Chom Thian Beach, and (<b>bH</b>) Bang Sare.</p>
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<p>Results of shoreline change analysis using the Digital Shoreline Analysis System (DSAS) for the Upper Gulf of Thailand.</p>
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<p>Trends in global mean sea level and average temperature, along with mean sea level, average temperature, and accumulated shoreline erosion in the Upper Gulf of Thailand.</p>
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<p>Correlation analyses between sea level, temperature, and coastal erosion: (<b>a</b>) Global mean sea level vs. global average temperature (<b>b</b>). Coastal erosion in the Upper Gulf of Thailand vs. global mean temperature (<b>c</b>). Coastal erosion in the Upper Gulf of Thailand vs. global mean sea level (<b>d</b>). Mean sea level vs. mean temperature in the Upper Gulf of Thailand (<b>e</b>). Coastal erosion vs. mean temperature in the Upper Gulf of Thailand (<b>e</b>), (<b>f</b>) Coastal erosion vs. mean sea level in the Upper Gulf of Thailand.</p>
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<p>Shoreline changes over six time periods from Hua Hin District to Laem Phak Bia region. (A) represents shoreline changes in the northern part of Cha-Am Beach, and (B) represents shoreline changes in Bang Kao Beach.</p>
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<p>Shoreline change analysis: sample of shoreline changes (<b>a</b>) over six time periods in Saphan Pla Cha-am (<b>c</b>), and sample of shoreline changes (<b>b</b>) over six time periods in the coastal area Bang Kao Subdistrict, Cha-am District, Phetchaburi (<b>d</b>).</p>
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<p>Shoreline changes over six time periods from Laem Phak Bia–Mae Klong River. (A) represents shoreline changes at the Klong Yi San Kao estuary, and (B) represents shoreline changes at Pak Thalenai.</p>
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<p>Shoreline change analysis: sample of shoreline changes (<b>a</b>) over six time periods in the coastal area between the Mae Klong estuary and the Khlong Bang Tabun estuary (<b>c</b>), and sample of shoreline changes (<b>b</b>) over six time periods in the coastal area Pak Thale Conservation Area, Pak Thale Subdistrict, Ban Laem District, Phetchaburi Province (<b>d</b>).</p>
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<p>Shoreline changes over six time periods from Mae Klong River to Tha Chin River. (A) represents shoreline changes at the mangrove area in Bang Krachao, and (B) represents shoreline changes at Ao Mahachai Mangrove Forest Study Centre.</p>
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<p>Shoreline change analysis: sample of shoreline changes (<b>a</b>) over six time periods in the coastal area Bang Phraek Subdistrict, Mueang District, Samut Sakhon Province (<b>c</b>), and a sample of shoreline changes (<b>b</b>) over six time periods in the coastal area Ao Mahachai Mangrove Forest Natural Education Center, Bang Phraek Subdistrict, Mueang District, Samut Sakhon Province (<b>d</b>).</p>
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<p>The shoreline changes over six time periods from Tha Chin River to Chao Phraya River. (A) represents shoreline changes at Khun Samut Chin, and (B) represents shoreline changes at the Tha Chin estuary.</p>
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<p>Shoreline change analysis: sample of shoreline changes (<b>a</b>) over six time periods in the coastal area Ban Khun Samut Chin, Laem Fa Pha Subdistrict, Phra Samut Chedi District, Samut Prakan Province (<b>c</b>), and sample of shoreline changes (<b>b</b>) over six time periods in the coastal area Marine and Coastal Resources Office, Samut Sakhon Mueang District, Samut Sakhon Province (<b>d</b>).</p>
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<p>Shoreline changes over six time periods from Chao Phraya River to Bang Pakong River. (A) represents shoreline changes at Khlong Nang Hong, and (B) represents shoreline changes at Bang Pu Mai.</p>
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<p>Shoreline change analysis: sample of shoreline changes (<b>a</b>) over six time periods in the coastal area Khlong Dan Subdistrict, Bang Bo District, Samut Prakan Province (<b>c</b>), and sample of shoreline changes (<b>b</b>) over six time periods in the coastal area Bang Pu Subdistrict, Mueang District, Samut Prakan Province (<b>d</b>).</p>
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<p>Shoreline changes over six time periods from Bang Pakong River to Sattahip District. (A) represents shoreline changes at the Bang Pakong estuary, and (B) represents shoreline changes at Laem Chabang Port.</p>
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<p>Shoreline change analysis: sample of shoreline changes (<b>a</b>) over six time periods in the coastal area Bang Pakong estuary, Khlong Tamhru Subdistrict, Mueang District, Chonburi Province (<b>c</b>), and sample of shoreline changes (<b>b</b>) over six time periods in Laem Chabang coastal area, Thung Sukhla Subdistrict, Sri Racha District, Chonburi Province (<b>d</b>).</p>
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16 pages, 4674 KiB  
Article
Wave Attenuation by Australian Temperate Mangroves
by Ruth Reef and Sabrina Sayers
J. Mar. Sci. Eng. 2025, 13(2), 382; https://doi.org/10.3390/jmse13020382 - 19 Feb 2025
Viewed by 249
Abstract
Wave attenuation by natural coastal features is recognised as a soft engineering approach to shoreline protection from storm surges and destructive waves. The effectiveness of wave energy dissipation is determined, in part, by vegetation structure, extent, and distribution. Mangroves line ca. 15% of [...] Read more.
Wave attenuation by natural coastal features is recognised as a soft engineering approach to shoreline protection from storm surges and destructive waves. The effectiveness of wave energy dissipation is determined, in part, by vegetation structure, extent, and distribution. Mangroves line ca. 15% of the world’s coastlines, primarily in tropical and subtropical regions but also extending into temperate climates, where mangroves are shorter and multi-stemmed. Using wave loggers deployed across mangrove and non-mangrove shorelines, we studied the wave attenuating capacity and the drag coefficient (CD) of temperate Avicennia marina mangrove forests of varying structure in Western Port, Australia. The structure of the vegetation obstructing the flow path was represented along each transect in a three-dimensional point cloud derived from overlapping uncrewed aerial vehicle (UAV) images and structure-from-motion (SfM) algorithms. The wave attenuation coefficient (b) calculated from a fitted exponential decay model at the vegetated sites was on average 0.011 m−1 relative to only 0.009 m−1 at the unvegetated site. We calculated a CD for this forest type that ranged between 2.7 and 4.9, which is within the range of other pencil-rooted species such as Sonneratia sp. but significantly lower than prop-rooted species such as Rhizophora spp. Wave attenuation efficiency significantly decreased with increasing water depth, highlighting the dominance of near-bed friction on attenuation in this forest type. The UAV-derived point cloud did not describe the vegetation (especially near-bed) in sufficient detail to accurately depict the obstacles. We found that a temperate mangrove greenbelt of just 100 m can decrease incoming wave heights by close to 70%, indicating that, similarly to tropical and subtropical forests, temperate mangroves significantly attenuate incoming wave energy under normal sea conditions. Full article
(This article belongs to the Section Coastal Engineering)
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<p>The bathymetry and geographical context of Western Port, Victoria. Red stars indicate the locations of wave–logger transects and the light green highlight is an estimation of mangrove cover [<a href="#B30-jmse-13-00382" class="html-bibr">30</a>]. Inset shows site location (red arrow) in Australia.</p>
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<p>(<b>Top</b>) The long-term average wind speeds from two weather stations in Western Port, showing the average wind speed and direction between June 1990 and August 2024 (Bureau of Meteorology). (<b>Bottom</b>) Map showing the location of the weather stations (black) and the sampling locations (red). Image of the seaward edge of the <span class="html-italic">Avicennia marina</span> mangrove forest at Stony Point. Scale bar is 1.5 m.</p>
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<p>UAV point cloud-derived bed slope and vegetation height distribution along the seaward &gt;&gt; landward transect at Stony Point (SP), the vegetated site at Pioneer Bay (PBV), Hastings, and the non-vegetated site at Pioneer Bay (PBNV). Black rectangles indicate the position of the loggers along the longest transect. The logger at 40 m indicates the appearance of pneumatophores in the vegetated sites.</p>
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<p>The change in significant wave height (Hs) over seaward &gt;&gt; landward distance at each site, as a percent of the incoming Hs (Hs<sub>0</sub>). Each line represents a time-independent 20 min average value (burst) collected during the high-tide slack period and is coloured differently. The black dashed line is the mean for each site. Logger 1 was the most seaward logger at 0 m. The dotted line at 40 m is the start of the vegetation at each site (Logger 2). Subsequent loggers were placed in 20 m intervals from this point landwards. Pioneer Bay (NV) is a non-vegetated site.</p>
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<p>The spread of attenuation coefficient value <span class="html-italic">b</span> from each individual burst period at each vegetated site. Larger <span class="html-italic">b</span> values indicate higher attenuation of incoming wave height. PBV indicates the mangrove site at Pioneer Bay and SP is the Stony Point vegetated site. Vertical dotted lines represent the mean.</p>
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<p>The effect of incoming significant wave period (<b>A</b>), incoming significant wave height (<b>B</b>), the number of aboveground points (<b>C</b>), wind speed (<b>D</b>), and incoming water depth (<b>E</b>), on wave attenuation coefficient <span class="html-italic">b</span> at the different sites. (<b>F</b>) A box plot of the landward distance from the start of the mangrove (Logger 2) at which significant wave height is reduced by 50%. Black points indicate outliers beyond 1.5 times the interquartile range. Please note that the attenuation coefficient derivation assumes that vegetation is the primary wave dissipation factor, thus <span class="html-italic">b</span> at the non-vegetated site should be interpreted with caution.</p>
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<p>Box plots of (<b>A</b>) the calculated dimensionless drag coefficient (C<sub>D</sub>) computed at each site from the reduction in wave height over distance (black points indicate outliers beyond 1.5 times the interquartile range) and (<b>B</b>) the number of subaqueous points counted across the 20 m wide and 100 m long wave logger transects at each site based on the UAV-derived point cloud and the depth during the burst.</p>
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20 pages, 4781 KiB  
Article
Seasonal Dynamics and Microenvironmental Drivers of Transpiration in Scrub Rhizophora mangle L. Trees from Yucatan
by Gabriela Cerón-Aguilera, Laura Yáñez-Espinosa, Ileana Echevarría-Machado, Rodrigo Méndez-Alonzo, Jorge Herrera-Silveira, Roberth Us-Santamaría, Julio Alberto Salas-Rabaza, Karina Elizabeth González-Muñoz and José Luis Andrade
Forests 2025, 16(2), 351; https://doi.org/10.3390/f16020351 - 15 Feb 2025
Viewed by 379
Abstract
Scrub mangrove forests, dominated by Rhizophora mangle L., are characterized by high porewater salinity, which might compromise individual sap flow rates (SF) due to seasonal and diurnal microenvironmental variations. We tested the functional, anatomical, and SF responses of 12 individuals to microenvironmental variables [...] Read more.
Scrub mangrove forests, dominated by Rhizophora mangle L., are characterized by high porewater salinity, which might compromise individual sap flow rates (SF) due to seasonal and diurnal microenvironmental variations. We tested the functional, anatomical, and SF responses of 12 individuals to microenvironmental variables such as solar radiation, photosynthetic photon flux, wind speed, evaporative demand, and porewater salinity, measured using an in situ weather station. Measurements were made in the dry and rainy seasons in the Yucatan Peninsula, using Granier heat dissipation sensors, installed on tree branches. During the rainy season, SF was twice as high as that during the dry season (0.22 ± 0.00 L h−1 and 0.11 ± 0.00 L h−1, respectively), despite lower evaporative demand. In both seasons, negative relationships between SF with vapor pressure deficit (VPD; dry τ = −0.54; rainy τ = −0.56) and with photosynthetic photon flux (PPF; dry τ = −0.97; rainy τ = −0.98) were found, indicating a strong hydraulic coupling to atmospheric conditions. Sap flow and transpiration rates of this R. mangle scrub mangrove forest exceeded those of some tropical dry deciduous forests, suggesting adaptations that support water transport in saline environments. The clustered xylem vessels of R. mangle ensure safe sap flow year-round. As an evergreen species, it contributes water to the atmosphere all year-round, underscoring its critical role in the tropical ecohydrological environment. Full article
(This article belongs to the Special Issue Water Relations in Tree Physiology)
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<p>Location of the study site is in the Celestun Biosphere Reserve. Yellow dots indicate the study site. Created with QGIS (3.22.14-Białowieża) [<a href="#B39-forests-16-00351" class="html-bibr">39</a>] (<b>A</b>). Scrub <span class="html-italic">R. mangle</span> trees (<b>B</b>), Granier’s sensor probes (heat dissipation method) placed in the tree branches (<b>C</b>).</p>
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<p>Diurnal mean patterns of sap flow (SF) measured over a continuous 8-day period during the dry and rainy seasons for <span class="html-italic">R. mangle</span> scrub mangroves. (<b>A</b>) Mean sap flow throughout a 24-h cycle. (<b>B</b>) Relative frequency of mean sap flow with a bimodal pattern in both seasons.</p>
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<p>Kendall correlation matrix for environmental and anatomical variables and Sap Flow (SF) during both seasons. (<b>A</b>) Dry season; (<b>B</b>) Rainy season. Variables include Sap Flow (SF), Vapor Pressure Deficit (VPD), Solar Radiation (SR), Photosynthetic Photon Flux (PPF), and Wind Speed (WS).</p>
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<p>Smooth effects of environmental variables on sap flow (SF) during dry seasons analyzed using Generalized Additive Models (GAM). (<b>A</b>) Effects of Vapor Pressure Deficit (VPD); (<b>B</b>) Photosynthetic Photon Flux (PPF); (<b>C</b>) solar radiation (SR); (<b>D</b>) wind speed (WS); (<b>E</b>) dew; and (<b>F</b>) porewater salinity.</p>
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<p>Smooth effects of environmental variables on sap flow (SF) during rainy season analyzed using Generalized Additive Models (GAM). (<b>A</b>) Effects of Vapor Pressure Deficit (VPD); (<b>B</b>) Photosynthetic Photon Flux (PPF); (<b>C</b>) solar radiation (SR); (<b>D</b>) wind speed (WS); and (<b>E</b>) porewater salinity.</p>
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<p>Stem secondary xylem: (<b>A</b>) transverse section showing diffuse porosity and vessel density, with a scale bar of 100 µm; (<b>B</b>) tangential section showing the scalariform perforation plate, scalariform intervascular pits of xylem vessels and wide xylem rays, with a scale bar of 50 µm; (<b>C</b>) radial sections showing detail of scalariform perforation plates overlapping at the tips of two vessel elements, with a scale bar of 10 µm; (<b>D</b>) dry season leaf transverse section showing epidermis, stomata, sub-stomatal chamber area (delimited by dotted line) and mesophyll parenchyma, with a scale bar of 100 µm. pp: perforation plates; f: fibers; ip: intervascular pits; ve: vessel elements; r: parenchymatous ray; sc: substomatal cavity; st: stomata; p: parenchyma.</p>
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16 pages, 3030 KiB  
Article
Shifts in Soil Fungal Community and Trophic Modes During Mangrove Ecosystem Restoration
by Xiaofang Shi, Shengyao Zhou, Lanzi Xu, Rajapakshalage Thashikala Nethmini, Yu Zhang, Liangliang Huang, Ke Dong, Huaxian Zhao and Lianghao Pan
J. Fungi 2025, 11(2), 146; https://doi.org/10.3390/jof11020146 - 14 Feb 2025
Viewed by 357
Abstract
Mangrove ecosystems are valuable coastal ecosystems; however, studies on the diversity and functional features of their soil fungal communities during restoration are limited. In this study, we examined fungal diversity and trophic modes across mudflat, young mangrove, and mature mangrove stages. We found [...] Read more.
Mangrove ecosystems are valuable coastal ecosystems; however, studies on the diversity and functional features of their soil fungal communities during restoration are limited. In this study, we examined fungal diversity and trophic modes across mudflat, young mangrove, and mature mangrove stages. We found that Ascomycota and Basidiomycota were the dominant phyla, with saprotrophs as the most abundant trophic mode. The abundance of the major phyla and trophic modes significantly varied across restoration stages. Although fungal alpha (α)-diversity remained stable among the stages, beta (β)-diversity showed significant differentiation. Spearman’s analysis and partial Mantel tests revealed that total nitrogen and inorganic phosphorus significantly influenced the fungal α-diversity, whereas temperature and pH primarily shaped the fungal β-diversity. Total nitrogen and carbon were key factors affecting the trophic mode α-diversity, whereas total phosphorus and inorganic phosphorus were the main drivers of the trophic mode β-diversity. Variation partitioning analysis confirmed that nutrients, rather than soil properties, were the primary factors shaping fungal communities and trophic modes. Random forest analysis identified key bioindicators, including species such as Paraphyton cookei, and trophic modes such as saprotrophs, both of which were strongly influenced by soil carbon. These findings advance our understanding of fungal ecology in mangrove restoration. Full article
(This article belongs to the Special Issue Fungal Communities in Various Environments)
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<p>Alpha (α)- and beta (β)-diversities across the three restoration stages. (<b>A</b>) α-diversity (richness and Shannon index), with the median indicated by a horizontal line. (<b>B</b>) Non-metric multidimensional scaling (NMDS) plot based on the Bray–Curtis dissimilarity of fungal communities, wherein gray lines represent the within-group variability. MF: mudflat; YM: young mangrove; MM: mature mangrove.</p>
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<p>Relative abundance distribution of fungal trophic modes across different stages of mangrove restoration in this study.</p>
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<p>Pairwise correlations between environmental factors (top right) and partial Mantel tests for fungal communities and trophic modes with each environmental factor. TN: total nitrogen; TC: total carbon; TOC: total organic carbon; TIC: total inorganic carbon; TP: total phosphorus; PO<sub>4</sub><sup>3</sup>⁻: dissolved phosphate; Pi: inorganic phosphorus; Po: organic phosphorus.</p>
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<p>Variation partitioning analysis of the effects of soil properties (water content, salinity, pH, and temperature) and nutrients (TN, TC, TOC, TIC, TP, PO<sub>4</sub><sup>3</sup>⁻, Pi, Po, NH<sub>4</sub><sup>+</sup>-N, NO<sub>3</sub><sup>−</sup>-N, and NO<sub>2</sub><sup>−</sup>-N) in the fungal community (<b>A</b>) and trophic mode composition (<b>B</b>).</p>
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<p>Bioindicators of fungal species in different mangrove restoration stages. <b>Left</b>: Gini rank of the bioindicator species, representing their importance level; <b>Middle</b>: Relative abundances of the bioindicator species; <b>Right</b>: Spearman’s correlations between the relative abundances of the species and environmental and nutrient factors. The asterisk indicates the significance level: *, <span class="html-italic">p</span> &lt; 0.05; **, <span class="html-italic">p</span> &lt; 0.01; ***, <span class="html-italic">p</span> &lt; 0.001.</p>
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<p>Bioindicators of fungal trophic modes in different mangrove restoration stages. <b>Left</b>: Gini rank of the bioindicator trophic modes, representing their importance level; <b>Middle</b>: relative abundances of the bioindicator trophic modes; <b>Right</b>: Spearman’s correlations between the relative abundances of the trophic modes and environmental and nutrient factors. The asterisk indicates the significance level: *, <span class="html-italic">p</span> &lt; 0.05; **, <span class="html-italic">p</span> &lt; 0.01; ***, <span class="html-italic">p</span> &lt; 0.001.</p>
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14 pages, 5594 KiB  
Article
Nature Meets Infrastructure: The Role of Mangroves in Strengthening Bangladesh’s Coastal Flood Defenses
by Alejandra Gijón Mancheño, Bramka A. Jafino, Bas Hofland, Bregje K. van Wesenbeeck, Swarna Kazi and Ignacio Urrutia
Sustainability 2025, 17(4), 1567; https://doi.org/10.3390/su17041567 - 13 Feb 2025
Viewed by 787
Abstract
Mangroves have been used for coastal protection in Bangladesh since the 1960s, but their integration with embankment designs has not been fully explored. This paper investigates the effect of existing mangroves on required embankment performance, with a focus on the wave-damping effect of [...] Read more.
Mangroves have been used for coastal protection in Bangladesh since the 1960s, but their integration with embankment designs has not been fully explored. This paper investigates the effect of existing mangroves on required embankment performance, with a focus on the wave-damping effect of mangroves. Existing mangroves reduce the required thickness of embankment revetment by up to 16–30% in the west, 47–82% in the central region, and 53–77% in the east. Notable mangrove sites include the belt south of polder 45 (Amtali), with an average width of 1.77 km, and the Kukri-Mukri polder, with an average width of 1.82 km. These mangroves reduce the need for thick slope protection, allowing the replacement of concrete revetments with softer materials, such as clay or grass, combined with mangrove foreshore. Additional large mangrove belts are found in Sandwip and Mirersarai. By replacing or reducing revetment requirements, mangrove forests can minimize carbon emissions from construction while providing carbon sequestration and other ecosystem services. This study can inform future sustainable investments in coastal protection systems by identifying areas where mangroves offer the greatest wave-damping benefits, which could be focus of follow-up feasibility studies. Full article
(This article belongs to the Section Environmental Sustainability and Applications)
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<p>Location of existing mangroves on the waterside of embankments (light green polygons) in Bangladesh at the west, center, and east regions. Basemap by Google Earth (2024).</p>
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<p>Histograms of mangrove forest belt width for the (<b>a</b>) west, (<b>b</b>) center and (<b>c</b>) east regions. The x-axis represents forest (cross-shore) width in meters, grouped in increments of 50 m, while the y-axis indicates the number of observations in each bin. Blue vertical lines mark the mean forest length, and black vertical lines indicate the median forest width for each region. The histograms highlight the distribution and central tendencies of forest width across the three regions.</p>
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<p>Wave transmission through mangrove belts (%) at (<b>a</b>) west, (<b>b</b>) center, and (<b>c</b>) east of Bangladesh. Blue areas show the range of wave reduction estimates for each belt width, based on the minimum and maximum values of <a href="#sustainability-17-01567-t001" class="html-table">Table 1</a>. Gray areas show the available belt widths in the region, the black dashed line marks a belt width of 100 m, and the orange line indicates the average belt width.</p>
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<p>Effect of mangrove afforestation in the west, center, and east of Bangladesh, in terms of (<b>a</b>,<b>d</b>,<b>g</b>) crest height reduction, (<b>b</b>,<b>e</b>,<b>h</b>) reduction in the revetment thickness, (<b>c</b>,<b>f</b>,<b>i</b>) and reduction in the shear stresses. Blue areas show the range of wave reduction estimates for each belt width, based on the minimum and maximum values of <a href="#sustainability-17-01567-t001" class="html-table">Table 1</a>. Gray areas show the available belt widths in the region, the black dashed line marks a belt width of 100 m and the orange line indicates the average belt width.</p>
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<p>Potential revetment reduction in Bangladesh (%), corresponding with the upper values of wide mangrove belts that could reduce embankment design requirements in Bangladesh in <a href="#sustainability-17-01567-f004" class="html-fig">Figure 4</a>, with close-ups of the mangrove belts of (<b>a</b>) Shamnagar (polder 7/1), (<b>b</b>) Shymnagar (polder 15), (<b>c</b>) Amtali (polder 45), (<b>d</b>) Kukri-Mukri, (<b>e</b>) Mirersarai (polder 61/2), (<b>f</b>) Boro Moheshkhali (polder 69). Basemaps by Google Earth (2024).</p>
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20 pages, 4669 KiB  
Article
Monitoring Mangrove Phenology Based on Gap Filling and Spatiotemporal Fusion: An Optimized Mangrove Phenology Extraction Approach (OMPEA)
by Yu Hong, Runfa Zhou, Jinfu Liu, Xiang Que, Bo Chen, Ke Chen, Zhongsheng He and Guanmin Huang
Remote Sens. 2025, 17(3), 549; https://doi.org/10.3390/rs17030549 - 6 Feb 2025
Viewed by 517
Abstract
Monitoring mangrove phenology requires frequent, high-resolution remote sensing data, yet satellite imagery often suffers from coarse resolution and cloud interference. Traditional methods, such as denoising and spatiotemporal fusion, faced limitations: denoising algorithms usually enhance temporal resolution without improving spatial quality, while spatiotemporal fusion [...] Read more.
Monitoring mangrove phenology requires frequent, high-resolution remote sensing data, yet satellite imagery often suffers from coarse resolution and cloud interference. Traditional methods, such as denoising and spatiotemporal fusion, faced limitations: denoising algorithms usually enhance temporal resolution without improving spatial quality, while spatiotemporal fusion models struggle with prolonged data gaps and heavy noise. This study proposes an optimized mangrove phenology extraction approach (OMPEA), which integrates Landsat and MODIS data with a denoising algorithm (e.g., Gap Filling and Savitzky–Golay filtering, GF–SG) and a spatiotemporal fusion model (e.g., Enhanced Spatial and Temporal Adaptive Reflectance Fusion Model, ESTARFM). The key of OMPEA is that GF–SG algorithm filled data gaps from cloud cover and satellite transit gaps, providing high-quality input to ESTARFM and improving its accuracy of NDVI imagery reconstruction in mangrove phenology extraction. By conducting experiments on the GEE platform, OMPEA generates 1-day, 30 m NDVI imagery, from which phenological parameters (i.e., the start (SoS), end (EoS), length (LoS), and peak (PoS) of the growing season) are derived using the maximum separation (MS) method. Validation in four mangrove areas along the coastal China shows that OMPEA significantly improves the potential to capture mangrove phenology in the presence of incomplete data. The OMPEA significantly increased usable data, adding 7–33 Landsat images and 318–415 MODIS images per region. The generated NDVI series exhibits strong spatiotemporal consistency with original data (R2: 0.788–0.998, RMSE: 0.007–0.253) and revealed earlier SoS and longer LoS at lower latitudes. Cross-correlation analysis showed a 2–3 month lagged effects of temperature on mangroves’ growth, with precipitation having minimal impact. The proposed OMPEA improves the possibility of capturing mangrove phenology under non-continuous and low-resolution data, providing valuable insights for large-scale and long-term mangrove conservation and management. Full article
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<p>Map of study area: (<b>a</b>) the overall distribution of study area; (<b>b1</b>–<b>b4</b>) Zhangjiangkou National Mangrove Nature Reserve (ZNR) in Fujian Province, Qi’ao Island Provincial Nature Reserve (QPR) in Guangdong Province, Beilun Estuary National Nature Reserve (BNR) in Guangxi Province, and Dongzhaigang National Mangrove Nature Reserve (DNR) in Hainan Province.</p>
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<p>Workflow of mangrove phenology extraction based on OMPEA.</p>
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<p>Landsat 8 NDVI (16-day 30 m) and denoised Landsat NDVI (16-day 30 m) generated by OMPEA. Gray pixel indicates pixel with no data.</p>
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<p>MODIS NDVI (1-day 500 m) and denoised MODIS NDVI (1-day 30 m) generated by OMPEA. Gray pixel indicates pixel with no data.</p>
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<p>The OMPEA-generated fused NDVI imagery. Gray pixel indicates pixel with no data.</p>
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<p>Scatter density plots and marginal histograms of fused NDVI and denoised Landsat NDVI.</p>
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<p>Composite scatter plots and line plots of various NDVI time series.</p>
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<p>Fused NDVI time-series curve and phenological parameters.</p>
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<p>Boxplots of mangrove phenological parameters.</p>
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<p>The time-series curves for fused NDVI, precipitation, temperature, and their lagged time-series curves with corresponding lag days.</p>
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<p>The OMPEA-generated fused NDVI in QPR from 17 January 2020 to 24 March 2021. (<b>a</b>) Description of denoised Landsat 8 NDVI in a full-time range. (<b>b</b>) Description of denoised Landsat 8 NDVI across three different time ranges, (<b>c</b>,<b>d</b>) is fused NDVI that using (<b>a</b>,<b>b</b>) as inputs, respectively. Gray pixel indicates pixel with no data.</p>
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18 pages, 4301 KiB  
Article
Metabolic Activity of Invasive Apple Snails Negatively Affects the Survival of Native Benthic Snail in Mangrove
by Jinling Liu, Caiying Zhang, Huixiu Yu, Zixin Fu, Huizhen Xie, Yiming Wang, Benliang Zhao, Qing Li, Kailin Kuang and Huanting Lin
Biology 2025, 14(2), 141; https://doi.org/10.3390/biology14020141 - 29 Jan 2025
Viewed by 724
Abstract
The golden apple snail (GAS, Pomacea canaliculata) has invaded mangrove forests. The effect of water contaminated by metabolic activity of GAS feeding on Acanthus ilicifolius (T1), Sonneratia apetala (T2), and without food (CK) on the native mangrove black helmet snail (BHS, Neritina [...] Read more.
The golden apple snail (GAS, Pomacea canaliculata) has invaded mangrove forests. The effect of water contaminated by metabolic activity of GAS feeding on Acanthus ilicifolius (T1), Sonneratia apetala (T2), and without food (CK) on the native mangrove black helmet snail (BHS, Neritina pulligera) was investigated under salinity conditions. The GAS deteriorated saline water quality (2.5‰). DO contents in T1 and T2 approached zero at 9 d. Compared to CK, the contents of COD, total N, NH4+, NO3, and total P of the contaminated water in T1 increased by 297%, 205%, 262%, 210%, and 518% after 9 d, while these indicators in T2 increased by 74%, 31%, 57%, 326%, and 154%, respectively. The LC50 of the contaminated water in T1 against the BHS reached 22.72%. The weight of the BHS exposed to the 100% contaminated water in T1 and T2 significantly decreased after exposure. The content of GPT of the BHS exposed to the 100%-contaminated water in T1 and T2 increased by 55% and 26%, while the MDA content increased by 38% and 34%. The 100%-contaminated water in T1 led to cell degeneration and incomplete structure in the hepatopancreas tissue of the BHS. The GAS feeding on holly mangroves can compete against native mangrove snails through water deterioration. Full article
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<p>Changes in pH of water contaminated by metabolic activity of golden apple snail (GAS, <span class="html-italic">Pomacea canaliculata</span>) under different feeding conditions. Note: CK—no feeding; T1—water contaminated by metabolic activity of GAS feeding on <span class="html-italic">Acanthus ilicifolius</span>; T2—water contaminated by metabolic activity of GAS feeding on <span class="html-italic">Sonneratia apetala</span>. Values with different lowercase letters are significantly different between T1, T2 and CK at <span class="html-italic">p</span> &lt; 0.01 or 0.05. Two asterisks indicated a significant difference in values of T1, T2 and CK between 9 d and 1 d at <span class="html-italic">p</span> &lt; 0.01.</p>
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<p>Changes in dissolved oxygen (DO, (<b>I</b>)) and chemical oxygen demand (COD, (<b>II</b>)) of water contaminated by metabolic activity of golden apple snail (GAS, <span class="html-italic">Pomacea canaliculata</span>) in T1, T2 and CK. Note: CK—no feeding; T1—water contaminated by metabolic activity of GAS feeding on <span class="html-italic">Acanthus ilicifolius</span>; T2—water contaminated by metabolic activity of GAS feeding on <span class="html-italic">Sonneratia apetala</span>. Values with different lowercase letters are significantly different between T1, T2 and CK at <span class="html-italic">p</span> &lt; 0.01 or 0.05. Two asterisks indicated a significant difference in values of T1, T2 and CK between 9 d and 1 d at <span class="html-italic">p</span> &lt; 0.01.</p>
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<p>Changes in NH<sub>4</sub><sup>+</sup> (<b>I</b>), TN (<b>II</b>), NO<sub>3</sub><sup>−</sup> (<b>III</b>), and TP (<b>IV</b>) of water contaminated by metabolic activity of of golden apple snail (GAS, <span class="html-italic">Pomacea canaliculata</span>) in T1, T2 and CK. Note: CK—no feeding; T1—water contaminated by metabolic activity of GAS feeding on <span class="html-italic">Acanthus ilicifolius</span>; T2—water contaminated by metabolic activity of GAS feeding on <span class="html-italic">Sonneratia apetala</span>. Values with different lowercase letters are significantly different between T1, T2 and CK at <span class="html-italic">p</span> &lt; 0.01 or 0.05. Two asterisks indicated a significant difference in values of T1, T2 and CK between 9 d and 1 d at <span class="html-italic">p</span> &lt; 0.01.</p>
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<p>Mortality of black helmet snails exposed to water contaminated by metabolic activity of golden apple snail (GAS, <span class="html-italic">Pomacea canaliculata</span>) in water contaminated by metabolic activity of GAS feeding on <span class="html-italic">Acanthus ilicifolius</span> (<b>I</b>), water contaminated by metabolic activity of GAS feeding on <span class="html-italic">Sonneratia apetala</span> (<b>II</b>), and no feeding (<b>III</b>). Note: For 100% of the original solution of the contaminated water; 75%—diluted to 75% of the original solution; 50%—diluted to 50% of the original solution; 25%—diluted to 25% of the original solution; 0—2.5‰ saline solution. Values with different lowercase letters are significantly different at <span class="html-italic">p</span> &lt; 0.01 or 0.05. One or two asterisks indicated a significant difference in values of five gradients between 9 d and 1 d at <span class="html-italic">p</span> &lt; 0.05 or 0.01.</p>
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<p>Protein (<b>I</b>), GOT (<b>II</b>), GPT (<b>III</b>), and MDA (<b>IV</b>) content of black helmet snails (BHS) exposed to different gradients of T1, T2, and CK. Note: CK—no feeding; T1—water contaminated by metabolic activity of GAS feeding on <span class="html-italic">Acanthus ilicifolius</span>; T2—water contaminated by metabolic activity of GAS feeding on <span class="html-italic">Sonneratia apetala</span>. For 100% the original solution of the contaminated water; 75%—diluted to 75% of the original solution; 50%—diluted to 50% of the original solution; 25%—diluted to 25% of the original solution; 0—2.5‰ saline solution. Foot was used to determine protein content. Hepatopancreas was used to determine GOT, GPT, and MDA content. Values with different lowercase letters are significantly different between CK, T1, and T2 at the same concentration at <span class="html-italic">p</span> &lt; 0.01 or 0.05. Values with different uppercase letters are significantly different between five gradients at <span class="html-italic">p</span> &lt; 0.01 or 0.05.</p>
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<p>Change of hepatopancreas structure of black helmet snails exposed to water contaminated by metabolic activity of golden apple snail (GAS, <span class="html-italic">Pomacea canaliculata</span>). note: (<b>I</b>)—25% water contaminated by metabolic activity of GAS fed <span class="html-italic">Acanthus ilicifolius</span> (T1); (<b>II</b>)—50% water contaminated by metabolic activity of GAS fed <span class="html-italic">Sonneratia apetala</span> (T2); (<b>III</b>)—100% water contaminated by metabolic activity of GAS without feeding (CK). dc: digestive cell; dv: digestive vacuole; bm: basal membrane; ct: connective tissue; tl: tubule lumen.</p>
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<p>Change of hepatopancreas structure of black helmet snails exposed to water contaminated by metabolic activity of golden apple snail (GAS, <span class="html-italic">Pomacea canaliculata</span>). note: (<b>I</b>)—25% water contaminated by metabolic activity of GAS fed <span class="html-italic">Acanthus ilicifolius</span> (T1); (<b>II</b>)—50% water contaminated by metabolic activity of GAS fed <span class="html-italic">Sonneratia apetala</span> (T2); (<b>III</b>)—100% water contaminated by metabolic activity of GAS without feeding (CK). dc: digestive cell; dv: digestive vacuole; bm: basal membrane; ct: connective tissue; tl: tubule lumen.</p>
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<p>Change of hepatopancreas structure of black helmet snails exposed to water contaminated by metabolic activity of golden apple snail (GAS, <span class="html-italic">Pomacea canaliculata</span>). note: (<b>I</b>)—25% water contaminated by metabolic activity of GAS fed <span class="html-italic">Acanthus ilicifolius</span> (T1); (<b>II</b>)—50% water contaminated by metabolic activity of GAS fed <span class="html-italic">Sonneratia apetala</span> (T2); (<b>III</b>)—100% water contaminated by metabolic activity of GAS without feeding (CK). dc: digestive cell; dv: digestive vacuole; bm: basal membrane; ct: connective tissue; tl: tubule lumen.</p>
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20 pages, 11052 KiB  
Article
Remote Sensing-Based Assessment of the Long-Term Expansion of Shrimp Ponds Along the Coastal and Protected Areas of the Gulf of California
by David A. González-Rivas, Alfredo Ortega-Rubio and Felipe-Omar Tapia-Silva
Diversity 2025, 17(2), 99; https://doi.org/10.3390/d17020099 - 29 Jan 2025
Viewed by 611
Abstract
Shrimp farming has expanded over coastal areas in Mexico, particularly in the protected regions of Sonora and Sinaloa. Over the past 30 years, the economic activity associated with these farms has grown so much that the amount of shrimp produced in these ponds [...] Read more.
Shrimp farming has expanded over coastal areas in Mexico, particularly in the protected regions of Sonora and Sinaloa. Over the past 30 years, the economic activity associated with these farms has grown so much that the amount of shrimp produced in these ponds now exceeds that harvested from traditional shrimp fisheries. Establishing shrimp ponds has led to significant land changes. The construction of these ponds has fragmented local ecosystems, resulting in permanent alterations to areas such as floodplains, mangrove forests, and dunes, many of which are protected zones. This study aimed to investigate the long-term growth of shrimp farms from 1993 to 2022 and their impact on land-use changes in surrounding ecosystems, focusing on protected areas in the Sinaloa and Sonora coastal regions. We analyzed Landsat images using the Google Earth Engine platform. Our findings indicate that shrimp farm development over the past three decades has been extensive, with protected areas experiencing fragmentation and changes. Remote sensing and platforms like Google Earth Engine enable the effective monitoring of these spatiotemporal changes and their impacts, helping to identify the most affected areas. Full article
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<p>Study area. The numbers in the boxes represent the order in which we present the results for the Ramsar sites or Biosphere Reserves where we analyzed pond expansion. Boxes 1 to 3 do not cover the entire protected area, as we focus solely on the sections that contain shrimp ponds. The figure provides a close-up view of the pond areas surrounding the Biosphere Reserve Cajón del Diablo.</p>
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<p>Expansion of the shrimp pond area from 1993 to 2022 along the Gulf of California. The plot shows bars with the total area in Ha per year of the ponds in the region and overall accuracy bars in %.</p>
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<p>The long-term expansion of the shrimp ponds in the Biosphere Reserve Marismas Nacionales. The arrows indicate the locations of the new ponds constructed in the indicated year.</p>
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<p>The long-term expansion of shrimp ponds in the Biosphere Reserve Cajón del Diablo. The arrows indicate the locations of the new ponds constructed in the indicated year.</p>
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<p>The long-term expansion of shrimp ponds in the Complejo Lagunar Bahía Guásimas–Estero Lobos. The arrows indicate the locations of the new ponds constructed in the indicated year.</p>
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<p>The long-term expansion of shrimp ponds within the sites of Sistema Lagunar Agiabampo–Bacorehuis–Rio Fuerte Antiguo, Lagunas de Santa María–Topolobampo–Ohuira, and Sistema Lagunar San Ignacio–Navachiste–Macapule. The arrows indicate the locations of the new ponds constructed in the indicated year.</p>
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<p>The long-term expansion of shrimp ponds within the sites Laguna Playa Colorada Santa Maria Reforma and Ensenada Pabellones. The arrows indicate the locations of the new ponds constructed in the indicated year.</p>
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17 pages, 4032 KiB  
Article
The Geometry of Southern China’s Mangroves: Small and Elongated
by Lin Zhang, Yijuan Deng, Wenqing Wang and Mao Wang
Forests 2025, 16(2), 212; https://doi.org/10.3390/f16020212 - 23 Jan 2025
Viewed by 527
Abstract
Mangrove wetlands are naturally divided into habitat patches by tidal creeks, with patch edges highly vulnerable to human activities and biological invasions, making them critical areas for mangrove degradation. Understanding the geometrical characteristics of these patches is essential for mangrove management in the [...] Read more.
Mangrove wetlands are naturally divided into habitat patches by tidal creeks, with patch edges highly vulnerable to human activities and biological invasions, making them critical areas for mangrove degradation. Understanding the geometrical characteristics of these patches is essential for mangrove management in the Anthropocene, yet their exploration remains limited. Using a high-resolution (2 m) mangrove distribution dataset from 2018, we analyzed the patch structure of mangroves in southern China. This study revealed predominantly small and elongated patches, with an average area of 0.044 km2 and a median of 0.011 km2 across 5857 patches. About 65% of patches had a major-axis length over twice their minor-axis length. The patch number and area peaked between 19° N and 22° N. The patch number and area peaked between 19° N and 22° N. In the 0.1° × 0.1° latitudinal-longitudinal grid, the maximum mangrove area was 9.03 km2, consisting of 192 patches. Additionally, the patch composition and geometric characteristics differed significantly among the existing reserves. These findings highlight the need to prioritize the patch geometry in management strategies, especially in regions with numerous small patches prone to degradation and invasion. Additionally, this study underscores a critical research gap: the ecological impacts of mangrove fragmentation on biodiversity and ecosystem services remain poorly understood. Future research should focus on how the patch structure and landscape configuration influence ecological processes in mangrove wetlands. Full article
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<p>Spatial distribution of mangroves along the southern coast of China in 2018. (<b>a</b>) A map illustrates the spatial distribution of mangroves. (<b>b</b>) Graph depicting the variation in mangrove area and the number of patches, summarized across 0.1° latitudinal intervals.</p>
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<p>Distribution patterns of mangrove area at patch scale and local aggregation scale. (<b>a</b>) Relationship between patch area and rank order of patch area; the inset in the upper right displays the original distribution of patch areas, while the subplot in the lower left shows the distribution after log-transformation. Notes on the number of patches (N), mean, and median are included. (<b>b</b>) Relationship between the number of connected groups and the distance threshold, with a red mark indicating the distance threshold of 9 km chosen for this study, which resulted in 105 connected groups; the histogram in the upper right displays the distribution of areas for these 105 connected groups. (<b>c</b>) Map illustrating the largest connected group among the 105 identified groups, annotated with patch number and total area. A map with pentagram marks its geographical location.</p>
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<p>Frequency distribution histograms of the nine geometric metrics used in this study. Each panel displays the histogram for a specific metric with the mean and median values indicated inside. All metrics were calculated across the 5857 patches included in the analysis.</p>
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<p>Comparison of geometric metrics across five selected national nature reserves or internationally important wetlands. (<b>a</b>) Locations of the five selected sites. (<b>b</b>) The relationship between the total mangrove area and number of patches in each reserve. (<b>c</b>) Differences in 10 metrics among the five sites. Different letters denote significant differences at the 0.05 level, based on a non-parametric test. The error bars represent one standard deviation. ZJE: Zhangjiang Estuary Mangrove National Nature Reserve; SZB: Shenzhen Bay Mangrove Wetland; SK: Shankou Mangrove National Nature Reserve; BLE: Beilun Estuary National Nature Reserve; DZG: Dongzhaigang Bay Mangrove National Nature Reserve.</p>
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<p>Correlations between all ten geometric metrics. Colors and numbers represent the corresponding Pearson correlation coefficients. An “×” indicates that the correlation is not significantly different from zero at the <span class="html-italic">p</span> &lt; 0.05 significance level. For definitions of each shape metric, refer to <a href="#forests-16-00212-t001" class="html-table">Table 1</a>.</p>
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<p>Relationship between patch area and geometric metrics. (<b>a</b>) Perimeter versus patch area. The blue solid line added via the “geom_smooth” function represents the smoothed trend, while the red solid line illustrates the theoretical relationship between perimeter and area for circles. (<b>b</b>) The inverse of elongation (1/elongation) versus patch area. The top right inset in panel (<b>b</b>) features a satellite image from Google Earth of the patch with the smallest elongation value, highlighting its elongated shape.</p>
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<p>Geographic patterns of mangrove geometry characteristics. (<b>a</b>) Variation in mangrove area with latitude. (<b>b</b>) Variation in mangrove patch number with latitude. (<b>c</b>) Map of mangrove area distribution. (<b>d</b>) Map of mangrove patch number distribution. (<b>e</b>) Distribution map of average 1/Elongation. Insets in the top-right corners of Panels (<b>a</b>,<b>b</b>) displaying satellite images from Google Earth showing the mangrove landscapes with the largest area and the highest number of patches, respectively. Panels (<b>a</b>,<b>b</b>) are summarized using a 0.1° by 0.1° latitude–longitude grid, while Panels (<b>c</b>–<b>e</b>) use a 0.5° by 0.5° latitude–longitude grid for mapping purposes.</p>
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<p>Non-metric Multidimensional Scaling (NMDS) plot illustrating the variation of all mangrove patches. (<b>a</b>) A 2D hexagonal heatmap of bin counts, used to show the true distribution where many data points overlap. (<b>b</b>) Envfit analysis results overlaid on the NMDS ordination plot. Arrows represent geometric metrics, with their direction indicating the gradient of influence and their length reflecting the strength of correlation with the ordination axes.</p>
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29 pages, 9654 KiB  
Article
Construction of Multi-Scale Fusion Attention Unified Perceptual Parsing Networks for Semantic Segmentation of Mangrove Remote Sensing Images
by Xin Wang, Yu Zhang, Wenquan Xu, Hanxi Wang, Jingye Cai, Qin Qin, Qin Wang and Jing Zeng
Appl. Sci. 2025, 15(2), 976; https://doi.org/10.3390/app15020976 - 20 Jan 2025
Viewed by 544
Abstract
Mangrove forests play a crucial role in coastal ecosystem protection and carbon sequestration processes. However, monitoring remains challenging due to the forests’ complex spatial distribution characteristics. This study addresses three key challenges in mangrove monitoring: limited high-quality datasets, the complex spatial characteristics of [...] Read more.
Mangrove forests play a crucial role in coastal ecosystem protection and carbon sequestration processes. However, monitoring remains challenging due to the forests’ complex spatial distribution characteristics. This study addresses three key challenges in mangrove monitoring: limited high-quality datasets, the complex spatial characteristics of mangrove distribution, and technical difficulties in high-resolution image processing. To address these challenges, we present two main contributions. (1) Using multi-source high-resolution satellite imagery from China’s new generation of Earth observation satellites, we constructed the Mangrove Semantic Segmentation Dataset of Beihai, Guangxi (MSSDBG); (2) We propose a novel Multi-scale Fusion Attention Unified Perceptual Network (MFA-UperNet) for precise mangrove segmentation. This network integrates Cascade Pyramid Fusion Modules, a Multi-scale Selective Kernel Attention Module, and an Auxiliary Edge Neck to process the unique characteristics of mangrove remote sensing images, particularly addressing issues of scale variation, complex backgrounds, and boundary accuracy. The experimental results demonstrate that our approach achieved a mean Intersection over Union (mIoU) of 94.54% and a mean Pixel Accuracy (mPA) of 97.14% on the MSSDBG dataset, significantly outperforming existing methods. This study provides valuable tools and methods for monitoring and protecting mangrove ecosystems, contributing to the preservation of these critical coastal environments. Full article
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<p>Several challenges in mangrove remote sensing image semantic segmentation.</p>
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<p>The geographic location of the study area. (<b>A</b>) The coastal area of Beihai City, Guangxi, China. (<b>B</b>) The study area (a. Coastal National Wetland Park of Beihai, Guangxi, and Hengluoshan area of Yinhai District, Beihai, Guangxi; b. Dugong and Shankou National Nature Reserve area of Hepu, Guangxi; c. the coastal area of Lianzhou Bay of Hepu, Beihai, Guangxi; and d. the coastal area of Maowei Sea and Dafeng River, Guangxi).</p>
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<p>Examples of Original Remote Sensing Images and Their Corresponding Annotation Results.</p>
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<p>Schematic diagram of the original and cropped images.</p>
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<p>Overall MFA-UperNet Network Structure (<b>A</b>. Feature Encoder, <b>B</b>. Auxiliary Edge Neck, <b>C</b>. Semantic Decoder).</p>
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<p>Overall Structure Diagram of ConvNeXt Feature Encoder.</p>
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<p>Overall Structure Diagram of MFA-UperNet Semantic Decoder.</p>
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<p>ECA Channel Attention Module Structure.</p>
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<p>Structure Diagram of LSK Module.</p>
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<p>A plot of the segmentation results of different models on the MSSDBG dataset. (White boxes are used to highlight the differences in the results under different methods.)</p>
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<p>Plot of Loss and Accuracy.</p>
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<p>ConvNeXt Improvement and Effectiveness Comparison Chart.</p>
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<p>The segmentation result graph of the different modules superimposed on the MRSDBG dataset. (White boxes are used to highlight the differences in the results under different methods.)</p>
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12 pages, 5552 KiB  
Article
Field Investigation of Wave Attenuation in a Mangrove Forest Dominated by Avicennia marina (Forsk.) Viern.
by Xing Wei, Wenyuan Mo, Lanlan Xiong, Xin Hu and Hao Cheng
Plants 2025, 14(1), 135; https://doi.org/10.3390/plants14010135 - 5 Jan 2025
Viewed by 771
Abstract
Based on field observation at the north coast of the Zhanjiang Bay in southern China, the characteristics of wave attenuation due to the drag force of one mangrove species, Avicennia marina (Forsk.) Viern., were quantitatively analyzed. The results demonstrated that the mean significant [...] Read more.
Based on field observation at the north coast of the Zhanjiang Bay in southern China, the characteristics of wave attenuation due to the drag force of one mangrove species, Avicennia marina (Forsk.) Viern., were quantitatively analyzed. The results demonstrated that the mean significant wave height decreased by ~62% within a forest belt up to 80 m due to various bio-physical interactions. Affected by the unique vertical configuration of vegetation, the wave attenuation rate is positively correlated with water depth. The drag force within the forest can be approximated by the function Cd=0.7344e0.1409Am, where Am is the projected area of the submerged obstacle at a certain water depth. The wave attenuation rate and the vegetation density (ρveg) in volume (‰) satisfy the fitting relationship of r=5×104·ρveg3.6×103. These findings can accumulate quantitative information for studying the influence of mangrove vegetation on wave attenuation characteristics and provide necessary basic data for modeling studies to investigate the processes contributing to the attenuation capacity of mangroves. Full article
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<p>(<b>A</b>) Schematic map of the Leizhou Peninsula and its location in relation to China. (<b>B</b>) The geomorphology of Zhanjiang Bay and the relative location of the study area. (<b>C</b>) Location of hydrological observation sites in the study area. (<b>D</b>) Elevation with respect to mean sea level (MSL) of the cross-shore transect including instrument positions. The vegetation zone and mudflat on the transect are demarcated by dashed line. Plot location for the vegetation survey is shown on the horizontal coordinate. Tidal water levels are indicated at the right axis (MHWL, mean highwater level; MLWL, mean low water level).</p>
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<p>(<b>A</b>) Characteristic of <span class="html-italic">Avicennia marina</span> (Forsk.) Viern. in the study area. (<b>B</b>) Variation in horizontal vegetation cover with elevation above the forest floor.</p>
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<p>The water depth (solid lines) and wave height (dotted lines) at the outermost station P1 during the observation period.</p>
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<p>Average wave energy density spectra of wave data during full inundation of the cross-shore transect.</p>
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<p>Wave parameter conditions along the transect. (<b>A</b>) Significant wave heights H<sub>x</sub> (m); (<b>B</b>) mean wave periods Tm (s); and (<b>C</b>) total wave energy Em (J/m<sup>2</sup>).</p>
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<p>Variation in wave reduction (<b>A</b>) and drag coefficient (<b>B</b>) with water depth.</p>
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<p>The relationship between the projected area of the obstacle per meter width and the drag coefficient.</p>
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<p>The correlation between the attenuation rate of wave height and the density of volumetric vegetation in a certain height above the forest surface. <span class="html-italic">ρ</span><sub>0.05</sub>, <span class="html-italic">ρ</span><sub>0.5</sub>, <span class="html-italic">ρ</span><sub>1.0</sub> and <span class="html-italic">ρ</span><sub>1.5</sub> denote the horizontal volumetric density of submerged vegetation at water depths of 0.05 m, 0.5 m, 1 m and 1.5 m, respectively.</p>
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25 pages, 7818 KiB  
Article
Geographic Distribution Patterns of Soil Microbial Community Assembly Process in Mangrove Constructed Wetlands, Southeast China
by Ping Hu and Qiong Yang
Diversity 2025, 17(1), 21; https://doi.org/10.3390/d17010021 - 28 Dec 2024
Viewed by 536
Abstract
Constructed wetlands, as an emerging wastewater treatment system, have been widely used worldwide due to their high purification efficiency and low investment and operating costs. Wetland plants, on the other hand, together with their inter-root microbes, significantly affect the ecological functions of constructed [...] Read more.
Constructed wetlands, as an emerging wastewater treatment system, have been widely used worldwide due to their high purification efficiency and low investment and operating costs. Wetland plants, on the other hand, together with their inter-root microbes, significantly affect the ecological functions of constructed wetlands. The mangrove constructed wetland within Futian District, Shenzhen, China, is a typical wastewater treatment area, but the structure and function of its soil microbial community remain largely unexplored. In this study, the assembly and processes of the soil microbial communities in this constructed wetland were intensively investigated using high-throughput sequencing technology. Our results showed that the three mangrove plants had significant effects on the soil bacterial microbial community α-diversity, insignificant effects on β-diversity, and significant effects on fungal α-diversity and β-diversity. The abundance of genera changed significantly between the treatment groups, such as the genus Candidatus_Udaeobacter for bacteria versus Russula for fungi, and the random forest model showed that rare genera (e.g., Acidibacter, Dyella, Sebacina, and Lachnellula) also play an important role in microbial community construction. Community assembly revealed the deterministic process of soil bacterial and fungal communities under different mangrove species. Overall, this study enhanced our understanding of soil microbial community composition and diversity in constructed wetlands ecosystems, providing insights into their manageability. Full article
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<p>Principal component analysis (PCA) of soil bacterial (<b>a</b>) and fungal (<b>b</b>) communities across different plant types. Dots of different colors represent different plant types. The <span class="html-italic">p</span>-values are used to assess whether the observed differences are merely due to random variations. SC: <span class="html-italic">Sonneratia caseolaris</span> treatment; AC: <span class="html-italic">Aegiceras corniculatum</span> treatment; KC: <span class="html-italic">Kandelia candel</span> treatment.</p>
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<p>Variance distributions of soil bacterial (<b>a</b>) and fungal (<b>b</b>) communities under three different treatments (SC, AC, and KC) based on significance levels from Monte Carlo permutation tests. Different colors represent distinct treatment conditions. The overlapping areas depict the common bacterial and fungal OTUs (operational taxonomic units) across different treatments. The non-overlapping areas indicate bacterial and fungal OTUs specific to each treatment condition. The numbers represent the counts of bacterial and fungal OTUs under various treatment conditions. SC: <span class="html-italic">Sonneratia caseolaris</span> treatment; AC: <span class="html-italic">Aegiceras corniculatum</span> treatment; KC: <span class="html-italic">Kandelia candel</span> treatment. The blue part represents the number of bacteria contained in group AC alone, the green part represents the number of bacteria contained in group SC alone, and the pink part represents the number of bacteria contained in group KC alone.</p>
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<p>Stacked bar charts representing the top 10 abundant soil bacterial genera (<b>a</b>) and soil fungal genera (<b>b</b>) under different treatments. SC: <span class="html-italic">Sonneratia caseolaris</span> treatment; AC: <span class="html-italic">Aegiceras corniculatum</span> treatment; KC: <span class="html-italic">Kandelia candel</span> treatment.</p>
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<p>Kruskal–Wallis tests for differences among treatments to examine variations in soil bacterial genera (<b>a</b>) and soil fungal genera (<b>b</b>) between treatments. Bar graphs of different colors represent distinct treatments. SC: <span class="html-italic">Sonneratia caseolaris</span> treatment; AC: <span class="html-italic">Aegiceras corniculatum</span> treatment; KC: <span class="html-italic">Kandelia candel</span> treatment. * indicates that the genus is significant among different treatments.</p>
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<p>The random forest classification model visually demonstrates the dominant bacterial genera (<b>a</b>) and fungal genera (<b>b</b>) under different treatments. The random forest variables derived from the classification algorithm highlight the importance of rare genera in predicting different plant types. Green bars represent variables selected using the classification algorithm. Asterisks indicate significant differences. SC: <span class="html-italic">Sonneratia caseolaris</span> treatment; AC: <span class="html-italic">Aegiceras corniculatum</span> treatment; KC: <span class="html-italic">Kandelia candel</span> treatment.</p>
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<p>Circos visualization of the top 10 genera of soil bacteria (<b>a</b>) and soil fungi (<b>b</b>) across different plant types. The width of the lines represents the abundance. There are five circles from outer to inner. The first circle indicates information on different genera and plant type treatments. The second circle displays information on the percentage of relative abundance of each OTU within the total OTUs. The third circle represents the main OTU blocks. The fourth circle shows the OTU sub-blocks, which correspond to the main blocks (third circle), illustrating the abundance of OTUs in each sample and information on the abundance of each OTU included in each treatment. The fifth circle displays the connections between the OTUs and the related information across different treatments corresponding to the fourth circle. SC: <span class="html-italic">Sonneratia caseolaris</span> treatment; AC: <span class="html-italic">Aegiceras corniculatum</span> treatment; KC: <span class="html-italic">Kandelia candel</span> treatment.</p>
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<p>Circular tree diagram of LEfSe (linear discriminant analysis effect size) for discriminating differences between groups in soil bacteria (<b>a</b>) and fungi (<b>b</b>). Different colors represent different groups. Nodes of different colors in the branches indicate microbial taxa that play significant roles in the corresponding group of that color, while yellow nodes represent microbial taxa that do not play significant roles. The species names denoted by English letters are shown in the legend on the right. If the colors are consistent in the diagram, it indicates that no significant marker was found.</p>
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<p>Correlation analysis between soil bacterial (<b>a</b>) and soil fungal (<b>b</b>) genera and environmental factors across different plant types. * indicates significance at the 0.05 level; ** indicates significance at the 0.01 level; *** indicates significance at the 0.001 level. The color gradient (from red to blue) represents the correlation strength from high to low. Red indicates a positive correlation, while blue indicates a negative correlation.</p>
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<p>Redundancy analysis between soil bacterial (<b>a</b>) and soil fungal (<b>b</b>) communities and environmental factors under different plant types. The samples and environmental factors are reflected on the same two-dimensional ordination plot, allowing for an intuitive visualization of the relationships between sample distribution and environmental factors. SC: <span class="html-italic">Sonneratia caseolaris</span> treatment; AC: <span class="html-italic">Aegiceras corniculatum</span> treatment; KC: <span class="html-italic">Kandelia candel</span> treatment.</p>
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<p>Fitting of soil bacterial ((<b>a</b>): SC, (<b>b</b>): AC, (<b>c</b>): KC) and fungal ((<b>d</b>): SC, (<b>e</b>): AC, (<b>f</b>): KC) communities across different plant types using the Neutral Community Model (NCM). R<sup>2</sup> represents the goodness of fit of the model. Nm: The product of metacommunity size (N) and migration rate (m) (Nm = N × m), which quantitatively estimates the degree of dispersal among communities and determines the correlation between occurrence frequency and relative abundance across regions. The blue solid line best fits the Neutral Community Model (NCM), and the blue dashed lines represent the 95% confidence interval predicted by the NCM. OTUs within this confidence interval (black dots) are considered to be neutrally distributed. SC: <span class="html-italic">Sonneratia caseolaris</span> treatment; AC: <span class="html-italic">Aegiceras corniculatum</span> treatment; KC: <span class="html-italic">Kandelia candel</span> treatment. The solid blue line is the best fit to the neutral community model (NCM), and the dashed blue line indicates 95% confidence intervals around the NCM prediction, and the OTUs within the confidence intervals (black dots) are viewed as neutrally distributed.</p>
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