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Search Results (1,028)

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19 pages, 9717 KiB  
Article
Piping Plover Habitat Changes and Nesting Responses Following Post-Tropical Cyclone Fiona on Prince Edward Island, Canada
by Ryan Guild and Xiuquan Wang
Remote Sens. 2024, 16(24), 4764; https://doi.org/10.3390/rs16244764 (registering DOI) - 20 Dec 2024
Abstract
Climate change is driving regime shifts across ecosystems, exposing species to novel challenges of extreme weather, altered disturbances, food web disruptions, and habitat loss. For disturbance-dependent species like the endangered piping plover (Charadrius melodus), these shifts present both opportunities and risks. [...] Read more.
Climate change is driving regime shifts across ecosystems, exposing species to novel challenges of extreme weather, altered disturbances, food web disruptions, and habitat loss. For disturbance-dependent species like the endangered piping plover (Charadrius melodus), these shifts present both opportunities and risks. While most piping plover populations show net growth following storm-driven habitat creation, similar gains have not been documented in the Eastern Canadian breeding unit. In September 2022, post-tropical cyclone Fiona caused record coastal changes in this region, prompting our study of population and nesting responses within the central subunit of Prince Edward Island (PEI). Using satellite imagery and machine learning tools, we mapped storm-induced change in open sand habitat on PEI and compared nest outcomes across habitat conditions from 2020 to 2023. Open sand areas increased by 9–12 months post-storm, primarily through landward beach expansion. However, the following breeding season showed no change in abundance, minimal use of new habitats, and mixed nest success. Across study years, backshore zones, pure sand habitats, and sandspits/sandbars had lower apparent nest success, while washover zones, sparsely vegetated areas, and wider beaches had higher success. Following PTC Fiona, nest success on terminal spits declined sharply, dropping from 45–55% of nests hatched in pre-storm years to just 5%, partly due to increased flooding. This suggests reduced suitability, possibly from storm-induced changes to beach elevation or slope. Further analyses incorporating geomorphological and ecological data are needed to determine whether the availability of suitable habitat is limiting population growth. These findings highlight the importance of conserving and replicating critical habitat features to support piping plover recovery in vulnerable areas. Full article
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<p>Map of all nesting sites on PEI with breeding activity since 2011.</p>
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<p>Classified landcover pre-storm (A) and 1-year post-storm (B) and total change in open sand area (C) over critical barrier island habitats for PIPL on PEI. Counts of breeding pairs (BP) and fledglings (FL) from each site indicated by light and dark blue bars, respectively. Black circle on the island map indicates nesting site with no data (ND).</p>
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<p>Classified landcover pre-storm (A) and post-storm (B) and total change in open sand area (C) over critical sandspit/bar habitats for PIPL on PEI. Counts of breeding pairs (BP) and fledglings (FL) from each site indicated by light and dark blue bars, respectively. Black circles on the island map indicate nesting sites with no data (ND). Additional classified sandspit/bar nesting sites are displayed in <a href="#app1-remotesensing-16-04764" class="html-app">Figure S3</a>.</p>
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<p>Classified landcover pre-storm (A) and 1-year post-storm (B) and total change in open sand area (C) over critical mainland beach habitats for PIPL on PEI. Counts of breeding pairs (BP) and fledglings (FL) from each site indicated by light and dark blue bars, respectively. Black circles on the island map indicate nesting sites with no data (ND).</p>
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<p>Nest locations and outcomes during three breeding seasons preceding (top three panels) and the initial season following (fourth panel) PTC Fiona over Conway Sandhills, PEI. Classified change in dry and wet sand area after one-year post-storm depicted in bottom panel, with colours representing change classes (in <a href="#remotesensing-16-04764-f002" class="html-fig">Figure 2</a>, <a href="#remotesensing-16-04764-f003" class="html-fig">Figure 3</a> and <a href="#remotesensing-16-04764-f004" class="html-fig">Figure 4</a>).</p>
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<p>Fledging rate across common nesting sites with at least three years of nesting attempts between 2020 and 2023. Horizontal line at 1.65 fledglings/pair indicates ECCC productivity target for the Eastern Canadian recovery unit. Vertical line distinguishes between pre- and post-storm breeding seasons.</p>
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<p>Model-averaged coefficient estimates (log-odds scale) from the top-ranked logistic regression GLMs of binary hatch success (<b>left</b>) and data summaries of hatch outcomes across habitat metrics from 2020–2023 on PEI (<b>right</b>). Number in white indicates nest counts in each respective category; error bars in GLM output display 95% confidence intervals (SE * 1.96). D2 ACCESS is represented as a categorical and continuous variable to convey complimentary insights.</p>
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<p>Summaries of binary hatch success by year across habitat measures on PEI from 2020–2023. Number in white indicates the number of nests in each respective category. D2 ACCESS is represented as a categorical and continuous variable to convey complimentary insights.</p>
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<p>Model averaged coefficient estimates (log-odds scale) from the top-ranked logistic regression GLMs of flooding and predation occurrences (<b>left</b>) and data summaries of nest outcomes across habitat metrics from 2020–2023 on PEI (<b>right</b>). Error bars in GLM output display 95% confidence intervals (SE * 1.96). D2 ACCESS is represented as a categorical and continuous variable to convey complimentary insights.</p>
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22 pages, 11599 KiB  
Article
A New Surface Waters Downscaling Approach Applicable at Global Scale
by Thu-Hang Nguyen and Filipe Aires
Remote Sens. 2024, 16(24), 4664; https://doi.org/10.3390/rs16244664 - 13 Dec 2024
Viewed by 324
Abstract
A surface water extent downscaling framework was developed in the past using a floodability index based on topography. We presented here a new downscaling approach including several improvements. (1) The use of a new Floodability Index (FI), including better integration of auxiliary permanent [...] Read more.
A surface water extent downscaling framework was developed in the past using a floodability index based on topography. We presented here a new downscaling approach including several improvements. (1) The use of a new Floodability Index (FI), including better integration of auxiliary permanent waters (i.e., presence of water during the whole time record). By using this updated FI, the new downscaling became a true data-fusion with permanent water databases originating mainly from visible observations. (2) Some discontinuities between low resolution cells have been reduced thanks to a new smoothing algorithm. (3) Finally, a coastal extrapolation scheme has been presented to deal with coarse resolution data contaminated by the ocean. This new and complex downscaling framework was tested here on the GIEMS (Global Inundation Extent from Multi-Satellite) database but the approach is generalizable and any surface water database could be used instead. It was shown that this new downscaling procedure (including several processing steps, algorithms and data sources) is a significant improvement compared to the previous version thanks to the new floodability index and the downscaling processing chain. Compared to the previous version, the downscaling results (GIEMS-D) were more coherent with the permanent water database and preserved better the original low-resolution information (e.g., mean scare error water fraction (0–1) of 0.0041 for the old version, and 0.0018 for the new version, over flooded areas in the Amazon). GIEMS-D has also been evaluated at the global scale and over the Amazon basin using independent datasets, showing an overall good performance of the downscaling. Full article
(This article belongs to the Special Issue Advances of Remote Sensing and GIS Technology in Surface Water Bodies)
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Figure 1
<p>Overall scheme of the downscaling framework. The several steps will be described in detail in the following sections.</p>
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<p>The HR permanent water information from the floodability index (top left) is used to downscale the permanent part of the LR data. <span class="html-italic">First, HR (binary) permanent water is upscaled to fractions in each LR cell. Then, if the LR inundation fraction is lower than the permanent water fraction (<math display="inline"><semantics> <mrow> <mi>L</mi> <mi>R</mi> <mo>≤</mo> <mi>L</mi> <msub> <mi>R</mi> <mrow> <mi>p</mi> <mi>e</mi> <mi>r</mi> <mi>m</mi> </mrow> </msub> </mrow> </semantics></math>), the transitory water fraction <math display="inline"><semantics> <mrow> <mi>L</mi> <msub> <mi>R</mi> <mrow> <mi>t</mi> <mi>r</mi> <mi>a</mi> <mi>n</mi> <mi>s</mi> </mrow> </msub> </mrow> </semantics></math> is set to zero, otherwise the permanent water fraction is subtracted from LR value (<math display="inline"><semantics> <mrow> <mi>L</mi> <msub> <mi>R</mi> <mrow> <mi>t</mi> <mi>r</mi> <mi>a</mi> <mi>n</mi> <mi>s</mi> </mrow> </msub> <mo>=</mo> <mi>L</mi> <mi>R</mi> <mo>−</mo> <mi>L</mi> <msub> <mi>R</mi> <mrow> <mi>p</mi> <mi>e</mi> <mi>r</mi> <mi>m</mi> </mrow> </msub> </mrow> </semantics></math>). HR permanent water is projected in the downscaling map, and it is the <math display="inline"><semantics> <mrow> <mi>L</mi> <msub> <mi>R</mi> <mrow> <mi>t</mi> <mi>r</mi> <mi>a</mi> <mi>n</mi> <mi>s</mi> </mrow> </msub> </mrow> </semantics></math> that will be allocated to HR transitory pixels based on the floodability index.</span></p>
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<p>Sketch representing the parameters in eq:smoothCoeff for the smoothing process.</p>
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<p>Downscaling with/without the smoothing procedure. Top-left: LR data to be downscaled. Top-right: floodability index. Bottom-left: downscaled data with edge effects as no smoothing procedure is used. Bottom right: edge effects have been removed thanks to the smoothing procedure.</p>
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<p>Coastal extrapolation scheme. (<b>a</b>) Process: From the HR water allocation at the Land-frontiers of the coastal cell (cell with bold black border), a threshold of floodability index <span class="html-italic">T</span> is defined for each Land-frontier, then a threshold <span class="html-italic">t</span> is derived for each HR pixel in the coastal cell. A pixel with floodability index higher than its threshold <span class="html-italic">t</span> is set to water. (<b>b</b>) Order in which coastal cells are extrapolated (from blue to red): The cells that have more contact with Land cells are extrapolated first. The cells processed first can then be used to extrapolate the following coastal cells.</p>
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<p>Downscaling of on single month (12/1994) over the Democratic Republic of the Congo and the Republic of the Congo: (<b>a</b>,<b>d</b>) GIEMS is corrected by GLWD in the previous version and by permanent water integrated in the floodability index in the new version (<span class="html-italic">Corrected GIEMS = max(GIEMS, reference permanent water fraction)</span>); (<b>b</b>,<b>e</b>) downscaling results; (<b>c</b>,<b>f</b>) upscaling of the HR results; (<b>g</b>) Google Earth extraction for this region. <math display="inline"><semantics> <msub> <mi>MSE</mi> <mrow> <mi>c</mi> <mo>,</mo> <mi>a</mi> </mrow> </msub> </semantics></math> = 0.0041 and <math display="inline"><semantics> <msub> <mi>MSE</mi> <mrow> <mi>d</mi> <mo>,</mo> <mi>f</mi> </mrow> </msub> </semantics></math> = 0.0018 over the whole site. <math display="inline"><semantics> <msub> <mi>MSE</mi> <mrow> <mi>c</mi> <mo>,</mo> <mi>a</mi> </mrow> </msub> </semantics></math> = 0.0084 and <math display="inline"><semantics> <msub> <mi>MSE</mi> <mrow> <mi>d</mi> <mo>,</mo> <mi>f</mi> </mrow> </msub> </semantics></math> = 0.0031 over flooded areas.</p>
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<p>Water occurrence from the downscaling of GIEMS around the Sagara Lake using (<b>a</b>) the old version versus, and (<b>b</b>) the new version. (<b>c</b>) GSWO from optical observations at 30 m resolution [<a href="#B20-remotesensing-16-04664" class="html-bibr">20</a>]. (<b>d</b>) Google satellite image.</p>
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<p>Water occurrence global map from GIEMS-D (<b>top</b>) and GSWO (<b>bottom</b>).</p>
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<p>Distribution of GIEMS-D versus GSWO occurrence (%) over all land covers and over some surface types. With higher vegetation, more samples can be seen in the upper-left part sections, meaning more water for the GIEMS-D estimates.</p>
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<p>Correlation between GIEMS-D water extent and GSIM river discharge over 2293 basins. The distribution of correlation coefficient is shown on the bottom left corner. Four locations (A, B, C, D) are selected to look into details in <a href="#remotesensing-16-04664-f011" class="html-fig">Figure 11</a>.</p>
Full article ">Figure 11
<p>Comparison of GIEMS-D and GSW water extent with GSIM river discharge over 4 basins. Left column: data accumulated over each basin. Central column: data averaged for each month of the year, representing seasonality. Right column: difference of monthly values against corresponding seasonality values, normalized by standard deviation of the whole time series. GSW values are amplified 10 times for better visualization. Numbers floating in the plots are correlation coefficients of water extent (blue for GIEMS-D, green for GSW) and river discharge.</p>
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<p>Comparison of GIEMS-D and SAR [<a href="#B23-remotesensing-16-04664" class="html-bibr">23</a>] in dry (<b>left</b>) and wet (<b>right</b>) states. Two zooms are provided over regions A and B. Google images are given to show the density of vegetation and the challenge to detect surface waters.</p>
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<p>Comparison of water occurrence from GIEMS-D (<b>a</b>), GSWO (<b>b</b>), and SAR (<b>c</b>), over the Amazon (−8° to 0° in latitude; and −66° to −54° in longitude).</p>
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27 pages, 13040 KiB  
Article
Digital Prototyping and Regenerative Design Toward Carbon-Neutrality and a Climate Resilient Built Environment: A Multi-Scale Assessment of Environmental Multi-Risks
by Domenico Lucanto, Consuelo Nava and Giuseppe Mangano
Buildings 2024, 14(12), 3934; https://doi.org/10.3390/buildings14123934 - 10 Dec 2024
Viewed by 640
Abstract
This study addresses the urgent need to move the construction sector toward carbon neutrality and climate resilience, by considering the increasingly intense impacts of climate change. The research aims to evaluate the application of advanced digital prototyping tools and regenerative design principles to [...] Read more.
This study addresses the urgent need to move the construction sector toward carbon neutrality and climate resilience, by considering the increasingly intense impacts of climate change. The research aims to evaluate the application of advanced digital prototyping tools and regenerative design principles to identify environmental risks at different scales, with a particular focus on cultural and natural heritage. The hypothesis is that the integration of climate data and predictive models with regenerative design can overcome existing barriers to sustainable practices and significantly enhance the adaptive capacity of the built environment, particularly in safeguarding cultural and natural heritage against the multi-hazard impacts of climate change. To test this hypothesis, an experimental study is conducted using a combination of climate data, advanced modeling and regenerative design tools to assess and manage multi-hazard impacts on cultural and natural heritage. Two case studies were analyzed: Palizzi Marina, a coastal town vulnerable to sea level rise and flooding, and Palazzo Mesiani in Bova, a historic building exposed to increased solar radiation and temperatures. This type of analysis has enabled a comprehensive multi-scenario and multi-hazard assessment that offers a detailed overview of the risks to be considered in the design phase. In conclusion, the research underscores the importance of interdisciplinary approaches and emerging technologies in resilient design frameworks. By integrating climate data and predictive models with regenerative design methodologies, this study can significantly contribute to enhancing the adaptive capacity of the built environment. This approach aids in the transition of the construction sector toward sustainability and climate resilience, particularly in protecting cultural and natural heritage. Full article
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<p>Climate change-oriented design workflow.</p>
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<p>Map of the Grecanica Area.</p>
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<p>(<b>Left</b>) highlighted map of the historical centre of Bova; (<b>Right</b>) highlighted map of Palizzi M.</p>
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<p>Methodological framework for the climate change-oriented design workflow.</p>
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<p>Drone survey process.</p>
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<p>Refined digital prototype of Palazzo Mesiani.</p>
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<p>First integrated map for the digital prototype of Palizzi Marina.</p>
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<p>Global temperature projections under RCP 4.5 and RCP 8.5 scenarios with key years. Elaboration on IPCC data by D. Lucanto.</p>
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<p>Irradiance graph of the Grecanica Area for different scenarios under RCP 4.5 and RCP 8.5.</p>
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<p>Enthalpy (SX) and humidity (DX) graphs of the Grecanica Area for different scenarios under RCP 4.5 and RCP 8.5.</p>
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<p>Cooling deg. days (SX) and heating deg. days (DX) graphs of the Grecanica Area for different scenarios under RCP 4.5 and RCP 8.5.</p>
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<p>Digital prototype of Palizzi Marina coastline data for SLR scenario analysis.</p>
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<p>SLR projections current trajectory (RCP 4.5, medium luck): 2050, 2080, 2100.</p>
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<p>SLR projections unchecked pollution (RCP 8.5, medium luck): 2050, 2080, 2100.</p>
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<p>SLR projections current trajectory (RCP 4.5, bad luck): 2050, 2080, 2100.</p>
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<p>SLR projections unchecked pollution (RCP 8.5, bad luck): 2050, 2080, 2100.</p>
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<p>Simulation on Palizzi Marina using Kangaroo Physics.</p>
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<p>Simulation results identifying key flood-prone areas in Palizzi Marina during intense rainfall events.</p>
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<p>Inc.radiation maps of Bova for RCP 4.5 climate change scenarios.</p>
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<p>Inc.radiation maps of Bova for different climate change scenarios.</p>
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<p>Analysis of direct sunlight hours on Palazzo Mesiani. (<b>Top left</b>): spring; (<b>top right</b>): summer; (<b>bottom left</b>): autumn; (<b>bottom right</b>): winter.</p>
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<p>Incident radiation on Palazzo Mesiani—current scenario. (<b>Top left</b>): spring; (<b>top right</b>): summer; (<b>bottom left</b>): autumn; (<b>bottom right</b>): winter.</p>
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<p>Radiation incident—2030 scenario—RCP 4.5. (<b>Top left</b>): spring; (<b>top right</b>): summer; (<b>bottom left</b>): autumn; (<b>bottom right</b>): winter.</p>
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<p>Radiation incident—2050 scenario—RCP 8.5. (<b>Top left</b>): spring; (<b>top right</b>): summer; (<b>bottom left</b>): autumn; (<b>bottom right</b>): winter.</p>
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<p>Radiation incident—2085 scenario—RCP 8.5. (<b>Top left</b>): spring; (<b>top right</b>): summer; (<b>bottom left</b>): autumn; (<b>bottom right</b>): winter.</p>
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<p>Radiation incident—2090 scenario—RCP 4. (<b>Top left</b>): spring; (<b>top right</b>): summer; (<b>bottom left</b>): autumn; (<b>bottom right</b>): winter.</p>
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<p>Image of the 3D-printed physical prototype of Bova.</p>
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<p>Image of the 3D-printed physical prototype of Palizzi Marina.</p>
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23 pages, 5438 KiB  
Article
The Impacts of an Artificial Sandbar on Wave Transformation and Runup over a Nourished Beach
by Cuiping Kuang, Liyuan Chen, Xuejian Han, Dan Wang, Deping Cao and Qingping Zou
Geosciences 2024, 14(12), 337; https://doi.org/10.3390/geosciences14120337 - 8 Dec 2024
Viewed by 567
Abstract
Due to increasing coastal flooding and erosion in changing climate and rising sea level, there is a growing need for coastal protection and ecological restoration. Artificial sandbars have become popular green coastal infrastructure to protect coasts from these natural hazards. To assess the [...] Read more.
Due to increasing coastal flooding and erosion in changing climate and rising sea level, there is a growing need for coastal protection and ecological restoration. Artificial sandbars have become popular green coastal infrastructure to protect coasts from these natural hazards. To assess the effect of an artificial sandbar on wave transformation over a beach under normal and storm wave conditions, a high-resolution non-hydrostatic model based on XBeach is established at the laboratory scale. Under normal wave conditions, wave energy is mainly concentrated in short wave frequency bands. The wave setup is negligible on the shoreface but becomes more significant over the beach face, and wave nonlinearity increases with decreasing water depth. The artificial sandbar reduces the wave setup by 22% and causes considerable changes in wave skewness, wave asymmetry, and flow velocity. Under storm wave conditions, as the incident wave height increases, the wave energy in the long wave frequency bands rises, while it decreases in the short wave frequency bands. The wave dissipation coefficient of an artificial sandbar increases first and then decreases with increasing incident wave height, and the opposite is true with the transmission coefficient. It features that the effect of an artificial sandbar on wave energy dissipation strengthens first and then weakens with increasing incident wave height. Additionally, an empirical formula for the wave runup was proposed based on the model results of the wave runup for storm wave conditions. The study reveals the complex processes of wave–structure–coast interactions and provides scientific evidence for the design of an artificial sandbar in beach nourishment projects. Full article
(This article belongs to the Section Hydrogeology)
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<p>Experimental layout and beach profile types: (<b>a</b>) without and (<b>b</b>) with an artificial sandbar (W1 to W13 indicates wave gauges). The blue horizontal line represents the still water level, and the yellow part is the beach profile.</p>
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<p>Comparisons of predicted and observed (<b>a</b>–<b>m</b>) wave spectra and (<b>n</b>) significant wave height over the beach profile without an artificial sandbar under normal wave conditions.</p>
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<p>Comparisons of predicted and observed (<b>a</b>–<b>m</b>) wave spectra and (<b>n</b>) significant wave height over the beach profile with an artificial sandbar from <span class="html-italic">X</span> = 10 m to <span class="html-italic">X</span> = 22 m under normal wave conditions.</p>
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<p><span class="html-italic">H</span><sub>s_total</sub>, <span class="html-italic">H</span><sub>s_short</sub>, and <span class="html-italic">H</span><sub>s_long</sub> under normal wave action on the beach (<b>a</b>) without and (<b>b</b>) with an artificial sandbar from <span class="html-italic">X</span> = 8 m to <span class="html-italic">X</span> = 18 m.</p>
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<p><span class="html-italic">H</span><sub>s_total</sub>, <span class="html-italic">H</span><sub>s_short</sub>, and <span class="html-italic">H</span><sub>s_long</sub> under normal wave action on the beach (<b>a</b>) without and (<b>b</b>) with an artificial sandbar from <span class="html-italic">X</span> = 8 m to <span class="html-italic">X</span> = 18 m.</p>
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<p>Mean water level under normal wave conditions on a nourished beach (<b>a</b>) without and (<b>b</b>) with an artificial sandbar from <span class="html-italic">X</span> = 8 m to <span class="html-italic">X</span> = 18 m.</p>
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<p>Wave skewness and wave asymmetry under normal wave conditions over a beach (<b>a</b>) without and (<b>b</b>) with an artificial sandbar (8 &lt; <span class="html-italic">X</span> &lt; 18 m).</p>
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<p>Depth-averaged velocity, upper and lower layer velocities, and their difference under normal wave conditions over a beach (<b>a</b>) without and (<b>b</b>) with an artificial sandbar (8 &lt; <span class="html-italic">x</span> &lt; 18 m).</p>
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<p>The (<b>a</b>) <span class="html-italic">H</span><sub>s_total</sub>, (<b>b</b>) <span class="html-italic">H</span><sub>s_short</sub>, and (<b>c</b>) <span class="html-italic">H</span><sub>s_long</sub> on the beach profile without an artificial sandbar under 6 storm wave conditions.</p>
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<p>The (<b>a</b>) <span class="html-italic">H</span><sub>s_total</sub>, (<b>b</b>) <span class="html-italic">H</span><sub>s_short</sub>, and (<b>c</b>) <span class="html-italic">H</span><sub>s_long</sub> on the beach profile with an artificial sandbar (8 &lt; <span class="html-italic">x</span> &lt; 18 m) under 6 storm wave conditions.</p>
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<p>Reflection, transmission, and dissipation coefficients of the artificial sandbar and the mean water level behind the sandbar (W3, W4, and W5) under 6 storm wave conditions.</p>
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<p>Simulated values of (<b>a</b>) wave runup of 2% cumulative frequency, (<b>b</b>) mean water level of wave runup, (<b>c</b>) high-frequency significant swash height, and (<b>d</b>) low-frequency significant swash height under storm wave conditions.</p>
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28 pages, 24331 KiB  
Article
A Holistic Approach for Coastal–Watershed Management on Tourist Islands: A Case Study from Petra–Molyvos Coast, Lesvos Island (Greece)
by Stamatia Papasarafianou, Ilias Siarkos, Aliki Gkaifyllia, Stavros Sahtouris, Giada Varra, Antonis Chatzipavlis, Thomas Hasiotis and Ourania Tzoraki
Geosciences 2024, 14(12), 326; https://doi.org/10.3390/geosciences14120326 - 2 Dec 2024
Viewed by 878
Abstract
Shoreline configurations are a complex outcome of the dynamic interplay between natural forces and human actions. This interaction shapes unique coastal morphologies and affects sediment transport and erosion patterns along the coastline. Meanwhile, ephemeral river systems play a vital role in shaping coastlines [...] Read more.
Shoreline configurations are a complex outcome of the dynamic interplay between natural forces and human actions. This interaction shapes unique coastal morphologies and affects sediment transport and erosion patterns along the coastline. Meanwhile, ephemeral river systems play a vital role in shaping coastlines and maintaining ecosystem sustainability, especially in island settings. In this context, the present study seeks to develop a holistic approach that views coast and watershed systems as a continuum, aiming to investigate their relationships in an island environment, while accounting for human interventions in the river regime. For this task, the empirical USLE method was employed to quantify sediment production and transport from the catchment area to the coast, while hydraulic simulations using HEC-RAS were conducted to assess sediment retention within flood-affected areas. Moreover, coastal vulnerability to erosion was evaluated by applying the InVEST CVI model in order to identify areas at risk from environmental threats. The coastal zone of Petra–Molyvos, Lesvos, Greece, was selected as the study area due to ongoing erosion issues, with particular emphasis on its interaction with the Petra stream as a result of significant human intervention at its mouth. According to the study’s findings, the examined coastal zone is highly vulnerable to combined erosion from wind and waves, while the river’s mouth receives only a small amount of sediment from water fluxes. Evidently, this leads to an increase in beach retreat phenomena, while highlighting the necessity for integrated coastal–watershed management. Full article
(This article belongs to the Section Hydrogeology)
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<p>(<b>a</b>) A location map of Lesvos Island, Greece, and Petra–Molyvos beach, (<b>b</b>) the coastal area, referred to as the “Vulnerability area”, where the vulnerability assessment was conducted (including topographic details), along with the main streams interacting with the coast, the mouths of the most significant streams such as Molyvos, Petra, and Anaxos rivers, and the boundaries of the Petra hydrological basin, which was included in the study analysis, and (<b>c</b>) topographic and hydrological details of the Petra basin, together with the area referred to as the “Flood Assessment Area”, where flood risk assessment was performed.</p>
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<p>(<b>a</b>) The geomorphology of the coast under study, along with the geological formations identified in the region, and (<b>b</b>) the types of land use observed throughout the broader area, referring to the year 2018 (112—discontinuous urban fabric, 131—mineral extraction sites, 142—sport and leisure facilities, 211—non-irrigated arable land, 223—olive groves, 231—pastures, 242—composite culture systems, 243—land principally occupied by agriculture, 312—coniferous forest, 321—natural grassland, 323—sclerophyllous vegetation, 324—transitional woodland/shrub, 523—sea and ocean).</p>
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<p>(<b>a</b>) The geological background of the Petra basin, and (<b>b</b>) the types of land use within the Petra basin, referring to the year 2018 (112—discontinuous urban fabric, 131—mineral extraction sites, 211—non-irrigated arable land, 223—olive groves, 242—composite culture systems, 243—land principally occupied by agriculture, 311—broad-leaved forest, 312—coniferous forest, 324—transitional woodland/shrub).</p>
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<p>Graphical representation of the methodological framework developed in the present study to investigate the interconnection among coastal vulnerability, sediment transport, and river flood risk.</p>
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<p>A Windrose depicting the primary wind directions in Petra–Molyvos and used to estimate wind exposure in the study area, during the period from 2017 to 2022.</p>
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<p>Map depiction of USLE factors for the Petra basin: (<b>a</b>) K-factor, (<b>b</b>) LS-factor, (<b>c</b>) C-factor, and (<b>d</b>) P-factor.</p>
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<p>The seven sub-basins and the three junctions (J1–J3) of the study area, along with the main tributaries (SB1–SB7), the “Flood Assessment Area” and the nine cross-sections located in its interior and considered in the hydraulic simulations.</p>
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<p>(<b>a</b>) The ranking evaluation of the first three parameters, i.e., Relief, Surge Potential, and Wind, of the coastal exposure index, (<b>b</b>) the ranking evaluation of the remaining parameters, i.e., Geomorphology, Habitats, Wave, alongside the Coastal Vulnerability estimated by the INVEST model considering all six parameters, and (<b>c</b>) Coastal Vulnerability also considering Sea Level Rise over a 10-year return period for the projected scenario RCP 8.5, compared to the previously estimated baseline scenario.</p>
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<p>Soil loss distribution for the Petra basin (the areal percentage of each soil erosion class is given in parentheses).</p>
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<p>Integrative water surface profile along the examined reach within the “Flood Assessment Area”, together with the plan view of water surface elevation at cross-sections XS-2, XS-7, and XS-8, for the three different flow profiles (5-year, 50-year, and 100-year return periods).</p>
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<p>Flood inundation maps for the three different recurrence intervals (5-year, 50-year, and 100-year return periods).</p>
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<p>Inundated areas in each type of land use (112—discontinuous urban fabric, 242—composite culture systems) for the three different recurrence intervals (5-year, 50-year, and 100-year return periods).</p>
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<p>Impact of natural and human factors on the coast–watershed system in the area of interest: (<b>a</b>) coastline morphology adjacent to the Petra river’s mouth in 2003 (Google Earth Image), (<b>b</b>) coastline morphology adjacent to the Petra river’s mouth both in 2003 and 2024 (Google Earth Image), clearly illustrating beach retreat over these years, (<b>c</b>) human interventions (i.e., bridge, channelization) in the riverbed, and (<b>d</b>) human interventions in the river’s mouth (Petra beach).</p>
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22 pages, 6416 KiB  
Article
Assessing Compound Coastal–Fluvial Flood Impacts and Resilience Under Extreme Scenarios in Demak, Indonesia
by Asrini Chrysanti, Ariz Adhani, Ismail Naufal Azkiarizqi, Mohammad Bagus Adityawan, Muhammad Syahril Badri Kusuma and Muhammad Cahyono
Sustainability 2024, 16(23), 10315; https://doi.org/10.3390/su162310315 - 25 Nov 2024
Viewed by 566
Abstract
Demak is highly vulnerable to flooding from both fluvial and coastal storms, facing increasing pressures on its sustainability and resilience due to multiple compounding flood hazards. This study assesses the inundation hazards in Demak coastal areas by modeling the impacts of compound flooding. [...] Read more.
Demak is highly vulnerable to flooding from both fluvial and coastal storms, facing increasing pressures on its sustainability and resilience due to multiple compounding flood hazards. This study assesses the inundation hazards in Demak coastal areas by modeling the impacts of compound flooding. We modeled eight scenarios incorporating long-term forces, such as sea level rise (SLR) and land subsidence (LS), as well as immediate forces, like storm surges, wind waves, and river discharge. Our findings reveal that immediate forces primarily increase inundation depth, while long-term forces expand the inundation area. Combined effects from storm tides and other factors resulted in a 10–20% increase in flood extent compared to individual forces. Fluvial flooding mostly impacts areas near river outlets, but the combination of river discharge and storm tides produces flood extents similar to those caused by SLR. Land subsidence emerged as the primary driver of coastal flooding, while other factors, adding just 25% to area increase, significantly impacted inundation depth. These findings underscore the effectiveness of mangroves in mitigating floods in low-lying areas against immediate forces. However, the resilience and sustainability of the Demak region are challenged by SLR, LS, and the need to integrate these factors into a comprehensive flood mitigation strategy. Full article
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<p>The location of the study area. The green line indicates four sub-districts in the Demak Regency. The white square indicates the location of the study area in Java Island.</p>
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<p>(<b>a</b>) Skew surge profile of selected storm events. The data are collected from the Semarang tidal monitoring station. The water level residuals are extracted from the observed water level and astronomical tide prediction. Observed water level and predicted storm events on (<b>b</b>) 1 December 2017; (<b>c</b>) 23 May 2018; (<b>d</b>) 7 April 2020; and (<b>e</b>) 3 June 2020.</p>
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<p>Return periods for (<b>a</b>) significant wave height and (<b>b</b>) wave period.</p>
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<p>(<b>a</b>) Watersheds of rivers that flow into the Demak Delta. Main river discharge: (<b>b</b>) 50-year return-period flood discharge; (<b>c</b>) flow duration curve (FDC) calibration of the Sacramento model and observation of Buyaran River discharge.</p>
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<p>Model domain: (<b>a</b>) the first model domain covers the area from Kendal City to Jepara City. Storm wave and high tidal forcing boundary conditions are used in this domain. (<b>b</b>) The second model domain covers a smaller area of Semarang City and some parts of southeastern Jepara City. No additional forcing was added to this domain. The smallest grid with the highest resolution was implemented in our area of interest: Demak Regency.</p>
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<p>Flowchart for the scenario simulated for the future projection of flood hazards. The gray background color indicates different forcings implemented in this study.</p>
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<p>(<b>a</b>) Skew surge abstracted at an extreme storm event (1 December 2017); (<b>b</b>) boundary condition for high-water spring and wind wave (blue); storm tides in the SH-WS scenario (orange); storm tides with SLR for the SS-SLR scenario (green).</p>
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<p>Maximum inundation depth values for the following scenarios: (<b>a</b>) baseline scenario; (<b>b</b>) storm tide scenario (SH-WS); (<b>c</b>) high-water spring and sea level rise scenario (SH-SLR); (<b>d</b>) high-water spring and land subsidence scenario (SH-LS). The inundation depth changes for all scenarios can be seen in <a href="#app1-sustainability-16-10315" class="html-app">Figure S4</a>. The red triangle in <a href="#sustainability-16-10315-f008" class="html-fig">Figure 8</a>a indicates the Wulan River outlet and the yellow line indicates sub-district region.</p>
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<p>Maximum inundation increases based on the baseline (HWS scenario): (<b>a</b>–<b>d</b>) single forcing scenarios; (<b>e</b>–<b>h</b>) compound scenarios under the storm tide condition. A visualization map of inundation depth increases can be seen in <a href="#app1-sustainability-16-10315" class="html-app">Figure S4</a>.</p>
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<p>(<b>a</b>) Water depth distribution during flooding period, data collected for the Bonang region, and (<b>b</b>) maximum inundation depth distribution for all simulated scenarios.</p>
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<p>Maximum inundation depth for compound scenarios: (<b>a</b>) storm tide and river discharge (SS-DR); (<b>b</b>) storm tide and sea level rise scenario (SS-SLR); (<b>c</b>) storm tide and land subsidence scenario (SS-LS); (<b>d</b>) worst-case (WC) scenario. Yellow line indicates sub-district region.</p>
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<p>Inundation depth distribution for all simulated scenarios.</p>
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<p>Flooding extent at higher topographical elevations (above MSL): (<b>a</b>) HWS (828.01 Ha inundated); (<b>b</b>) storm tide (1525.26 Ha inundated) (<b>c</b>) worst-case scenario (6315.31 Ha inundated). The yellow line indicates sub-district region.</p>
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18 pages, 3781 KiB  
Article
A Multiscale Model to Assess Bridge Vulnerability Under Extreme Wave Loading
by Umberto De Maio, Fabrizio Greco, Paolo Lonetti and Paolo Nevone Blasi
J. Mar. Sci. Eng. 2024, 12(12), 2145; https://doi.org/10.3390/jmse12122145 - 25 Nov 2024
Viewed by 515
Abstract
A multiscale model is proposed to assess the impact of wave loading on coastal or inland bridges. The formulation integrates various scales to examine the effects of flooding actions on fluid and structural systems, transitioning from global to local representation scales. The fluid [...] Read more.
A multiscale model is proposed to assess the impact of wave loading on coastal or inland bridges. The formulation integrates various scales to examine the effects of flooding actions on fluid and structural systems, transitioning from global to local representation scales. The fluid flow was modeled using a turbulent two-phase level set formulation, while the structural system employed the 3D solid mechanics theory. Coupling between subsystems was addressed through an FSI formulation using the ALE moving mesh methodology. The proposed model’s validity was confirmed through comparisons with numerical and experimental data from the literature. A parametric study was conducted on wave load characteristics associated with typical flood or tsunami scenarios. This included verifying the wave load formulas from existing codes or refined formulations found in the literature, along with assessing the dynamic amplification’s effects on key bridge design variables and the worst loading cases involving bridge uplift and horizontal forces comparable to those typically used in seismic actions. Furthermore, a parametric study was undertaken to examine fluid flow and bridge characteristics, such as bridge elevation, speed, inundation ratio, and bearing system typology. The proposed study aims to identify the worst-case scenarios for bridge deck vulnerability. Full article
(This article belongs to the Special Issue Analysis and Design of Marine Structures)
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<p>General model and multiscale formulation for the fluid and structural systems.</p>
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<p>Multiscale model: fluid (2D) and structural (3D) systems.</p>
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<p>Schematic test configuration GM (<b>a</b>) and definition of the Reduced Model (RM) geometry (<b>b</b>).</p>
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<p>Comparisons between experimental, numerical [<a href="#B38-jmse-12-02145" class="html-bibr">38</a>], and proposed model results in terms of (<b>a</b>) horizontal and (<b>b</b>) vertical forces.</p>
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<p>Mesh discretization of Global Model (GM) and Reduced Model (RM): mesh discretization with details around the bridge.</p>
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<p>DAFs of midspan centroid displacements (V<sub>2</sub>, V<sub>3</sub>) and hydrodynamic forces (F<sub>2</sub>, F<sub>3</sub>) vs. inundation ratio <span class="html-italic">H</span>* at fixed inlet speed ratio equal to <span class="html-italic">U</span>* = 0.5 (<b>a</b>) and <span class="html-italic">U</span>* = 0.7 (<b>b</b>).</p>
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<p>DAFs of midspan centroid displacements (V<sub>2</sub>, V<sub>3</sub>) and hydrodynamic forces (F<sub>2</sub>, F<sub>3</sub>) vs. inlet speed factor <span class="html-italic">U</span>* at fixed inundation ratio equal to <span class="html-italic">H</span>* = 3 (<b>a</b>) or <span class="html-italic">H</span>* = 4 (<b>b</b>).</p>
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<p>DAFs of midspan centroid transverse displacements V<sub>2</sub> (<b>a</b>) and V<sub>3</sub> (<b>b</b>) vs. deformability parameter (<span class="html-italic">s</span>*) for different values of inlet speed (<span class="html-italic">U</span>* = 0.3; 0.5; 0.7).</p>
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<p>Time histories of the vertical reaction force R<sub>3</sub> normalized on the value under dead loads (Rg) for different values of inundation ratios <span class="html-italic">H</span>* (<b>a</b>) and inlet speed ratios equal to <span class="html-italic">U</span>* = 0.7 (<b>a</b>) and <span class="html-italic">U</span>* = 0.5 (<b>b</b>).</p>
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<p>Time histories of the transverse reaction force (R<sub>2</sub>) normalized on the total weight of the deck (M<sub>b</sub>g) for different values of inlet speed ratio <span class="html-italic">U</span>* (<b>a</b>) and inundation ratios <span class="html-italic">H</span>* (<b>b</b>).</p>
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<p>Maximum displacements along transverse (V<sub>2</sub>) or vertical (V<sub>3</sub>) normalized on the bridge length (<span class="html-italic">L<sub>B</sub></span>) vs. support stiffness ratio (<span class="html-italic">K</span>/<span class="html-italic">K<sub>ISO</sub></span>) for different values of inlet speed ratios (<span class="html-italic">U</span>*) at a fixed inundation ratio (<span class="html-italic">H</span>*).</p>
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<p>Time histories of the vertical and transverse displacements (V<sub>3</sub>, V<sub>2</sub>) normalized on the maximum value: comparisons between isolated (I) or classical bridge configuration.</p>
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<p>Reaction forces along transverse (R<sub>2</sub>) or vertical (R<sub>3</sub>) normalized girder weight (M<sub>b</sub>g) or hydrodynamic forces (F<sub>2</sub>, F<sub>3</sub>) vs. support stiffness ratio (<span class="html-italic">K</span>/<span class="html-italic">K<sub>ISO</sub></span>) at a fixed inundation ratio (<span class="html-italic">H</span>*) and inlet speed at <span class="html-italic">U</span>* = 0.5 (<b>a</b>) and <span class="html-italic">U</span>* = 0.5 (<b>b</b>).</p>
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<p>Maximum tsunami-induced forces calculated by the present model with different mesh sizes in the main calculation domain.</p>
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25 pages, 10748 KiB  
Article
Advancing Coastal Flood Risk Prediction Utilizing a GeoAI Approach by Considering Mangroves as an Eco-DRR Strategy
by Tri Atmaja, Martiwi Diah Setiawati, Kiyo Kurisu and Kensuke Fukushi
Hydrology 2024, 11(12), 198; https://doi.org/10.3390/hydrology11120198 - 23 Nov 2024
Viewed by 789
Abstract
Traditional coastal flood risk prediction often overlooks critical geographic features, underscoring the need for accurate risk prediction in coastal cities to ensure resilience. This study enhances the prediction of coastal flood occurrence by utilizing the Geospatial Artificial Intelligence (GeoAI) approach. This approach employed [...] Read more.
Traditional coastal flood risk prediction often overlooks critical geographic features, underscoring the need for accurate risk prediction in coastal cities to ensure resilience. This study enhances the prediction of coastal flood occurrence by utilizing the Geospatial Artificial Intelligence (GeoAI) approach. This approach employed models—random forest (RF), k-nearest neighbor (kNN), and artificial neural networks (ANN)—and compared them to the IPCC risk framework. This study used El Salvador as a demonstration case. The models incorporated seven input variables: extreme sea level, coastline proximity, elevation, slope, mangrove distance, population, and settlement type. With a recall score of 0.67 and precision of 0.86, the RF model outperformed the other models and the IPCC approach, which could avoid imbalanced datasets and standard scaler issues. The RF model improved the reliability of flood risk assessments by reducing false negatives. Based on the RF model output, scenario analysis predicted a significant increase in flood occurrences by 2100, mainly under RCP8.5 with SSP5. The study also highlights that the continuous mangrove along the coastline will reduce coastal flood occurrences. The GeoAI approach results suggest its potential for coastal flood risk management, emphasizing the need to integrate natural defenses, such as mangroves, for coastal resilience. Full article
(This article belongs to the Special Issue Impacts of Climate Change and Human Activities on Wetland Hydrology)
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<p>Workflow for coastal flood risk prediction utilizing the GeoAI approach compared to the IPCC risk approach. The data under (*) and (**) indicated that the data had been projected for future ESL and population change following RCP and SSP scenarios, respectively.</p>
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<p>Coastal flood pathways and key variables adapted from [<a href="#B72-hydrology-11-00198" class="html-bibr">72</a>].</p>
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<p>Coastal flood occurrences and seven key forcing variables in El Salvador.</p>
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<p>Comparison of historical coastal flood occurrence 2000–2018 (<b>a</b>) and prediction of coastal flood at the baseline period in El Salvador case based on RF model (<b>b</b>), kNN model (<b>c</b>), and ANN model (<b>d</b>).</p>
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<p>Comparison of model performance using classification report and accuracy, specifically RF model (<b>a</b>), kNN model (<b>b</b>), and ANN model (<b>c</b>).</p>
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<p>Feature importance.</p>
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<p>Coastal flood risk assessment and its performance based on the IPCC risk approach overlaid with historical flood data in El Salvador. The same weighting method (<b>a</b>) and its performance (<b>c</b>) and the adjusted weight method based on RF feature importance (<b>b</b>) and its performance (<b>d</b>).</p>
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<p>RF model evaluation report for baseline and projection.</p>
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<p>Coastal flood prediction in the baseline and projection periods in 2050 and 2100 using RCP4.5 and RCP8.5, as well as SSP1 to SSP5 scenarios based on RF Model results in El Salvador. Cf is defined as the frequency of coastal flood occurrence.</p>
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<p>Percentage of coastal flood occurrence at baseline and projection based on RF Model. Cf means coastal flood, while cfo represents coastal flood occurrence.</p>
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<p>Coastal flood prediction in the baseline and projection periods in 2050 and 2100 using RCP4.5 and RCP8.5, as well as SSP1 to SSP5 scenarios based on RF Model results in El Salvador.</p>
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14 pages, 10922 KiB  
Article
Assessment of Beach Erosion Vulnerability in the Province of Valencia, Spain
by Pablo Ortiz, Isabel López and José Ignacio Pagán
J. Mar. Sci. Eng. 2024, 12(12), 2111; https://doi.org/10.3390/jmse12122111 - 21 Nov 2024
Viewed by 531
Abstract
This research analyses beach vulnerability to erosion along the coast of Valencia province, Spain. The Coastal Vulnerability Index (CVI) is used to assess vulnerability, considering the following variables: beach width, beach erosion/accretion rate, dune width, wave height, relative coastal flood level, submerged vegetation, [...] Read more.
This research analyses beach vulnerability to erosion along the coast of Valencia province, Spain. The Coastal Vulnerability Index (CVI) is used to assess vulnerability, considering the following variables: beach width, beach erosion/accretion rate, dune width, wave height, relative coastal flood level, submerged vegetation, upper depth limit of submerged vegetation, and percentage of vegetated dune. The results show that vulnerability varies significantly along the coast. The vulnerability assessment revealed that 26.9% of the coastal sections were classified as having very low susceptibility to erosion, 34.5% as low, 22.3% as moderate, 12% as high, and 4.3% as very high. Urbanized areas with reduced dunes are more vulnerable than natural areas with wide beaches and well-developed dunes. The study highlights and discusses limitations of the CVI method and suggests using the mean instead of the square root to calculate the overall vulnerability index due to the influence of one single variable in this formula. It is concluded that natural areas characterized by the presence of dunes exhibit a diminished vulnerability to erosion when compared to highly urbanized regions devoid of dunes and marine vegetation. Full article
(This article belongs to the Special Issue Coastal Evolution and Erosion under Climate Change)
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<p>Area of study: (<b>a</b>) province of Valencia, Spain; (<b>b</b>) coastal stretch studied, with municipalities marked, SIMAR nodes, and submerged vegetation.</p>
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<p>Example of a coastal strip with sections marked, representative transects, baseline, shorelines from 2018 to 2023, bathymetry, dune limit, and GNSS survey points.</p>
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<p>Example of detailed beach profile surveyed, with the different parts of a beach marked, and the flood level calculated. Note that in this case, the flood level overpasses the dune foot, but not the dune crest.</p>
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<p>Dune vegetation coverage method: (<b>a</b>) RGBI image for 2022, (<b>b</b>) NDVI for 2022, (<b>c</b>) vegetation extracted at a spatial resolution of 1 m/pix, (<b>d</b>) average dune vegetation coverage and percentage of dune area.</p>
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<p>Vulnerability obtained from CVI values for each transect. (<b>a</b>) Overall view and zones studied; (<b>b</b>) province limit to Port of Sagunto; (<b>c</b>) Port of Sagunto to Port of Valencia; (<b>d</b>) Port of Valencia to Perellonet estuary; (<b>e</b>) Perellonet estuary to Cape Cullera; (<b>f</b>) Cape Cullera to Tavernes de la Valldigna; (<b>g</b>) Tavernes de la Valldigna to Port of Gandia; (<b>h</b>) Port of Gandia to Girona river (province limit).</p>
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<p>Distribution of the 391 sections analysed by vulnerability for CVI and each variable considered.</p>
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<p>Example of three adjacent sections with different vulnerability and the values of CVI variables.</p>
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18 pages, 4406 KiB  
Article
A Baroclinic Fluid Model and Its Application in Investigating the Salinity Transport Process Within the Sediment–Water Interface in an Idealized Estuary
by Jun Zhao, Liangsheng Zhu, Bo Hong and Jianhua Li
J. Mar. Sci. Eng. 2024, 12(11), 2107; https://doi.org/10.3390/jmse12112107 - 20 Nov 2024
Viewed by 491
Abstract
Understanding the salinity transport process around the sediment–water interface is important for water resources management in the upper reach of an estuary. In this study, we developed a baroclinic fluid dynamic model for investigating the flow and salt transport characteristics within the sediment–water [...] Read more.
Understanding the salinity transport process around the sediment–water interface is important for water resources management in the upper reach of an estuary. In this study, we developed a baroclinic fluid dynamic model for investigating the flow and salt transport characteristics within the sediment–water interface under tidal forcing. The validation showed robust model performance on the salinity transport within the sediment–water interface. The results revealed that the turbulent kinetic energy, dissipation rate, and kinetic energy production rate exhibited periodic variations within the seabed boundary layer. The thickness of the viscous sublayer and the mean flow showed an inverse relationship. Water and salinity exchange within the sediment–water interface occurred predominantly via turbulent diffusion, with extreme turbulent kinetic energy production rates appearing during the tidal reversal, flood, and ebb stages. The sediment acted as a source of salinity release during ebb tides and a sink for salinity absorption during flood tides. As the sediment depth increased, fluctuations in salinity were weakened. These results clearly illustrated that the sediment layer is important in modulating the salinity transport in the upper reach of an estuary. However, such an important process was usually excluded by previous studies. The model developed in this study can be used as a sediment–water interface module that, coupled with other hydrodynamic models, can evaluate the contributions of the sediment layer to the salinity exchange in coastal water. Full article
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<p>Flow chart of the numerical model solution.</p>
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<p>Diagram of the calculation area. (<b>a</b>) Schematic of the computational domain and grid partitioning. The grid size <math display="inline"><semantics> <mrow> <mo>∆</mo> <mi>x</mi> <mo>=</mo> <mo>∆</mo> <mi>y</mi> <mo>=</mo> <mn>2</mn> <mo> </mo> <mi mathvariant="normal">m</mi> </mrow> </semantics></math>, and the minimum grid size <math display="inline"><semantics> <mi>z</mi> </semantics></math> coordinate is <math display="inline"><semantics> <mrow> <mo>∆</mo> <mi>z</mi> <mo>=</mo> <mn>0.002</mn> <mo> </mo> <mi mathvariant="normal">m</mi> </mrow> </semantics></math>. The sediment–water interface layer was at a depth of 0 m, while the free water surface was at a depth of 10 m. Monitoring point A was located at (500, 25, <math display="inline"><semantics> <mi>z</mi> </semantics></math>); (<b>b</b>) diagram of section across the estuary; (<b>c</b>) diagram of sediment–water interface layer (OL represents the overlying water layer, BBL represents the benthic boundary layer, SWI represents the sediment–water interface, SL represents the sediment layer, LLL represents the logarithm law layer, VSL represents the viscous sublayer, and SSL represents the sediment surface layer).</p>
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<p>Upstream and downstream boundary conditions. (<b>a</b>) Time series of velocity at the upstream boundary; (<b>b</b>) time series of the water level at the downstream boundary.</p>
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<p>Comparison of observed and computed values of salinity at the entrance of the estuary (10 m away from the downstream saltwater boundary). (<b>a</b>) Salinity time series in the bottom layer; (<b>b</b>) salinity time series in the middle layer.</p>
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<p>Vertical transect of salinity along the channel of estuary (<span class="html-italic">y</span> = 25 m). (<b>a</b>) Salinity distribution at typical flood tide (20:00); (<b>b</b>) salinity distribution at typical ebb tide (02:00). The flooding tide presented from 18:00 to 00:00 and the ebb tide lasted from 00:00 to 06:00.</p>
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<p>Salinity variations at different depths within the sediment–water interface at monitoring station A (see <a href="#jmse-12-02107-f002" class="html-fig">Figure 2</a> for the location).</p>
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<p>Salinity distribution at the sediment–water interface at monitoring station A (see <a href="#jmse-12-02107-f002" class="html-fig">Figure 2</a> for the location). (<b>a</b>) Salinity profiles during the flood tide (from 19:00 to 00:00); (<b>b</b>) salinity profiles during the ebb tide (from 01:00 to 06:00); (<b>c</b>) depth–time profile of salinity (psu) at station A.</p>
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<p>Temporal evolution of the average flow velocity, turbulent kinetic energy, turbulent dissipation rate, roughness height, and viscous sublayer thickness in the vertical direction for the seabed boundary layer during the course of two tidal cycles at monitoring station A. (<b>a</b>) Time series of mean flow velocity; (<b>b</b>) time series of turbulent kinetic energy; (<b>c</b>) time series of turbulent dissipation rate; (<b>d</b>) time series of viscous sublayer thickness (the ebb tide period was from 08–07 12:00 to 18:00 and from 08–08 0:00 to 06:00, while the flood tide period was from 08–07 18:00 to 24:00 and from 08–08 06:00 to 12:00).</p>
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<p>Contour of turbulent kinetic energy production rate (<span class="html-italic">P<sub>TKE</sub></span>) in the water column at monitoring station A. (<b>a</b>) Time series of the water level; (<b>b</b>) time–depth variation of turbulent kinetic energy production rate (<span class="html-italic">P<sub>TKE</sub></span>) (the ebb tide period was from 08–07 12:00 to 18:00 and from 08–08 0:00 to 06:00, while the flood tide period was from 08–07 18:00 to 24:00 and from 08–08 06:00 to 12:00).</p>
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<p>Variation of convective and diffusive fluxes at the sediment–water interface. (<b>a</b>) Time series of convective flux; (<b>b</b>) time series of diffusive flux (the ebb tide period was from 08–07 12:00 to 18:00 and from 08–08 0:00 to 06:00, while the flood tide period was from 08–07 18:00 to 24:00 and from 08–08 06:00 to 12:00).</p>
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22 pages, 4456 KiB  
Article
Fluvial Sediment Load Characteristics from the Yangtze River to the Sea During Severe Droughts
by Xiujuan Liu, Yuanyuan Sun, Albert J. Kettner, Daosheng Wang, Jun Cheng and Zhenhua Zou
Water 2024, 16(22), 3319; https://doi.org/10.3390/w16223319 - 19 Nov 2024
Viewed by 523
Abstract
Most river deltas worldwide are located in well-developed, densely populated lowland regions that face challenges from accelerated sea level rise. Deltas with morphological equilibrium are the foundation for associated prosperous economies and societies, as well as for preserving ecological fragile environments. And for [...] Read more.
Most river deltas worldwide are located in well-developed, densely populated lowland regions that face challenges from accelerated sea level rise. Deltas with morphological equilibrium are the foundation for associated prosperous economies and societies, as well as for preserving ecological fragile environments. And for deltas to be in morphological equilibrium, sufficient fluvial sediment supplies are fundamental. Severe droughts have significant impacts on the sediment load discharged to the sea, but this is considerably less studied compared to flooding events. This study examines the characteristics of Yangtze River sediment flowing toward the East China Sea during severe droughts. The effect of the Three Gorges Dam (TGD) was investigated by comparing the difference before and after its construction in 2003. Results indicate that the sediment load from the Yangtze River to the sea has experienced a more pronounced decrease during severe drought years since 2003. The primary cause is a substantial reduction in sediment supply from the upper reaches, resulting from the impoundment of the Three Gorges Reservoir created in 2003 and the construction of additional major reservoirs in the upper reach thereafter. Simultaneously, this is accompanied by the fining of sediment grain size. The fining of sediment and considerably reduced sediment load discharged to the sea during severe droughts after 2003 are likely to accelerate the erosion of the Yangtze subaqueous delta. The rating parameter values during severe drought years fall within the range observed in normal years, indicating that these drought events do not align with extreme rating parameter values. Less than 30% of the average discrepancy between measured and reconstructed sediment loads in severe drought years before 2003, and approximately 10% of the discrepancy after 2003, demonstrate the feasibility of reconstructing sediment loads for severe drought events using a sediment rating curve. This rating curve is based on daily water discharge and sediment concentration data collected during the corresponding period. These findings indicate that the rating curve-based reconstruction of sediment load performs well during severe droughts, with relative error slightly exceeding the average error of normal years prior to 2003 and approaching that observed after 2003. This study provides insights on sediment management of the Yangtze River system, including its coastal zone, and is valuable for many other large river systems worldwide. Full article
(This article belongs to the Section Oceans and Coastal Zones)
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<p>Overview of the study area.</p>
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<p>Sediment budgets within the tidal influenced reach and the estuary of the Yangtze River. Data for 1958–1992 are from Wu et al. [<a href="#B36-water-16-03319" class="html-bibr">36</a>], those for 1992–2002 and 2002–2012 are from Yang et al. [<a href="#B37-water-16-03319" class="html-bibr">37</a>], and those for 2007–2019 are from Guo et al. [<a href="#B38-water-16-03319" class="html-bibr">38</a>].</p>
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<p>Time series (early 1950s–2022) of runoff and sediment load along the main stream of the Changjiang River and the construction of large dams (gray vertical lines) in the upper reaches for: (<b>a</b>) Yichang station, (<b>b</b>) Hankou station, and (<b>c</b>) Datong station.</p>
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<p>(<b>a</b>) Rating curves derived from daily water discharge and suspended sediment concentration data during different periods at the Datong station from 1954 to 2021 (the data from 1988–1997 are excluded, as data for suspended sediment concentration are unavailable), and (<b>b</b>) rating parameters obtained from annual sediment load during the different periods.</p>
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<p>(<b>a</b>) Rating curves derived from daily water discharge and suspended sediment concentration data during different periods at the Datong station from 1954 to 2021 (the data from 1988–1997 are excluded, as data for suspended sediment concentration are unavailable), and (<b>b</b>) rating parameters obtained from annual sediment load during the different periods.</p>
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<p>(<b>a</b>) Comparison of reconstructed annual sediment load without correction and the measured load at the Datong station from 1955 to 2021, including severe droughts; (<b>b</b>) comparison of the reconstructed annual sediment load after correction and the measured load at the Datong station from 1955 to 2021, including severe droughts; and (<b>c</b>) measured annual sediment load, reconstructed load without correction, and reconstructed load with correction from 1954 to 2021.</p>
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<p>(<b>a</b>) Log daily water discharge vs. log daily suspended sediment concentration from 1955 to 1969 and for 1954 (<b>a1</b>), 1959 (<b>a2</b>), and 1960 (<b>a3</b>); (<b>b</b>) log daily water discharge vs. log daily suspended sediment concentration from 1970 to 1985 and for 1972 (<b>b1</b>) and 1978 (<b>b2</b>); (<b>c</b>) log daily water discharge vs. log daily suspended sediment concentration from 1986 to 2002 and for 1986 (<b>c1</b>) and 1998 (<b>c2</b>); and (<b>d</b>) log daily water discharge vs. log daily suspended sediment concentration from 2003 to 2013 and for 2006 (<b>d1</b>) and 2011 (<b>d2</b>).</p>
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<p>(<b>a</b>) Log daily water discharge vs. log daily suspended sediment concentration from 1955 to 1969 and for 1954 (<b>a1</b>), 1959 (<b>a2</b>), and 1960 (<b>a3</b>); (<b>b</b>) log daily water discharge vs. log daily suspended sediment concentration from 1970 to 1985 and for 1972 (<b>b1</b>) and 1978 (<b>b2</b>); (<b>c</b>) log daily water discharge vs. log daily suspended sediment concentration from 1986 to 2002 and for 1986 (<b>c1</b>) and 1998 (<b>c2</b>); and (<b>d</b>) log daily water discharge vs. log daily suspended sediment concentration from 2003 to 2013 and for 2006 (<b>d1</b>) and 2011 (<b>d2</b>).</p>
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21 pages, 24656 KiB  
Article
Climate Change May Increase the Impact of Coastal Flooding on Carbon Storage in China’s Coastal Terrestrial Ecosystems
by Shuyu Yang, Jiaju Lin and Xiongzhi Xue
Land 2024, 13(11), 1871; https://doi.org/10.3390/land13111871 - 8 Nov 2024
Viewed by 609
Abstract
Climate warming exacerbates the deterioration of soil and degradation of vegetation caused by coastal flooding, impairing ecosystem climate-regulating functions. This will elevate the risk of carbon storage (CS) loss, further intensifying climate change. To delve deeper into this aspect, we aimed to integrate [...] Read more.
Climate warming exacerbates the deterioration of soil and degradation of vegetation caused by coastal flooding, impairing ecosystem climate-regulating functions. This will elevate the risk of carbon storage (CS) loss, further intensifying climate change. To delve deeper into this aspect, we aimed to integrate future land use/land cover changes and global mean sea-level rise to assess the impact of coastal floods on terrestrial CS under the effects of climate change. We compared the 10-year (RP10) and 100-year (RP100) return-period floods in 2020 with projected scenarios for 2050 under SSP1-26, SSP2-45, SSP3-70, and SSP5-85. The study findings indicate that CS loss caused by coastal flooding in China’s coastal zones was 198.71 Tg (RP10) and 263.46 Tg (RP100) in 2020. In 2050, under the SSP1-26, SSP2-45, and SSP3-70 scenarios, the CS loss is projected to increase sequentially, underscoring the importance of implementing globally coordinated strategies for mitigating climate change to effectively manage coastal flooding. The value of CS loss is expected to increase in 2050, with an anticipated rise of 97–525% (RP10) and 91–498% (RP100). This highlights the essential need to include coastal flood-induced CS changes in carbon emission management and coastal climate risk assessments. Full article
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<p>Research Framework.</p>
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<p>Study area.</p>
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<p>Schematic diagram of inundation simulation zoning.</p>
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<p>Land use/land cover (LULC) conversion in 2020 and 2050 under different SSP-RCP scenarios: (<b>a</b>) SSP1-26; (<b>b</b>) SSP2-45; (<b>c</b>) SSP3-70; (<b>d</b>) SSP5-85.</p>
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<p>Distribution and changes in carbon storage (CS): (<b>a</b>) distribution of CS in 2020; (<b>b</b>) total CS in 2020 and 2050 for SSP-RCPs (Tg); (<b>c</b>) distribution of changes in CS in 2050.</p>
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<p>(<b>a</b>) Extreme sea-level (ESL) distribution on shoreline, and (<b>b</b>) regional average ESL.</p>
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<p>Land-use/land-cover types within inundated areas: (<b>a1</b>) 10-year flood (RP10) in 2020; (<b>a2</b>) 100-year (RP100) flood in 2020; (<b>b1</b>) RP10 flood in 2050 under SSP1-26; (<b>b2</b>) RP100 flood in 2050 under SSP1-26; (<b>c1</b>) RP10 flood in 2050 under SSP2-45; (<b>c2</b>) RP100 flood in 2050 under SSP2-45; (<b>d1</b>) RP10 flood in 2050 under SSP3-70; (<b>d2</b>) RP100 flood in 2050 under SSP3-70; (<b>e1</b>) RP10 flood in 2050 under SSP5-85; (<b>e2</b>) RP100 flood in 2050 under SSP5-85.</p>
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<p>Land-use/land-cover (LULC) conversion in inundated regions: (<b>a1</b>–<b>d1</b>) denote the LULC inundated by the coastal flood of RP10 in 2050 under scenarios SSP1-25, SSP2-45, SSP3-70, and SSP5-85, respectively; (<b>a2</b>–<b>d2</b>) represent the individual flooding-inundation scenarios for the RP100.</p>
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<p>Carbon storage loss of different regions (Tg): (<b>a1</b>) 10-year flood (RP10) in 2020; (<b>a2</b>) 100-year (RP100) flood in 2020; (<b>b1</b>) RP10 flood in 2050 under SSP1-26; (<b>b2</b>) RP100 flood in 2050 under SSP1-26; (<b>c1</b>) RP10 flood in 2050 under SSP2-45; (<b>c2</b>) RP100 flood in 2050 under SSP2-45; (<b>d1</b>) RP10 flood in 2050 under SSP3-70; (<b>d2</b>) RP100 flood in 2050 under SSP3-70; (<b>e1</b>) RP10 flood in 2050 under SSP5-85; (<b>e2</b>) RP100 flood in 2050 under SSP5-85.</p>
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<p>Change in CSL per 10 km, 2020 and 2050 (t).</p>
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<p>Values of carbon storage loss in different regions (M<span>$</span>): (<b>a1</b>) 10-year flood (RP10) in 2020; (<b>a2</b>) 100-year (RP100) flood in 2020; (<b>b1</b>) RP10 flood in 2050 under SSP1-26; (<b>b2</b>) RP100 flood in 2050 under SSP1-26; (<b>c1</b>) RP10 flood in 2050 under SSP2-45; (<b>c2</b>) RP100 flood in 2050 under SSP2-45; (<b>d1</b>) RP10 flood in 2050 under SSP3-70; (<b>d2</b>) RP100 flood in 2050 under SSP3-70; (<b>e1</b>) RP10 flood in 2050 under SSP5-85; (<b>e2</b>) RP100 flood in 2050 under SSP5-85.</p>
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23 pages, 3116 KiB  
Article
Assessing Flood Risks in Coastal Plain Cities of Zhejiang Province, Southeastern China
by Saihua Huang, Weidong Xuan, He Qiu, Jiandong Ye, Xiaofei Chen, Hui Nie and Hao Chen
Water 2024, 16(22), 3208; https://doi.org/10.3390/w16223208 - 8 Nov 2024
Viewed by 579
Abstract
Constructing a precise and effective evaluation index system is crucial to flood disaster prevention and management in coastal areas. This study takes Lucheng District, Wenzhou City, Zhejiang Province, southeastern China, as a case study and constructs an evaluation index system comprising three criterion [...] Read more.
Constructing a precise and effective evaluation index system is crucial to flood disaster prevention and management in coastal areas. This study takes Lucheng District, Wenzhou City, Zhejiang Province, southeastern China, as a case study and constructs an evaluation index system comprising three criterion levels: disaster-causing factors, disaster-gestation environments, and disaster-bearing bodies. The weights of each evaluation index are determined by combining the Analytic Hierarchy Process (AHP) and the entropy method. The fuzzy matter-element model is utilized to assess the flood disaster risk in Lucheng District quantitatively. By calculating the correlation degree of each evaluation index, the comprehensive index of flood disaster risk for each street area is obtained, and the flood disaster risk of each street area is classified according to the risk level classification criteria. Furthermore, the distribution of flood disaster risks in Lucheng District under different daily precipitation conditions is analyzed. The results indicate that: (1) the study area falls into the medium-risk category, with relatively low flood risks; (2) varying precipitation conditions will affect the flood resilience of each street in Lucheng District, Wenzhou City. The flood disaster evaluation index system and calculation framework constructed in this study provide significant guidance for flood risk assessment in coastal plain cities. Full article
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<p>Location of the study area and the eight highly urbanized sub-districts.</p>
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<p>The general framework of the study.</p>
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<p>The layered structure of flood disaster assessment.</p>
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<p>Geographical distribution map of flood risk assessment in Lucheng district.</p>
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<p>Comprehensive score distribution map of street area.</p>
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<p>Line chart of secondary index scores of disaster-causing environments.</p>
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<p>Distribution map of flood risk assessment in Lucheng district under different daily precipitation conditions. The areas (<b>a</b>–<b>e</b>) depict the distribution maps of flood risk assessments under daily precipitation conditions of 403.8 mm, 350 mm, 250 mm, 150 mm, and 50 mm.</p>
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<p>Accuracy test of flood disaster risk index. The disaster grade in the figure is divided into four levels: 1, 2, 3, and 4, with level 1 being the most severe and level 4 being the least severe.</p>
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20 pages, 17386 KiB  
Article
Spectral Water Wave Dissipation by Biomimetic Soft Structure
by Garance Marlier, Frédéric Bouchette, Samuel Meulé, Raphaël Certain and Jean-Yves Jouvenel
J. Mar. Sci. Eng. 2024, 12(11), 2004; https://doi.org/10.3390/jmse12112004 - 7 Nov 2024
Viewed by 496
Abstract
Coastal protection solutions can be categorised as grey, hybrid or natural. Grey infrastructure includes artificial structures like dykes. Natural habitats like seagrasses are considered natural protection infrastructure. Hybrid solutions combine both natural and grey infrastructure. Evidence suggests that grey solutions can negatively impact [...] Read more.
Coastal protection solutions can be categorised as grey, hybrid or natural. Grey infrastructure includes artificial structures like dykes. Natural habitats like seagrasses are considered natural protection infrastructure. Hybrid solutions combine both natural and grey infrastructure. Evidence suggests that grey solutions can negatively impact the environment, while natural habitats prevent flooding without such adverse effects and provide many ecosystem services. New types of protective solutions, called biomimetic solutions, are inspired by natural habitats and reproduce their features using artificial materials. Few studies have been conducted on these new approaches. This study aims to quantify wave dissipation observed in situ above a biomimetic solution inspired by kelps, known for their wave-dampening properties. The solution was deployed in a full water column near Palavas-les-Flots in southern France. A one-month in situ experiment showed that the biomimetic solution dissipates around 10% of total wave energy on average, whatever the meteo-marine conditions. Wave energy dissipation is frequency-dependent: short waves are dissipated, while low-frequency energy increases. An anti-dissipative effect occurs for forcing conditions with frequencies close to the eigen mode linked to the biomimetic solution’s geometry, suggesting that resonance should be considered in designing future biomimetic protection solutions. Full article
(This article belongs to the Section Coastal Engineering)
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<p>(<b>a</b>) A map of the study area, where A and B refer to the dyke and the beach in <a href="#sec5dot1-jmse-12-02004" class="html-sec">Section 5.1</a>. (<b>b</b>) A map of the position of the device and the biomimetic structures, composed of ten modules. The black dotted lines forming a rectangle delineate the extension of the biomimetic solution and the domain on which Rabinovitch formalism was used (<a href="#sec5dot1-jmse-12-02004" class="html-sec">Section 5.1</a>). The coloured area represents the bathymetry. (<b>c</b>) The diagram and the photo show one biomimetic structure. (<b>d</b>) A plot of the instrumented transect, where pressure sensors (red diamond) and idealised biomimetic structures are shown. The seabed (black solid line) is placed as a function of the depth measurements (black dots) made at each device.</p>
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<p>Energy spectral density spectra calculated at stations R1 to R5. Each spectrum is calculated by averaging all the spectra calculated over the 30 min long bursts. The dotted vertical lines represent the frequency cuts of the infragravity, the swell and the wind wave bands, clearly identified by relative minima on every mean spectrum.</p>
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<p>Wind and hydrodynamic forcings during the experimentation. The yellow, green and red boxes represent type 1, 2 and 3 conditions, respectively, observed in two periods, a and b. Periods in white are not used in the analysis. The wave characteristics at Sète are offshore conditions. (<b>a</b>) Wave direction (<math display="inline"><semantics> <msub> <mi>θ</mi> <mrow> <mi>s</mi> <mi>e</mi> <mi>t</mi> <mi>e</mi> </mrow> </msub> </semantics></math>) at Sète, wind direction (<math display="inline"><semantics> <msub> <mi>θ</mi> <mrow> <mi>w</mi> <mi>i</mi> <mi>n</mi> <mi>d</mi> </mrow> </msub> </semantics></math>) and wind speed (<math display="inline"><semantics> <msub> <mi>v</mi> <mrow> <mi>w</mi> <mi>i</mi> <mi>n</mi> <mi>d</mi> </mrow> </msub> </semantics></math>) recorded at the Montpellier airport weather station; (<b>b</b>) Significant wave height measured at Sète (<math display="inline"><semantics> <msub> <mi>H</mi> <mrow> <mi>s</mi> <mi>e</mi> <mi>t</mi> <mi>e</mi> </mrow> </msub> </semantics></math>) and at R1 station, and the ratio <math display="inline"><semantics> <mrow> <msub> <mi>H</mi> <mrow> <mn>5</mn> <mo>,</mo> <mi>T</mi> <mi>O</mi> <mi>T</mi> </mrow> </msub> <mo>/</mo> <msub> <mi>H</mi> <mrow> <mn>1</mn> <mo>,</mo> <mi>T</mi> <mi>O</mi> <mi>T</mi> </mrow> </msub> </mrow> </semantics></math>; (<b>c</b>) The mean wave period measured at Sète (<math display="inline"><semantics> <msub> <mi>T</mi> <msub> <mi>m</mi> <mrow> <mi>s</mi> <mi>e</mi> <mi>t</mi> <mi>e</mi> </mrow> </msub> </msub> </semantics></math>) and at the R1 station.</p>
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<p>(<b>a</b>) Plots of mean wave height reduction for <math display="inline"><semantics> <mrow> <mi>T</mi> <mi>O</mi> <mi>T</mi> </mrow> </semantics></math>, <math display="inline"><semantics> <mrow> <mi>I</mi> <mi>G</mi> </mrow> </semantics></math>, <math display="inline"><semantics> <mrow> <mi>S</mi> <mi>S</mi> </mrow> </semantics></math> and <math display="inline"><semantics> <mrow> <mi>W</mi> <mi>W</mi> </mrow> </semantics></math> frequency bands from the R1 to R5 stations for the three types of meteo-marine conditions, including both periods a and b. The coloured envelope represents the standard deviation at each station and for each frequency band. (<b>b</b>) Ternary diagrams of normalised <math display="inline"><semantics> <msub> <mi>E</mi> <mrow> <mi>I</mi> <mi>G</mi> </mrow> </msub> </semantics></math>, <math display="inline"><semantics> <msub> <mi>E</mi> <mrow> <mi>S</mi> <mi>S</mi> </mrow> </msub> </semantics></math> and <math display="inline"><semantics> <msub> <mi>E</mi> <mrow> <mi>W</mi> <mi>W</mi> </mrow> </msub> </semantics></math> by <math display="inline"><semantics> <msub> <mi>E</mi> <mrow> <mi>T</mi> <mi>O</mi> <mi>T</mi> </mrow> </msub> </semantics></math> for the three types of meteo-marine conditions. The two smaller ternary diagrams represent the same information for periods a and b considered separately. Each arrow represents the evolution of the relative contributions of <math display="inline"><semantics> <mrow> <mi>I</mi> <mi>G</mi> </mrow> </semantics></math>, <math display="inline"><semantics> <mrow> <mi>S</mi> <mi>S</mi> </mrow> </semantics></math> and <math display="inline"><semantics> <mrow> <mi>W</mi> <mi>W</mi> </mrow> </semantics></math> to the energy between the R1 and R5 stations for each burst.</p>
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<p>Plots of energy density spectra at R1 to R5 stations for (<b>a</b>) type 1, (<b>b</b>) type 2 and (<b>c</b>) type 3 meteo-marine conditions. Each spectrum is calculated by averaging all elementary spectra calculated over 30 min long bursts for each type of meteo-marine condition.</p>
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<p>A plot of the wavelength <math display="inline"><semantics> <msub> <mi>λ</mi> <mn>1</mn> </msub> </semantics></math> and peak period <math display="inline"><semantics> <msub> <mi>T</mi> <mrow> <mi>p</mi> <mn>1</mn> </mrow> </msub> </semantics></math> defined at the R1 station as a function of <math display="inline"><semantics> <mrow> <msub> <mi>H</mi> <mrow> <mn>5</mn> <mo>,</mo> <mi>T</mi> <mi>O</mi> <mi>T</mi> </mrow> </msub> <mo>/</mo> <msub> <mi>H</mi> <mrow> <mn>1</mn> <mo>,</mo> <mi>T</mi> <mi>O</mi> <mi>T</mi> </mrow> </msub> </mrow> </semantics></math> for each burst. Bursts related to different meteo-marine condition types are represented by different colours. The grey dots represent the burst not related to the different meteo-marine condition types. The wavelength is calculated from each frequency peak for each burst with the approximation of Guo [<a href="#B69-jmse-12-02004" class="html-bibr">69</a>]. The peak period is calculated from the peak frequency. The vertical dashed line separates the dissipative (<math display="inline"><semantics> <mrow> <msub> <mi>H</mi> <mrow> <mn>5</mn> <mo>,</mo> <mi>T</mi> <mi>O</mi> <mi>T</mi> </mrow> </msub> <mo>/</mo> <msub> <mi>H</mi> <mrow> <mn>1</mn> <mo>,</mo> <mi>T</mi> <mi>O</mi> <mi>T</mi> </mrow> </msub> <mo>&lt;</mo> <mn>1</mn> </mrow> </semantics></math>) and anti-dissipative (<math display="inline"><semantics> <mrow> <msub> <mi>H</mi> <mrow> <mn>5</mn> <mo>,</mo> <mi>T</mi> <mi>O</mi> <mi>T</mi> </mrow> </msub> <mo>/</mo> <msub> <mi>H</mi> <mrow> <mn>1</mn> <mo>,</mo> <mi>T</mi> <mi>O</mi> <mi>T</mi> </mrow> </msub> <mo>&gt;</mo> <mn>1</mn> </mrow> </semantics></math>) domains. The horizontal dashed line is placed at <math display="inline"><semantics> <msub> <mi>λ</mi> <mn>1</mn> </msub> </semantics></math> = 37 m (<math display="inline"><semantics> <msub> <mi>T</mi> <mrow> <mi>p</mi> <mn>1</mn> </mrow> </msub> </semantics></math> = 6.47 s), which is roughly equal to the diagonal length of the biomimetic solution.</p>
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<p>Empirical <math display="inline"><semantics> <msub> <mi>C</mi> <mi>D</mi> </msub> </semantics></math> represented as a function of the Reynolds <math display="inline"><semantics> <msub> <mi>R</mi> <mi>e</mi> </msub> </semantics></math> number (<b>a</b>) and the Keulegan–Carpenter <math display="inline"><semantics> <msub> <mi>K</mi> <mi>C</mi> </msub> </semantics></math> number (<b>b</b>) for all bursts. Bursts related to different meteo-marine condition types are represented by different colours. The grey dots represent bursts not related to the different meteo-marine condition types. Empirical <math display="inline"><semantics> <msub> <mi>C</mi> <mi>D</mi> </msub> </semantics></math> laws as a function of (<b>c</b>) <math display="inline"><semantics> <msub> <mi>R</mi> <mi>e</mi> </msub> </semantics></math> and (<b>d</b>) <math display="inline"><semantics> <msub> <mi>K</mi> <mi>C</mi> </msub> </semantics></math> in comparison with other analytical expression of <math display="inline"><semantics> <msub> <mi>C</mi> <mi>D</mi> </msub> </semantics></math> from the literature (see <a href="#jmse-12-02004-t003" class="html-table">Table 3</a>). Dashed lines represent the new empirical <math display="inline"><semantics> <msub> <mi>C</mi> <mi>D</mi> </msub> </semantics></math> laws calculated with the equivalent diameter volume <math display="inline"><semantics> <msub> <mi>D</mi> <mi>V</mi> </msub> </semantics></math>. Empirical <math display="inline"><semantics> <msub> <mi>C</mi> <mi>D</mi> </msub> </semantics></math> is shown as a function of <math display="inline"><semantics> <mrow> <mn>1</mn> <mo>/</mo> <msub> <mi>R</mi> <mi>e</mi> </msub> </mrow> </semantics></math> (<b>e</b>). The colours represent the dissipation intervals over which the new fitted laws are calculated. The optimised parameters associated with each interval are presented in the table next to the plot (<b>f</b>).</p>
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21 pages, 2073 KiB  
Article
The Effects of Anthropogenic Stressors on Above- and Belowground Phytochemical Diversity of the Wetland Grass, Phragmites australis
by Andrea E. Glassmire, Ana L. Salgado, Rodrigo Diaz, Joseph Johnston, Laura A. Meyerson, Joshua S. Snook and James T. Cronin
Plants 2024, 13(22), 3133; https://doi.org/10.3390/plants13223133 - 7 Nov 2024
Viewed by 555
Abstract
Coastal wetlands face threats from climate change-induced flooding and biological invasions. Plants respond to these stressors through changes in their phytochemical metabolome, but it is unclear whether stressors affecting one tissue compartment (e.g., leaves) create vulnerabilities in others (e.g., roots) or elicit similar [...] Read more.
Coastal wetlands face threats from climate change-induced flooding and biological invasions. Plants respond to these stressors through changes in their phytochemical metabolome, but it is unclear whether stressors affecting one tissue compartment (e.g., leaves) create vulnerabilities in others (e.g., roots) or elicit similar responses across tissues. Additionally, responses to multiple simultaneous stressors remain poorly understood due to the focus on individual metabolites in past studies. This study aims to elucidate how the phytochemical metabolome of three Phragmites australis (Cav.) lineages, common in the Mississippi River Delta, responds to flooding and infestation by the non-native scale insect Nipponaclerda biwakoensis (Kuwana). Among these lineages, one is non-native and poses a threat to North American wetlands. Results indicate that metabolomic responses are highly specific, varying with lineage, tissue type, stressor type, and the presence of multiple stressors. Notably, the non-native lineage displayed high chemical evenness, while the other two showed stressor-dependent responses. The 10 most informative features identified by a machine learning model showed less than 1% overlap with known metabolites linked to water and herbivory stress, underscoring gaps in our understanding of plant responses to environmental stressors. Our metabolomic approach offers a valuable tool for identifying candidate plant genotypes for wetland restoration. Full article
(This article belongs to the Special Issue Phytochemical Diversity and Interactions with Herbivores)
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Figure 1

Figure 1
<p>Mean ± SE ion abundance of the top 10 most influential chemical features based on flooding and scale infestation treatments for leaf and root tissues. Random Forest models were run separately for each <span class="html-italic">P. australis</span> lineage and tissue type. The treatments consisted of four types: control conditions, flooding, scale infestation, and the combination of flooding and scale infestation. Panels (<b>A</b>,<b>B</b>) depict the top 10 features for each lineage by leaf and root tissues, respectively. Within lineages, means ± SE are reported and significant differences among treatments are indicated with different letters (<span class="html-italic">p</span> ≤ 0.05; based on one-way ANOVA and Tukey pairwise-comparison tests with uncorrected <span class="html-italic">p</span> values).</p>
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<p>Among pairs of <span class="html-italic">P. australis</span> lineages, a comparison of the number of similar and dissimilar top 10 chemical features identified by the Random Forest analysis for (<b>a</b>) leaf and (<b>b</b>) root tissues. Percent chemical feature overlap is based on the proportion of the top 10 most informative features that are shared between lineages.</p>
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<p>Mean ± SE phytochemical evenness of (<b>a</b>) leaf tissue (filled symbols) and (<b>b</b>) root tissue (open symbols) for the top 10 most informative features from the entire metabolome as a function of scale infestation and flooding treatment combinations. Pielou’s evenness represents the relative abundance for each metabolite. Significant differences among treatments are indicated with different letters and are only meant for comparison within a lineage (<span class="html-italic">p</span> ≤ 0.05; based on one-way ANOVA and Tukey pairwise-comparison tests with uncorrected <span class="html-italic">p</span> values).</p>
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<p>Responses of (<b>a</b>) abscisic acid and (<b>b</b>) citric acid to stress treatments. These two metabolites were among the top 10 most informative features extracted from the Random Forest model in root tissue only. Each shape represents a distinct lineage (see legend). Within lineages, means ± SE are reported and significant differences among treatments are indicated with different letters (<span class="html-italic">p</span> ≤ 0.05; based on one-way ANOVA and Tukey pairwise-comparison tests with uncorrected <span class="html-italic">p</span> values).</p>
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<p>Responses of (<b>a</b>) chlorogenic acid, (<b>b</b>) proline, (<b>c</b>) rutin, and (<b>d</b>) trigonelline to flooding stress. Left panel is for leaf tissues (solid symbols) and right panel is for root tissues (open symbols). The relative abundance of each metabolite is in units of mAU/s. Within lineages, means ± SE are reported and significant differences among treatments are indicated with different letters (<span class="html-italic">p</span> ≤ 0.05; based on one-way ANOVA and Tukey pairwise-comparison tests with uncorrected <span class="html-italic">p</span> values).</p>
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<p>Responses of (<b>a</b>) jasmonic acid, (<b>b</b>) methyl jasmonate and (<b>c</b>) methyl dihydrojasmonate to herbivore stress. Left panel is for leaf tissues (solid symbols) and right panel is for root tissues (open symbols). The relative abundance of each metabolite is in units of mAU/s. Within lineages, significant differences among treatments are indicated with different letters (<span class="html-italic">p</span> ≤ 0.05; based on one-way ANOVA and Tukey pairwise-comparison tests with uncorrected <span class="html-italic">p</span> values).</p>
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