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21 pages, 12271 KiB  
Article
Detection of Marine Oil Spill from PlanetScope Images Using CNN and Transformer Models
by Jonggu Kang, Chansu Yang, Jonghyuk Yi and Yangwon Lee
J. Mar. Sci. Eng. 2024, 12(11), 2095; https://doi.org/10.3390/jmse12112095 - 19 Nov 2024
Viewed by 391
Abstract
The contamination of marine ecosystems by oil spills poses a significant threat to the marine environment, necessitating the prompt and effective implementation of measures to mitigate the associated damage. Satellites offer a spatial and temporal advantage over aircraft and unmanned aerial vehicles (UAVs) [...] Read more.
The contamination of marine ecosystems by oil spills poses a significant threat to the marine environment, necessitating the prompt and effective implementation of measures to mitigate the associated damage. Satellites offer a spatial and temporal advantage over aircraft and unmanned aerial vehicles (UAVs) in oil spill detection due to their wide-area monitoring capabilities. While oil spill detection has traditionally relied on synthetic aperture radar (SAR) images, the combined use of optical satellite sensors alongside SAR can significantly enhance monitoring capabilities, providing improved spatial and temporal coverage. The advent of deep learning methodologies, particularly convolutional neural networks (CNNs) and Transformer models, has generated considerable interest in their potential for oil spill detection. In this study, we conducted a comprehensive and objective comparison to evaluate the suitability of CNN and Transformer models for marine oil spill detection. High-resolution optical satellite images were used to optimize DeepLabV3+, a widely utilized CNN model; Swin-UPerNet, a representative Transformer model; and Mask2Former, which employs a Transformer-based architecture for both encoding and decoding. The results of cross-validation demonstrate a mean Intersection over Union (mIoU) of 0.740, 0.840 and 0.804 for all the models, respectively, indicating their potential for detecting oil spills in the ocean. Additionally, we performed a histogram analysis on the predicted oil spill pixels, which allowed us to classify the types of oil. These findings highlight the considerable promise of the Swin Transformer models for oil spill detection in the context of future marine disaster monitoring. Full article
(This article belongs to the Special Issue Remote Sensing Applications in Marine Environmental Monitoring)
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<p>Examples of image processing steps: (<b>a</b>) original satellite images, (<b>b</b>) images after gamma correction and histogram adjustment, and (<b>c</b>) labeled images.</p>
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<p>Flowchart of this study, illustrating the processes of labeling, modeling, optimization, and evaluation using the DeepLabV3+, Swin-UPerNet, and Mask2Former models [<a href="#B23-jmse-12-02095" class="html-bibr">23</a>,<a href="#B24-jmse-12-02095" class="html-bibr">24</a>,<a href="#B25-jmse-12-02095" class="html-bibr">25</a>].</p>
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<p>Concept of the 5-fold cross-validation in this study.</p>
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<p>Examples of image data augmentation using the Albumentations library. The example images include random 90-degree rotation, horizontal flip, vertical flip, optical distortion, grid distortion, RGB shift, and random brightness/contrast adjustment.</p>
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<p>Randomly selected examples from fold 1, including PlanetScope RGB images, segmentation labels, and predictions from DeepLabV3+ (DL), Swin-UPerNet (Swin), and Mask2Former (M2F).</p>
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<p>Randomly selected examples from fold 2, including PlanetScope RGB images, segmentation labels, and predictions from DeepLabV3+ (DL), Swin-UPerNet (Swin), and Mask2Former (M2F).</p>
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<p>Randomly selected examples from fold 3, including PlanetScope RGB images, segmentation labels, and predictions from DeepLabV3+ (DL), Swin-UPerNet (Swin), and Mask2Former (M2F).</p>
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<p>Randomly selected examples from fold 4, including PlanetScope RGB images, segmentation labels, and predictions from DeepLabV3+ (DL), Swin-UPerNet (Swin), and Mask2Former (M2F).</p>
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<p>Randomly selected examples from fold 5, including PlanetScope RGB images, segmentation labels, and predictions from DeepLabV3+ (DL), Swin-UPerNet (Swin), and Mask2Former (M2F).</p>
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<p>Thick oil layers with a dark black tone: histogram distribution graph and box plot of oil spill pixels extracted from the labels, DeepLabV3+, Swin-UPerNet, and Mask2Former. The <span class="html-italic">x</span>-axis values represent the digital numbers (DNs) from PlanetScope images. (<b>a</b>) Oil mask, (<b>b</b>) histogram, and (<b>c</b>) box plot.</p>
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<p>Thin oil layers with a bright silver tone: histogram distribution graph and box plot of oil spill pixels extracted from the labels, DeepLabV3+, Swin-UPerNet, and Mask2Former. The <span class="html-italic">x</span>-axis values represent the digital numbers (DNs) from PlanetScope images. (<b>a</b>) Oil mask, (<b>b</b>) histogram, and (<b>c</b>) box plot.</p>
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<p>Thin oil layers with a bright rainbow tone: histogram distribution graph and box plot of oil spill pixels extracted from the labels, DeepLabV3+, Swin-UPerNet, and Mask2Former. The <span class="html-italic">x</span>-axis values represent the digital numbers (DNs) from PlanetScope images. (<b>a</b>) Oil mask, (<b>b</b>) histogram, and (<b>c</b>) box plot.</p>
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22 pages, 12163 KiB  
Article
Assessing the Use of Electrical Resistivity for Monitoring Crude Oil Contaminant Distribution in Unsaturated Coastal Sands Under Varying Salinity
by Margaret A. Adeniran, Michael A. Oladunjoye and Kennedy O. Doro
Geosciences 2024, 14(11), 308; https://doi.org/10.3390/geosciences14110308 - 14 Nov 2024
Viewed by 520
Abstract
Monitoring crude oil spills in coastal areas is challenging due to limitations in traditional in situ methods. Electrical resistivity imaging (ERI) offers a high-resolution approach to monitoring the subsurface spatial distribution of crude oil, but its effectiveness in highly-resistive, unsaturated coastal sands with [...] Read more.
Monitoring crude oil spills in coastal areas is challenging due to limitations in traditional in situ methods. Electrical resistivity imaging (ERI) offers a high-resolution approach to monitoring the subsurface spatial distribution of crude oil, but its effectiveness in highly-resistive, unsaturated coastal sands with varying salinity remains unexplored. This study assessed the effectiveness of ERI for monitoring crude oil spills in sandy soil using a 200 × 60 × 60 cm 3D sandbox filled with medium-fine-grained sand under unsaturated conditions. Two liters of crude oil were spilled under controlled conditions and monitored for 48 h using two surface ERI transects with 98 electrodes spaced every 2 cm and a dipole–dipole electrode array. The influence of varying salinity was simulated by varying the pore-fluid conductivities at four levels (0.6, 20, 50, and 85 mS/cm). After 48 h, the results show a percentage resistivity increase of 980%, 280%, 142%, and 70% for 0.6, 20, 50, and 85 mS/cm, respectively. The crude oil migration patterns varied with porewater salinity as higher salinity enhanced the crude oil retention at shallow depth. High salinity produces a smaller resistivity contrast, thus limiting the sensitivity of ERI in detecting the crude oil contaminant. These findings underscore the need to account for salinity variations when designing remediation strategies, as elevated salinity may restrict crude oil migration, resulting in localized contaminations. Full article
(This article belongs to the Section Geophysics)
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<p>(<b>a</b>) Experimental design of the sandbox showing an inflow and outflow chamber on the left and right sides; (<b>b</b>) Laboratory setup of the sandbox and the geophysical measurements with the cables connected to 98 electrodes. The electrodes are spaced 2 cm apart along a 198 cm profile length.</p>
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<p>Two-dimensional resistivity inversion results for (<b>a</b>) unsaturated sand with a concentration of (0.6 mS/cm), iteration no. = 3, RMS = 1.12; (<b>b</b>) unsaturated salt-impacted sand with a concentration of (20 mS/cm), iteration no. = 3, RMS = 1; and (<b>c</b>) unsaturated salt-impacted sand with a concentration of (50 mS/cm), iteration no. = 3, RMS = 1.2; (<b>d</b>) unsaturated salt-impacted sand with concentration of (85 mS/cm), iteration no = 3, RMS = 1.5.</p>
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<p>Two-dimensional resistivity inversion result taken across Profile 1 and Profile 2 for unsaturated sand during the crude oil spillage experiment. Five separate measurements were taken at different times for over 49.15 h using the dipole–dipole array. The red box at the top of the profile shows the crude oil spill surface location between x = 60 cm and x = 75 cm. The white-dashed lines show the left and right boundaries of the crude oil contaminant front.</p>
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<p>Two-dimensional resistivity inversion results across Profiles 1 and 2 for unsaturated salt-impacted sand with a salinity of 20 mS/cm during the crude oil spill experiment. Five separate measurements were taken at different times for over 49.15 h using the dipole–dipole array. The red box at the top of the profiles show the crude oil spill surface location between x = 60 cm and x = 75 cm. The white-dashed lines show the left and right boundaries of the crude oil contaminant front.</p>
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<p>Two-dimensional resistivity inversion results taken across Profiles 1 and 2 for unsaturated salt-impacted sand with a salt concentration of 50 mS/cm during the crude oil spill experiment. Five separate measurements were taken at different times for over 49.15 h using a dipole–dipole array. The red box at the top of the profile shows the crude oil spill surface location between x = 60 cm and x = 75 cm. The white-dashed lines show the left and right boundaries of the crude oil contaminant front.</p>
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<p>Two-dimensional resistivity inversion results taken across Profiles 1 and 2 for unsaturated salt-impacted sand with a salt concentration of 85 mS/cm during the crude oil spill experiment. Five separate measurements were taken at different times for over 49.15 h using a dipole–dipole array. The red box at the top of the profile shows the crude oil spill surface location between x = 60 cm and x = 75 cm. The white-dashed lines show the left and right boundaries of the crude oil contaminant front.</p>
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<p>Two-dimensional time-lapse inversion results showing the percentage difference in an unsaturated sand with 0.6 mS/cm concentration, from 0 h to 49.15 h using a dipole–dipole array. The red box at the top of the profile shows the crude oil spill surface location between x = 60 cm and x = 75 cm.</p>
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<p>Two-dimensional time-lapse inversion results showing the percentage difference in an unsaturated salt-impacted sand with salt concentration of 20 mS/cm from 0 h to 49.15 h using a dipole–dipole array. The red box at the top of the profile shows the crude oil spill surface location between x = 60 cm and x = 75 cm.</p>
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<p>Two-dimensional time-lapse inversion result showing the percentage difference in an unsaturated salt-impacted sand with salt concentration of 50 mS/cm from 0 h to 49.15 h using a dipole–dipole array. The red box at the top of the profile shows the crude oil spill surface location between x = 60 cm and x = 75 cm.</p>
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<p>Two-dimensional time-lapse inversion results showing the percentage difference in an unsaturated salt-impacted sand with salt concentration of 85 mS/cm from 0 h to 49.15 h using a dipole–dipole array. The red box at the top of the profile shows the crude oil spill surface location between x = 60 cm and x = 75 cm.</p>
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<p>Scattered plots showing variations in percentage difference in resistivity with depth for an unsaturated sand extracted from inverted resistivity model for (<b>A1</b>–<b>A4</b>) 0.6 mS/cm, at x = 0.5 m, 0.9 m, 1.1 m, and 1.3 m, respectively; (<b>B1</b>–<b>B4</b>) 20 mS/cm, at x = 0.5 m, 0.9 m, 1.1 m, and 1.3 m, respectively; (<b>C1</b>–<b>C4</b>) 50 mS/cm at x = 0.5 m, 0.9 m, 1.1 m, and 1.3 m, respectively; and (<b>D1</b>–<b>D4</b>) 85 mS/cm at x = 0.5 m, 0.9 m, 1.1 m, and 1.3 m, respectively.</p>
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29 pages, 3631 KiB  
Review
Review on Hardware Devices and Software Techniques Enabling Neural Network Inference Onboard Satellites
by Lorenzo Diana and Pierpaolo Dini
Remote Sens. 2024, 16(21), 3957; https://doi.org/10.3390/rs16213957 - 24 Oct 2024
Viewed by 878
Abstract
Neural networks (NNs) have proven their ability to deal with many computer vision tasks, including image-based remote sensing such as the identification and segmentation of hyperspectral images captured by satellites. Often, NNs run on a ground system upon receiving the data from the [...] Read more.
Neural networks (NNs) have proven their ability to deal with many computer vision tasks, including image-based remote sensing such as the identification and segmentation of hyperspectral images captured by satellites. Often, NNs run on a ground system upon receiving the data from the satellite. On the one hand, this approach introduces a considerable latency due to the time needed to transmit the satellite-borne images to the ground station. On the other hand, it allows the employment of computationally intensive NNs to analyze the received data. Low-budget missions, e.g., CubeSat missions, have computation capability and power consumption requirements that may prevent the deployment of complex NNs onboard satellites. These factors represent a limitation for applications that may benefit from a low-latency response, e.g., wildfire detection, oil spill identification, etc. To address this problem, in the last few years, some missions have started adopting NN accelerators to reduce the power consumption and the inference time of NNs deployed onboard satellites. Additionally, the harsh space environment, including radiation, poses significant challenges to the reliability and longevity of onboard hardware. In this review, we will show which hardware accelerators, both from industry and academia, have been found suitable for onboard NN acceleration and the main software techniques aimed at reducing the computational requirements of NNs when addressing low-power scenarios. Full article
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<p>The main products featuring the Google Coral TPU. Image taken from [<a href="#B45-remotesensing-16-03957" class="html-bibr">45</a>].</p>
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<p>On the left, Loris architecture. On the right, the camera and multiplexing electronic sub-module. Images taken from [<a href="#B57-remotesensing-16-03957" class="html-bibr">57</a>].</p>
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<p>The architecture of CloudSaNet-1. Image taken from [<a href="#B69-remotesensing-16-03957" class="html-bibr">69</a>].</p>
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<p>HW and SW inference flow on the MPSoC. Image taken from [<a href="#B71-remotesensing-16-03957" class="html-bibr">71</a>].</p>
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<p>Cloud screening neural network architecture. Image taken from [<a href="#B93-remotesensing-16-03957" class="html-bibr">93</a>].</p>
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<p>HO-ShipNet architecture. Image taken from [<a href="#B100-remotesensing-16-03957" class="html-bibr">100</a>].</p>
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<p>PL and PS architecture developed for the HO-ShipNet. Image taken from [<a href="#B100-remotesensing-16-03957" class="html-bibr">100</a>].</p>
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<p>Architecture of the anomaly detection pipeline proposed in [<a href="#B105-remotesensing-16-03957" class="html-bibr">105</a>]. Image taken from [<a href="#B105-remotesensing-16-03957" class="html-bibr">105</a>].</p>
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15 pages, 2289 KiB  
Technical Note
Detection of Complex Formations in an Inland Lake from Sentinel-2 Images Using Atmospheric Corrections and a Fully Connected Deep Neural Network
by Damianos F. Mantsis, Anastasia Moumtzidou, Ioannis Lioumbas, Ilias Gialampoukidis, Aikaterini Christodoulou, Alexandros Mentes, Stefanos Vrochidis and Ioannis Kompatsiaris
Remote Sens. 2024, 16(20), 3913; https://doi.org/10.3390/rs16203913 - 21 Oct 2024
Viewed by 566
Abstract
The detection of complex formations, initially suspected to be oil spills, is investigated using atmospherically corrected multispectral satellite images and deep learning techniques. Several formations have been detected in an inland lake in Northern Greece. Four atmospheric corrections (ACOLITE, iCOR, Polymer, and C2RCC) [...] Read more.
The detection of complex formations, initially suspected to be oil spills, is investigated using atmospherically corrected multispectral satellite images and deep learning techniques. Several formations have been detected in an inland lake in Northern Greece. Four atmospheric corrections (ACOLITE, iCOR, Polymer, and C2RCC) that are specifically designed for water applications are examined and implemented on Sentinel-2 multispectral satellite images to eliminate the influence of the atmosphere. Out of the four algorithms, iCOR and ACOLITE are able to depict the formations sufficiently; however, the latter is chosen for further processing due to fewer uncertainties in the depiction of these formations as anomalies across the multispectral range. Furthermore, a number of formations are annotated at the pixel level for the 10 m bands (red, green, blue, and NIR), and a deep neural network (DNN) is trained and validated. Our results show that the four-band configuration provides the best model for the detection of these complex formations. Despite not being necessarily related to oil spills, studying these formations is crucial for environmental monitoring, pollution detection, and the advancement of remote sensing techniques. Full article
(This article belongs to the Section Ocean Remote Sensing)
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<p>Schematic showing the work flow of our methodology.</p>
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<p>North–south cross-section of the 18 January 2021 formation, showing the remote sensing reflectance in all available bands after atmospheric corrections have been applied. For ACOLITE, all corrected bands are displayed, and for iCOR, only the 10 m bands are displayed.</p>
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<p>Visualization of the 18 January 2021 formation with B5 (560 nm) after C2RCC, iCOR, Polymer, and ACOLITE corrections have been implemented. Note that the color bar is not the same for all images to improve the direct comparison of formation characteristics after different atmospheric corrections have been applied.</p>
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<p>Visualization of the 18 January 2021 formation with NIR (833 nm) after C2RCC, iCOR, Polymer, and ACOLITE corrections have been implemented. Note that for C2RCC, we plot the 865 nm band, given that the NIR band is not available. Lack of data in the polymer illustration indicates that the polymer algorithm overestimates the correction resulting in a negative <math display="inline"><semantics> <msub> <mi>R</mi> <mrow> <mi>r</mi> <mi>s</mi> </mrow> </msub> </semantics></math>, and therefore is masked out.</p>
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<p>Visualization of the 30 December 2017 formation with B4 (665 nm) after C2RCC, iCOR, Polymer, and ACOLITE corrections have been implemented. Note that the color bar scale is lower for C2RCC. The feature in the upper right corner represents land.</p>
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<p>(<b>a</b>) False color image where three patches of different sizes (30 December 2017) are “puzzled together” to form one of the patches that is chosen for annotation, (<b>b</b>) formation annotation, (<b>c</b>) DNN prediction after ACOLITE is applied, and (<b>d</b>) DNN prediction without ACOLITE. For (<b>b</b>–<b>d</b>) oil spill pixels appear with yellow.</p>
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<p>(<b>a</b>) False color image of one of the formations (18 January 2021) chosen for annotation, (<b>b</b>) formation annotation, (<b>c</b>) DNN prediction after ACOLITE is applied, and (<b>d</b>) DNN prediction without ACOLITE. For (<b>b</b>–<b>d</b>) oil spill pixels appear with yellow.</p>
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<p>Red–NIR <math display="inline"><semantics> <msub> <mi>R</mi> <mrow> <mi>r</mi> <mi>s</mi> </mrow> </msub> </semantics></math> scatterplot for the formation and clear water pixels that are annotated and used for the DNN training.</p>
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<p>Schematic showing the DNN in three different configurations corresponding to the three types of experiments: (<b>a</b>) Red-NIR, (<b>b</b>) Green-NIR, and (<b>c</b>) 4-Bands.</p>
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<p>(<b>a</b>) Sentinel-2 false color image (green–red–NIR) showing the oil spill case for the 27 February 2017, (<b>b</b>) zoomed area in yellow box, (<b>c</b>) DNN prediction.</p>
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21 pages, 18455 KiB  
Article
Marine Oil Pollution Monitoring Based on a Morphological Attention U-Net Using SAR Images
by Lena Chang, Yi-Ting Chen, Ching-Min Cheng, Yang-Lang Chang and Shang-Chih Ma
Sensors 2024, 24(20), 6768; https://doi.org/10.3390/s24206768 - 21 Oct 2024
Viewed by 671
Abstract
This study proposed an improved full-scale aggregated MobileUNet (FA-MobileUNet) model to achieve more complete detection results of oil spill areas using synthetic aperture radar (SAR) images. The convolutional block attention module (CBAM) in the FA-MobileUNet was modified based on morphological concepts. By introducing [...] Read more.
This study proposed an improved full-scale aggregated MobileUNet (FA-MobileUNet) model to achieve more complete detection results of oil spill areas using synthetic aperture radar (SAR) images. The convolutional block attention module (CBAM) in the FA-MobileUNet was modified based on morphological concepts. By introducing the morphological attention module (MAM), the improved FA-MobileUNet model can reduce the fragments and holes in the detection results, providing complete oil spill areas which were more suitable for describing the location and scope of oil pollution incidents. In addition, to overcome the inherent category imbalance of the dataset, label smoothing was applied in model training to reduce the model’s overconfidence in majority class samples while improving the model’s generalization ability. The detection performance of the improved FA-MobileUNet model reached an mIoU (mean intersection over union) of 84.55%, which was 17.15% higher than that of the original U-Net model. The effectiveness of the proposed model was then verified using the oil pollution incidents that significantly impacted Taiwan’s marine environment. Experimental results showed that the extent of the detected oil spill was consistent with the oil pollution area recorded in the incident reports. Full article
(This article belongs to the Section Sensing and Imaging)
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<p>Oil spill images from the dataset. Cyan, red, brown, green, and black correspond to oil spills, lookalikes, ships, land, and sea surface, respectively. (<b>a</b>) Original SAR image; (<b>b</b>) ground truth data.</p>
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<p>The structure of the improved FA-MobileUNet model.</p>
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<p>The structure of the FA module of stage 3.</p>
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<p>The structure of the MAM.</p>
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<p>The training process of the improved FA-MobileUNet model. (<b>a</b>) Accuracy. (<b>b</b>) Loss.</p>
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<p>The segmentation results of different semantic segmentation models. (<b>a</b>) SAR image. (<b>b</b>) Ground truth data. (<b>c</b>) U-Net model. (<b>d</b>) LinkNet model. (<b>e</b>) PSPNet model. (<b>f</b>) DeepLabv2 model. (<b>g</b>) DeepLabv3+ model. (<b>h</b>) FA-MobileUNet model. (<b>i</b>) Improved FA-MobileUNet model. Black, cyan, and red represent the sea surface, oil spills, and lookalikes, respectively.</p>
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<p>The segmentation results of different semantic segmentation models. (<b>a</b>) SAR image. (<b>b</b>) Ground truth data. (<b>c</b>) U-Net model. (<b>d</b>) LinkNet model. (<b>e</b>) PSPNet model. (<b>f</b>) DeepLabv2 model. (<b>g</b>) DeepLabv3+ model. (<b>h</b>) FA-MobileUNet model. (<b>i</b>) Improved FA-MobileUNet model. Black, cyan, and red represent the sea surface, oil spills, and lookalikes, respectively.</p>
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<p>The areas of oil pollution incidents in Taiwan. Regions A–C are located near the Kaohsuing Port, Xiaoliuqiu Island and Taichung Port, respectively.</p>
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<p>Oil spill detection results caused by a shipwreck. (<b>a</b>) SAR image; (<b>b</b>) oil spill detection results (oil spills: cyan, lookalikes: red, and ships: brown).</p>
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<p>Oil spill detection results in Xiaoliuqiu Island. (<b>a</b>) SAR image. (<b>b</b>) Oil spill detection results (oil spills: cyan, and ships: brown).</p>
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<p>Oil spill detection results in Kenting National Park. (<b>a</b>) SAR image. (<b>b</b>) Oil spill detection results (oil spills: cyan, and ships: brown).</p>
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<p>Comparison of the segmentation results by the proposed model combined with the original and modified CBAM, respectively. (<b>a</b>) SAR image; (<b>b</b>) ground truth data; (<b>c</b>) the FA-MobileUNet model using original CBAM; (<b>d</b>) the improved FA-MobileUNet model using modified CBAM (with 1 iteration of the closing operation). (<b>e</b>) The improved FA-MobileUNet model using modified CBAM (with 2 iterations of the closing operation). (<b>f</b>) The improved FA-MobileUNet model using modified CBAM (with 3 iterations of the closing operation). Black, cyan, red, and brown represent the sea surface, oil spills, lookalikes, and ships, respectively.</p>
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<p>Comparison of the segmentation results by the proposed model combined with the original and modified CBAM, respectively. (<b>a</b>) SAR image; (<b>b</b>) ground truth data; (<b>c</b>) the FA-MobileUNet model using original CBAM; (<b>d</b>) the improved FA-MobileUNet model using modified CBAM (with 1 iteration of the closing operation). (<b>e</b>) The improved FA-MobileUNet model using modified CBAM (with 2 iterations of the closing operation). (<b>f</b>) The improved FA-MobileUNet model using modified CBAM (with 3 iterations of the closing operation). Black, cyan, red, and brown represent the sea surface, oil spills, lookalikes, and ships, respectively.</p>
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<p>Tracking ships suspected of discharging oil spills using SAR and AIS data. (<b>a</b>) SAR image. (<b>b</b>) Oil spill detection results (oil spills: cyan, and ships: brown). (<b>c</b>) Ship trajectories provided by AIS (in orange dotted line). (<b>d</b>) Trajectory of suspected oil-discharging ship.</p>
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<p>Tracking ships suspected of discharging oil spills using SAR and AIS data. (<b>a</b>) SAR image. (<b>b</b>) Oil spill detection results (oil spills: cyan, and ships: brown). (<b>c</b>) Ship trajectories provided by AIS (in orange dotted line). (<b>d</b>) Trajectory of suspected oil-discharging ship.</p>
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19 pages, 9028 KiB  
Article
Revolutionizing Ocean Cleanup: A Portuguese Case Study with Unmanned Vehicles Fighting Spills
by Nuno Pessanha Santos, Ricardo Moura, Teresa Lourenço Antunes and Victor Lobo
Environments 2024, 11(10), 224; https://doi.org/10.3390/environments11100224 - 13 Oct 2024
Viewed by 1280
Abstract
It is of the utmost importance for every country to monitor and control maritime pollution within its exclusive economic zone (EEZ). The European Maritime Safety Agency (EMSA) has developed and implemented the CleanSeaNet (CSN) satellite monitoring system to aid in the surveillance and [...] Read more.
It is of the utmost importance for every country to monitor and control maritime pollution within its exclusive economic zone (EEZ). The European Maritime Safety Agency (EMSA) has developed and implemented the CleanSeaNet (CSN) satellite monitoring system to aid in the surveillance and control of hydrocarbon and hazardous substance spills in the ocean. This system’s primary objective is to alert European Union (EU) coastal states to potential spills within their EEZs, enabling them to take the necessary legal and operational actions. To reduce operational costs and increase response capability, the feasibility of implementing a national network (NN) of unmanned vehicles (UVs), both surface and aerial, was explored using a Portuguese case study. The following approach and analysis can be easily generalized to other case studies, bringing essential knowledge to the field. Analyzing oil spill alert events in the Portuguese EEZ between 2017 and 2021 and performing a strengths, weaknesses, opportunities, and threats (SWOT) analysis, essential information has been proposed for the optimal location of an NN of UVs. The study results demonstrate that integrating spill alerts at sea with UVs may significantly improve response time, costs, and personnel involvement, making maritime pollution combat actions more effective. Full article
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Graphical abstract

Graphical abstract
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<p>Simplified diagram of the proposed approach for using a network of UVs for maritime pollution combat operations.</p>
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<p><span class="html-italic">Tekever</span> company AR5 UAV [<a href="#B85-environments-11-00224" class="html-bibr">85</a>] (<b>left</b>) and <span class="html-italic">Elbit Systems</span> company <span class="html-italic">Silver Marlin</span> USV [<a href="#B88-environments-11-00224" class="html-bibr">88</a>] (<b>right</b>).</p>
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<p>Density of maritime traffic near Portugal in 2022 [<a href="#B94-environments-11-00224" class="html-bibr">94</a>]. Regions with lower traffic are represented in lighter shades of red, while regions with higher traffic are shown in darker red.</p>
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<p>The Portuguese EEZ, encompassing the mainland, Azores, and Madeira, is represented by orange polygons, while the region delimitations are shown in green [<a href="#B96-environments-11-00224" class="html-bibr">96</a>].</p>
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<p>Alerts for oil spills in Portuguese waters from 2017 to 2021, visualized as circles whose sizes correspond to the potential spill area. Different colors indicate various clusters of spill incidents.</p>
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<p>Alerts for oil spills near the Portuguese mainland from 2017 to 2021, visualized as circles representing the potential spill area, with sizes corresponding to the area. Different colors indicate various clusters of spill incidents.</p>
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<p>Alerts for oil spills near the Azores and Madeira islands from 2017 to 2021, visualized as circles that represent the potential spill area, with sizes reflecting the scale of the spill. Different colors indicate distinct clusters of spill incidents.</p>
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<p>Oil spill alerts, represented as blue dots, that occurred in Portuguese waters from 2017 to 2021.</p>
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<p>Blue circles represent the coverage areas of potential USV bases, while red circles indicate the coverage areas of potential UAV bases near the Portuguese mainland and the Azores and Madeira islands.</p>
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<p>Search and rescue incidents in the Portuguese EEZ between 2013 and 2021. Red: aerial accidents; green: sinking; blue: flooding; yellow: alerts outside the Portuguese search and rescue area; light blue: breakdowns; pink: collisions, black: strandings; brown: medical assistance; light orange: false alerts; light pink: man overboard; gray: missing persons; dark yellow: bridge falls; green: towing and lighter; blue: telemedical assistance services.</p>
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17 pages, 13470 KiB  
Article
Hydrocarbonoclastic Biofilm-Based Microbial Fuel Cells: Exploiting Biofilms at Water-Oil Interface for Renewable Energy and Wastewater Remediation
by Nicola Lovecchio, Roberto Giuseppetti, Lucia Bertuccini, Sandra Columba-Cabezas, Valentina Di Meo, Mario Figliomeni, Francesca Iosi, Giulia Petrucci, Michele Sonnessa, Fabio Magurano and Emilio D’Ugo
Biosensors 2024, 14(10), 484; https://doi.org/10.3390/bios14100484 - 8 Oct 2024
Viewed by 868
Abstract
Microbial fuel cells (MFCs) represent a promising technology for sustainable energy generation, which leverages the metabolic activities of microorganisms to convert organic substrates into electrical energy. In oil spill scenarios, hydrocarbonoclastic biofilms naturally form at the water–oil interface, creating a distinct environment for [...] Read more.
Microbial fuel cells (MFCs) represent a promising technology for sustainable energy generation, which leverages the metabolic activities of microorganisms to convert organic substrates into electrical energy. In oil spill scenarios, hydrocarbonoclastic biofilms naturally form at the water–oil interface, creating a distinct environment for microbial activity. In this work, we engineered a novel MFC that harnesses these biofilms by strategically positioning the positive electrode at this critical junction, integrating the biofilm’s natural properties into the MFC design. These biofilms, composed of specialized hydrocarbon-degrading bacteria, are vital in supporting electron transfer, significantly enhancing the system’s power generation. Next-generation sequencing and scanning electron microscopy were used to characterize the microbial community, revealing a significant enrichment of hydrocarbonoclastic Gammaproteobacteria within the biofilm. Notably, key genera such as Paenalcaligenes, Providencia, and Pseudomonas were identified as dominant members, each contributing to the degradation of complex hydrocarbons and supporting the electrogenic activity of the MFCs. An electrochemical analysis demonstrated that the MFC achieved a stable power output of 51.5 μW under static conditions, with an internal resistance of about 1.05 kΩ. The system showed remarkable long-term stability, which maintained consistent performance over a 5-day testing period, with an average daily energy storage of approximately 216 mJ. Additionally, the MFC effectively recovered after deep discharge cycles, sustaining power output for up to 7.5 h before requiring a recovery period. Overall, the study indicates that MFCs based on hydrocarbonoclastic biofilms provide a dual-functionality system, combining renewable energy generation with environmental remediation, particularly in wastewater treatment. Despite lower power output compared to other hydrocarbon-degrading MFCs, the results highlight the potential of this technology for autonomous sensor networks and other low-power applications, which required sustainable energy sources. Moreover, the hydrocarbonoclastic biofilm-based MFC presented here offer significant potential as a biosensor for real-time monitoring of hydrocarbons and other contaminants in water. The biofilm’s electrogenic properties enable the detection of organic compound degradation, positioning this system as ideal for environmental biosensing applications. Full article
(This article belongs to the Special Issue Microbial Biosensor: From Design to Applications)
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<p>(<b>a</b>) Schematic representation of the 100-L MFC showing the placement of electrodes, Nafion panels, and diesel layer. (<b>b</b>) Photograph of the MFC during its construction, illustrating the assembly of the plexiglass panels and the Nafion panels. The positions where the positive and negative electrodes will subsequently be mounted are indicated.</p>
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<p>Experimental setup for long-term performance evaluations, including the MFC, EH4295 board, electrolytic capacitor, resistor, and acquisition board.</p>
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<p>SEM micrographs of the membranous layer that develops at the oil–water interface of the MFC (3BF1; one out of nine samples): (<b>a</b>) The membranous layer above a lipid phase (*) where rod-shaped bacteria are clearly visible, embedded within the layer and aggregated on its surface (arrows), on the water side. (<b>b</b>) Lipid side of the layer with rod-shaped structures visible under the membranous layer (inset).</p>
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<p>Diagram showing the percentage of microbial Classes (<b>a</b>) and Genera (<b>b</b>) found in the initial inoculum and in the MFC at the end of the experiment. For the MFC data, the values reported in the pie charts were obtained by averaging the analyses performed on the 9 samples collected.</p>
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<p>Phylogenetic tree illustrating the evolutionary relationships among the predominant microbial families, genera, and species identified in the MFC. The tree structure combines family-level (**), genus-level (*), and species-level insights, providing a comprehensive overview of the microbial community composition.</p>
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<p>(<b>a</b>) Voltage (left y-axis) and current (right y-axis) measurements of the MFC. The resistances used for each discharging step are reported in the figure. The data are obtained by averaging 5 measurements performed at 1-h intervals on the same day. (<b>b</b>) Peak power output as a function of current. Experimental data are shown as symbols, while the fitting curve is represented by the dashed line. Error bars, both for current and power values, indicate 5 different measurements performed at 1-h intervals on the same day.</p>
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<p>(<b>a</b>) Voltage (left axis) and current (right axis) evolution of the MFC during the static output power characterization. (<b>b</b>) Static power output as a function of current. Experimental data are shown as symbols, with the fitting curve represented by the dashed line. Error bars, both for current and power values, indicate 5 different measurements performed at 1-h intervals on the same day.</p>
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<p>(<b>a</b>) Voltage (left y-axis) and corresponding current (right y-axis) across the 100 kΩ resistor over a 5-day period, showing 8-h discharges between 16-h recovery cycles. The EH4295 board switches off after approximately 7.5 h, indicating the deep discharge status. The inset shows the integrated electric charge value for each day. (<b>b</b>) Power output of the MFC immediately after the 8-h measurement cycles (purple symbols with blue fitting curve) and one hour later (green symbols with red fitting curve and corresponding equation). (<b>c</b>) Zoomed view of the power output immediately after the 8-h measurement cycles and related fitting equation. Error bars, both for current and power values and for both curves, indicate the 5 different acquisitions performed in the considered days of measurements.</p>
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18 pages, 853 KiB  
Article
Detection of Nitrate-Reducing/Denitrifying Bacteria from Contaminated and Uncontaminated Tallgrass Prairie Soil: Limitations of PCR Primers
by Samer M. AbuBakr, Fares Z. Najar and Kathleen E. Duncan
Microorganisms 2024, 12(10), 1981; https://doi.org/10.3390/microorganisms12101981 - 30 Sep 2024
Viewed by 566
Abstract
Contamination of soil by spills of crude oil and oilfield brine is known to affect the species composition and functioning of soil microbial communities. However, the effect of such contamination on nitrogen cycling, an important biogeochemical cycle in tallgrass prairie soil, is less [...] Read more.
Contamination of soil by spills of crude oil and oilfield brine is known to affect the species composition and functioning of soil microbial communities. However, the effect of such contamination on nitrogen cycling, an important biogeochemical cycle in tallgrass prairie soil, is less well known. Detecting nitrate-reducing (NR) and denitrifying (DN) bacteria via PCR amplification of the genes essential for these processes depends on how well PCR primers match the sequences of these bacteria. In this study, we enriched for NR and DN bacteria from oil/brine tallgrass prairie soil contaminated 5–10 years previously versus those cultured from uncontaminated soil, confirmed the capacity of 75 strains isolated from the enrichments to reduce nitrate and/nitrite, then screened the strains with primers specific to seven nitrogen cycle functional genes. The strains comprised a phylogenetically diverse group of NR and DN bacteria, with proportionately more γ-Proteobacteria in oil-contaminated sites and more Bacilli in brine-contaminated sites, suggesting some residual effect of the contaminants on the NR and DN species distribution. Around 82% of the strains shown to reduce nitrate/nitrite would not be identified as NR and DN bacteria by the battery of NR and DN primers used. Our results indicate an urgent need to expand the NR/DN functional gene primer database by first identifying novel NR/DN strains through their capacity to reduce nitrate/nitrite. Full article
(This article belongs to the Section Environmental Microbiology)
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<p>Taxonomic Affiliation of Strains. The number of strains affiliated with different higher taxonomic level bacterial groups found in oil-, brine-, and prairie-soils. The 16S rRNA gene sequences of seventy-five strains were classified by the RDP Classifier tool. Brine: isolated from sites contaminated primarily by oil field brine but also by crude oil (10:1 vol/vol), G5 and G7. Oil: isolated from sites contaminated by crude oil, J6-F, J6-NF, and LF. Prairie: isolated from uncontaminated sites, G5P, G7P, J6P, and LFP. “All” indicates the distribution of the 75 strains isolated after enrichment in nitrate broth, and “NR/DN” indicates the distribution of 54 strains confirmed as nitrate/nitrite reducers after incubation in nitrate broth as described in Materials and Methods.</p>
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<p>Phylogenetic tree of the 16S rRNA gene of 75 bacterial strains isolated from tallgrass prairie soils with respect to related sequences. There were 29 OTUs (indicated in bold letters) at the 98% level of similarity. One strain representing each OTU was used for phylogenetic analysis. The number of strains contained in each OTU is included between parentheses next to the representative strain. The numbers of strains of NR (nitrate-reducing) bacteria, DN (nitrite-reducing) bacteria, and None (strains that did not reduce nitrate or nitrite) are also included next to the total number of strains included in the OTU. The tree is constructed from approximately 1400 bp 16S rRNA gene sequence using the neighbor-joining algorithm. One thousand bootstrap replications were performed; only values greater than 700 are shown. (<b>a</b>) (Bar: 0.02 nucleotide substitutions per nucleotide) shows the γ-Proteobacteria where the sequence of <span class="html-italic">Ensifer adhaerens</span> strain WJB69 (KU877644) was included as the outgroup, while (<b>b</b>) (Bar: 0.03 nucleotide substitutions per nucleotide) shows the remaining groups where the sequence of <span class="html-italic">Archaeoglobus infectus</span> DSM 18877 strain Arc51 (NR_028166) was included as the outgroup.</p>
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<p>Phylogenetic tree of the 16S rRNA gene of 75 bacterial strains isolated from tallgrass prairie soils with respect to related sequences. There were 29 OTUs (indicated in bold letters) at the 98% level of similarity. One strain representing each OTU was used for phylogenetic analysis. The number of strains contained in each OTU is included between parentheses next to the representative strain. The numbers of strains of NR (nitrate-reducing) bacteria, DN (nitrite-reducing) bacteria, and None (strains that did not reduce nitrate or nitrite) are also included next to the total number of strains included in the OTU. The tree is constructed from approximately 1400 bp 16S rRNA gene sequence using the neighbor-joining algorithm. One thousand bootstrap replications were performed; only values greater than 700 are shown. (<b>a</b>) (Bar: 0.02 nucleotide substitutions per nucleotide) shows the γ-Proteobacteria where the sequence of <span class="html-italic">Ensifer adhaerens</span> strain WJB69 (KU877644) was included as the outgroup, while (<b>b</b>) (Bar: 0.03 nucleotide substitutions per nucleotide) shows the remaining groups where the sequence of <span class="html-italic">Archaeoglobus infectus</span> DSM 18877 strain Arc51 (NR_028166) was included as the outgroup.</p>
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21 pages, 10576 KiB  
Article
Prediction and Management of the Groundwater Environmental Pollution Impact in Anning Refinery in Southern China
by Xiaoqi Fang, Shiyao Tang, Zhenru Niu and Juntao Tong
Water 2024, 16(19), 2713; https://doi.org/10.3390/w16192713 - 24 Sep 2024
Viewed by 696
Abstract
Anning Refinery, a large-scale joint venture in southern China, possesses significant potential in regard to polluting local groundwater environments due to its extensive petroleum raw materials. This study aims to mitigate the substantial risks associated with oil spills and prevent consequential groundwater pollution [...] Read more.
Anning Refinery, a large-scale joint venture in southern China, possesses significant potential in regard to polluting local groundwater environments due to its extensive petroleum raw materials. This study aims to mitigate the substantial risks associated with oil spills and prevent consequential groundwater pollution by developing a robust groundwater flow model using the MODFLOW module in GMS software that aligns closely with natural and pumping test conditions. Furthermore, by integrating the MT3DMS model, a groundwater solute transport model is constructed and calibrated using sodium chloride tracer dispersion data. Notably, the wax hydrocracking unit and aviation coal finished product tank area are identified as key pollution sources warranting attention. By considering local constraints such as karst collapse, ground subsidence, and single-well water output capacity, the study introduces a tailored groundwater pollution management model. The research simulates various scenarios of petroleum pollutant migration in groundwater and proposes multi-objective emergency response optimization plans. In Scenario 1, simulations show that petroleum pollutants migrate within the unconfined aquifer and enter the karst aquifer as low-concentration plumes over an extended period. Detection of these plumes in karst water monitoring wells indicates upstream unconfined aquifer contamination at higher concentrations, necessitating immediate activation of the nearest monitoring or emergency wells in both layers. Conversely, in Scenario 2, pollutants reside briefly in the unconfined aquifer before entering the karst aquifer at relatively higher concentrations. Here, low-efficiency pollutant discharge through unconfined aquifer monitoring wells prompts the activation of nearby karst aquifer monitoring or emergency wells for effective pollution control. This model underscores the necessity for proactive monitoring and validates the efficacy of coupled numerical modeling in understanding pollutant behavior, offering valuable insights into pollution control scenario assessments. In summary, the study emphasizes the importance of targeted monitoring and emergency protocols, demonstrating the benefits of integrated modeling approaches in industrial areas prone to pollution risks, and provides critical theoretical and practical guidance for groundwater protection and pollution management, offering transferable insights for similar industrial settings worldwide. Full article
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<p>Hydrogeological profile.</p>
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<p>Distribution map of groundwater monitoring points in the refinery area.</p>
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<p>Conceptual model of the unconsolidated layer.</p>
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<p>Conceptualization of Boundary Conditions.</p>
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<p>Error bar illustration.</p>
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<p>Natural field fitting graph.</p>
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<p>Pollution source location distribution map.</p>
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<p>Contaminant plume on the 360th day in Scenario 1.</p>
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<p>Scenario 2, contaminant plume at 75 days.</p>
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<p>Migration of the pollution plume under continuous pumping conditions at JC02.</p>
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<p>Trend chart of the center concentration of pollutants at the pollution source when pumping directly from JC02.</p>
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<p>The movement of the pollution plume under continuous pumping conditions at the pollution source.</p>
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<p>Migration of the pollution plume under continuous pumping conditions at JC03.</p>
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18 pages, 3626 KiB  
Article
Detection of Oil Spill in SAR Image Using an Improved DeepLabV3+
by Jiahao Zhang, Pengju Yang and Xincheng Ren
Sensors 2024, 24(17), 5460; https://doi.org/10.3390/s24175460 - 23 Aug 2024
Viewed by 790
Abstract
Oil spill SAR images are characterized by high noise, low contrast, and irregular boundaries, which lead to the problems of overfitting and insufficient capturing of detailed features of the oil spill region in the current method when processing oil spill SAR images. An [...] Read more.
Oil spill SAR images are characterized by high noise, low contrast, and irregular boundaries, which lead to the problems of overfitting and insufficient capturing of detailed features of the oil spill region in the current method when processing oil spill SAR images. An improved DeepLabV3+ model is proposed to address the above problems. First, the original backbone network Xception is replaced by the lightweight MobileNetV2, which significantly improves the generalization ability of the model while drastically reducing the number of model parameters and effectively addresses the overfitting problem. Further, the spatial and channel Squeeze and Excitation module (scSE) is introduced and the joint loss function of Bce + Dice is adopted to enhance the sensitivity of the model to the detailed parts of the oil spill area, which effectively solves the problem of insufficient capture of the detailed features of the oil spill area. The experimental results show that the mIOU and F1-score of the improved model in an oil spill region in the Gulf of Mexico reach 80.26% and 88.66%, respectively. In an oil spill region in the Persian Gulf, the mIOU and F1-score reach 81.34% and 89.62%, respectively, which are better than the metrics of the control model. Full article
(This article belongs to the Special Issue Applications of Synthetic-Aperture Radar (SAR) Imaging and Sensing)
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<p>Structure of SAR image oil spill detection model.</p>
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<p>Structure of the scSE module.</p>
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<p>Structure of scSE–MobileNetV2: (<b>a</b>) Inverted residual block with a stride of 1; (<b>b</b>) Inverted residual block with a stride of 2.</p>
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<p>Structure of scSE–ASPP.</p>
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<p>Oil spill SAR images from the ALOS satellite: (<b>a</b>) with filename 10777_sat in dataset; (<b>b</b>) with filename 10794_sat; (<b>c</b>) with filename 11148_sat; (<b>d</b>) with filename 11064_sat; (<b>e</b>) with filename 11168_sat.</p>
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<p>Prediction results of different backbone networks in the Gulf of Mexico oil spill area: (<b>a</b>) SAR image; (<b>b</b>) Ground truth; (<b>c</b>) Xception–DeepLabV3+ model; (<b>d</b>) MobileNetV2–DeepLabV3+ model.</p>
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<p>Prediction results of different backbone networks in the Persian Gulf oil spill area: (<b>a</b>) SAR image; (<b>b</b>) Ground truth; (<b>c</b>) Xception–DeepLabV3+ model; (<b>d</b>) MobileNetV2–DeepLabV3+ model.</p>
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<p>Prediction results of different models in the Gulf of Mexico oil spill area: (<b>a</b>) SAR image; (<b>b</b>) Ground truth; (<b>c</b>) ABCNet; (<b>d</b>) CGNet; (<b>e</b>) DFANet; (<b>f</b>) LEDNet; (<b>g</b>) MANet; (<b>h</b>) UNet; (<b>i</b>) Ours.</p>
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<p>Prediction results of different models in the Persian Gulf oil spill area: (<b>a</b>) SAR image; (<b>b</b>) Ground truth; (<b>c</b>) ABCNet; (<b>d</b>) CGNet; (<b>e</b>) DFANet; (<b>f</b>) LEDNet; (<b>g</b>) MANet; (<b>h</b>) UNet; (<b>i</b>) Ours.</p>
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32 pages, 7438 KiB  
Article
Monitoring of Spatio-Temporal Variations of Oil Slicks via the Collocation of Multi-Source Satellite Images
by Tran Vu La, Ramona-Maria Pelich, Yu Li, Patrick Matgen and Marco Chini
Remote Sens. 2024, 16(16), 3110; https://doi.org/10.3390/rs16163110 - 22 Aug 2024
Viewed by 940
Abstract
Monitoring oil drift by integrating multi-source satellite imagery has been a relatively underexplored practice due to the limited time-sampling of datasets. However, this limitation has been mitigated by the emergence of new satellite constellations equipped with both Synthetic Aperture Radar (SAR) and optical [...] Read more.
Monitoring oil drift by integrating multi-source satellite imagery has been a relatively underexplored practice due to the limited time-sampling of datasets. However, this limitation has been mitigated by the emergence of new satellite constellations equipped with both Synthetic Aperture Radar (SAR) and optical sensors. In this manuscript, we take advantage of multi-temporal and multi-source satellite imagery, incorporating SAR (Sentinel-1 and ICEYE-X) and optical data (Sentinel-2/3 and Landsat-8/9), to provide insights into the spatio-temporal variations of oil spills. We also analyze the impact of met–ocean conditions on oil drift, focusing on two specific scenarios: marine floating oil slicks off the coast of Qatar and oil spills resulting from a shipwreck off the coast of Mauritius. By overlaying oils detected from various sources, we observe their short-term and long-term evolution. Our analysis highlights the finding that changes in oil structure and size are influenced by strong surface winds, while surface currents predominantly affect the spread of oil spills. Moreover, to detect oil slicks across different datasets, we propose an innovative unsupervised algorithm that combines a Bayesian approach used to detect oil and look-alike objects with an oil contours approach distinguishing oil from look-alikes. This algorithm can be applied to both SAR and optical data, and the results demonstrate its ability to accurately identify oil slicks, even in the presence of oil look-alikes and under varying met–ocean conditions. Full article
(This article belongs to the Special Issue Marine Ecology and Biodiversity by Remote Sensing Technology)
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<p>Footprints of multi-sensor and multi-temporal images for observing oil spills. (<b>a</b>) Offshore Qatar, as covered by Sentinel-1 (28 March 2021, 14:33:06), Sentinel-2 (27 March 2021, 06:56:21), and Sentinel-3 (28 March 2021, 06:34:43). (<b>b</b>) Mauritius Island, as covered by Sentinel-1 IW (10 August 2020, 01:37:55), Sentinel-1 EW (10 August 2020, 14:36:16), and ICEYE-X (11 August 2020, 11:12:41).</p>
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<p>Oil slicks with low NRCS (dark objects) observed on the extracted scenes of (<b>a</b>) a Sentinel-1 image, 28 March 2021, 14:33:06; and (<b>b</b>) an ICEYE-X image, 6 August 2020, 18:33:23.</p>
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<p>Oil slick observed on the extracted scene of a Sentinel-2 image, offshore Qatar, 3 September 2021, 06:56:21: (<b>a</b>) RGB image; (<b>b</b>) oil index (in dB) calculated from the averages of RGB bands.</p>
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<p>Oil slick observed on the Sentinel-3 image, offshore Qatar, 28 March 2021, 06:34:43: (<b>a</b>) Sentinel-3 OLCI tristimulus image (Sentinel-3 User Handbook); (<b>b</b>) T865 variable (in dB) from Sentinel-3 Level-2 data.</p>
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<p>Flowchart of oil-slick detection from Sentinel-1/ICEYE-X SAR, Sentinel-2/Landsat-8 optical, and Sentinel-3 visible/near-infrared data.</p>
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<p>An example of the HSBA algorithm’s results for a Sentinel-1 SAR image, 5 July 2021, 02:23:25. One can find a detailed description of the HSBA algorithm in [<a href="#B33-remotesensing-16-03110" class="html-bibr">33</a>]. The purple box displays the histogram of backscattering values for the complete scene, in which the bimodality is less noticeable, making it difficult to identify T and BG. The red box presents the backscattering value histogram for the areas selected by HSBA, where oil slick is present, clearly highlighting a bimodal behavior. The green box is a histogram of the sea’s backscattering value.</p>
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<p>Floating-oil-slick detection for Case #Q1, 27–28 March 2021. (<b>a</b>–<b>c</b>) Extracted scenes from Sentinel-2 (27 March, 06:56:21), Sentinel-3 (28 March, 06:34:43), and Sentinel-1 (28 March, 14:33:06) images, respectively. (<b>Left</b>) Sentinel-2 RGB, Sentinel-3 OLCI tristimulus, and Sentinel-1 NRCS images, respectively. (<b>Right</b>) Oil slicks detected from Sentinel-2/3/1 images (<b>left</b>), respectively.</p>
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<p>Collocation of Sentinel-2/3/1 images (Case #Q1, 27–28 March 2021) for observations of oil-slick evolution in periods of about (<b>a</b>) 24 h (between Sentinel-2/3), (<b>b</b>) 8 h (between Sentinel-3/1), and (<b>c</b>) 32 h (between Sentinel-2/1).</p>
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<p>Surface wind and current speed and direction (indicated by the arrows), corresponding to the extracted Sentinel-2/3/1 scenes (<a href="#remotesensing-16-03110-f007" class="html-fig">Figure 7</a>a–c), respectively. (<b>i</b>) ERA-5 wind vectors for (<b>a</b>) 06:00, 27 March 2021; (<b>b</b>) 06:00, 28 March; and (<b>c</b>) 14:00, 28 March. (<b>ii</b>) CMEMS current vectors for (<b>d</b>) 06:30, 27 March; (<b>e</b>) 06:30, 28 March; and (<b>f</b>) 14:30, 28 March. (<b>iii</b>) Mean values of wind and current fields from 06:00, 27 March, to 14:00 28 March.</p>
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<p>Surface wind and current speed and direction (indicated by the arrows), corresponding to the extracted Sentinel-2/3/1 scenes (<a href="#remotesensing-16-03110-f007" class="html-fig">Figure 7</a>a–c), respectively. (<b>i</b>) ERA-5 wind vectors for (<b>a</b>) 06:00, 27 March 2021; (<b>b</b>) 06:00, 28 March; and (<b>c</b>) 14:00, 28 March. (<b>ii</b>) CMEMS current vectors for (<b>d</b>) 06:30, 27 March; (<b>e</b>) 06:30, 28 March; and (<b>f</b>) 14:30, 28 March. (<b>iii</b>) Mean values of wind and current fields from 06:00, 27 March, to 14:00 28 March.</p>
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<p>Floating-oil-slick detection for Case #Q2, 5–6 July 2021. (<b>a</b>–<b>c</b>) Extracted scenes from Sentinel-1 (July 5, 02:23:25), Sentinel-2 (5 July, 06:56:21), and Landsat-8 (6 July, 06:58:26), respectively. (<b>Left</b>) Sentinel-1 NRCS, Sentinel-2 RGB, and Landsat-8 RGB, respectively. (<b>Right</b>) Oil slicks detected from Sentinel-1/2 and Landsat-8 images (<b>left</b>), respectively.</p>
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<p>Floating-oil-slick detection for Case #Q2, 5–6 July 2021. (<b>a</b>–<b>c</b>) Extracted scenes from Sentinel-1 (July 5, 02:23:25), Sentinel-2 (5 July, 06:56:21), and Landsat-8 (6 July, 06:58:26), respectively. (<b>Left</b>) Sentinel-1 NRCS, Sentinel-2 RGB, and Landsat-8 RGB, respectively. (<b>Right</b>) Oil slicks detected from Sentinel-1/2 and Landsat-8 images (<b>left</b>), respectively.</p>
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<p>Collocation of Sentinel-1/2 and Landsat-8 images (Case #Q2, 5–6 July 2021) for observations of oil-slick evolution after about (<b>a</b>) 4 h (between Sentinel-1/2), (<b>b</b>) 24 h (between Sentinel-2 and Landsat-8), and (<b>c</b>) 28 h (between Sentinel-1 and Landsat-8).</p>
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<p>Collocation of Sentinel-1/2 and Landsat-8 images (Case #Q2, 5–6 July 2021) for observations of oil-slick evolution after about (<b>a</b>) 4 h (between Sentinel-1/2), (<b>b</b>) 24 h (between Sentinel-2 and Landsat-8), and (<b>c</b>) 28 h (between Sentinel-1 and Landsat-8).</p>
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<p>Surface wind and current speed and direction (indicated by the arrows), corresponding to the extracted Sentinel-1/2 and Landsat-8 scenes (<a href="#remotesensing-16-03110-f010" class="html-fig">Figure 10</a>a–c), respectively. (<b>i</b>) ERA-5 wind vectors for (<b>a</b>) 02:00, 5 July 2021; (<b>b</b>) 07:00, 5 July; and (<b>c</b>) 07:00, 6 July. (<b>ii</b>) CMEMS current vectors on (<b>d</b>) 02:30, 5 July; (<b>e</b>) 07:30, 5 July; and (<b>f</b>) 07:30, 6 July. (<b>iii</b>) Mean values of wind and current fields from 02:00, 5 July, to 09:00, 6 July.</p>
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<p>Surface wind and current speed and direction (indicated by the arrows), corresponding to the extracted Sentinel-1/2 and Landsat-8 scenes (<a href="#remotesensing-16-03110-f010" class="html-fig">Figure 10</a>a–c), respectively. (<b>i</b>) ERA-5 wind vectors for (<b>a</b>) 02:00, 5 July 2021; (<b>b</b>) 07:00, 5 July; and (<b>c</b>) 07:00, 6 July. (<b>ii</b>) CMEMS current vectors on (<b>d</b>) 02:30, 5 July; (<b>e</b>) 07:30, 5 July; and (<b>f</b>) 07:30, 6 July. (<b>iii</b>) Mean values of wind and current fields from 02:00, 5 July, to 09:00, 6 July.</p>
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<p>Floating-oil-slick detection for Case #Q3, 3 September 2021. (<b>a</b>,<b>c</b>) Three extracted scenes (#S1–3, <b>left</b>–<b>right</b>) from the Sentinel-1 NRCS (3 September, 02:23:54) and Sentinel-2 RGB (3 September, 06:56:21) images, respectively. (<b>b</b>,<b>d</b>) Oil slicks detected from the Sentinel-1/2 scenes #S1–3, respectively.</p>
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<p>Floating-oil-slick detection for Case #Q3, 3 September 2021. (<b>a</b>,<b>c</b>) Three extracted scenes (#S1–3, <b>left</b>–<b>right</b>) from the Sentinel-1 NRCS (3 September, 02:23:54) and Sentinel-2 RGB (3 September, 06:56:21) images, respectively. (<b>b</b>,<b>d</b>) Oil slicks detected from the Sentinel-1/2 scenes #S1–3, respectively.</p>
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<p>Collocation of Sentinel-1/2 images (Case #Q3, 3 September 2021) for observations of oil-slick evolution after about 4 h. (<b>a</b>–<b>c</b>) Oil slicks detected from the extracted Sentinel-1/2 scenes #S1–3 (<a href="#remotesensing-16-03110-f013" class="html-fig">Figure 13</a>), respectively.</p>
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<p>Collocation of Sentinel-1/2 images (Case #Q3, 3 September 2021) for observations of oil-slick evolution after about 4 h. (<b>a</b>–<b>c</b>) Oil slicks detected from the extracted Sentinel-1/2 scenes #S1–3 (<a href="#remotesensing-16-03110-f013" class="html-fig">Figure 13</a>), respectively.</p>
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<p>(<b>Left</b>–<b>Right</b>) Surface wind and current speed and direction (indicated by the arrows), corresponding to the extracted Sentinel-1/2 scenes #S1–3, respectively. (<b>a</b>) ERA-5 wind vectors for 02:00, 3 September 2021. (<b>b</b>) CMEMS current vectors for 02:30, 3 September 2021. (<b>c</b>) Mean values of wind and current fields from 02:00 to 07:00, 3 September.</p>
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<p>(<b>Left</b>–<b>Right</b>) Surface wind and current speed and direction (indicated by the arrows), corresponding to the extracted Sentinel-1/2 scenes #S1–3, respectively. (<b>a</b>) ERA-5 wind vectors for 02:00, 3 September 2021. (<b>b</b>) CMEMS current vectors for 02:30, 3 September 2021. (<b>c</b>) Mean values of wind and current fields from 02:00 to 07:00, 3 September.</p>
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<p>Oil-slick observation on Sentinel-1 IW/EW and ICEYE-X images, offshore Mauritius, 10–11 August 2020. (<b>a</b>–<b>c</b>) Extracted scenes corresponding to the MV Wakashio oil spill, from Sentinel-1 IW (10 August, 01:37:55); Sentinel-1 EW (10 August, 14:36:16); and ICEYE-X (11 August, 11:12:41), respectively. (<b>d</b>–<b>f</b>) Oil spill, as detected by HSBA from the extracted scenes (<b>a</b>–<b>c</b>).</p>
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<p>Surface wind and current speed and direction (indicated by the arrows), corresponding to the extracted Sentinel-1 IW, EW, and ICEYE-X scenes (<a href="#remotesensing-16-03110-f016" class="html-fig">Figure 16</a>a–c), respectively. (<b>i</b>) ERA-5 wind vectors (<b>a</b>) 01:00, 10 August 2020, and (<b>b</b>) 14:00 and (<b>c</b>) 11:00, 11 August. (<b>ii</b>) CMEMS current vectors on (<b>d</b>) 01:30, 10 August, and (<b>e</b>) 14:30 and (<b>f</b>) 11:30, 11 August. (<b>iii</b>) Mean values of wind and current fields from 01:00, 10 August, to 11:00, 11 August.</p>
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<p>(<b>i</b>,<b>ii</b>) Comparison between the oil slicks identified from the Sentinel-2 (scene S#3–<a href="#remotesensing-16-03110-f013" class="html-fig">Figure 13</a>c) and Sentinel-1 (scene S#2–<a href="#remotesensing-16-03110-f013" class="html-fig">Figure 13</a>a) images, respectively, for Case Q#3, 3 September 2021, by only HSBA (<a href="#remotesensing-16-03110-f018" class="html-fig">Figure 18</a>i–a, <a href="#remotesensing-16-03110-f018" class="html-fig">Figure 18</a>ii–d), those identified from HSBA plus oil contour (<a href="#remotesensing-16-03110-f018" class="html-fig">Figure 18</a>i–b, <a href="#remotesensing-16-03110-f018" class="html-fig">Figure 18</a>ii–e), and those manually segmented (<a href="#remotesensing-16-03110-f018" class="html-fig">Figure 18</a>i–c, <a href="#remotesensing-16-03110-f018" class="html-fig">Figure 18</a>ii–f).</p>
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<p>Comparison between the oil slicks (<b>a</b>) detected by HSBA plus oil contour and (<b>b</b>) those manually segmented, from the Sentinel-2 image, 5 July 2021, 06:56:21. (<b>c</b>) Difference between the detected pixels (<b>a</b>) and ground truth (<b>b</b>).</p>
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<p>Comparison between the oil slicks (<b>a</b>) detected by HSBA plus oil contour and (<b>b</b>) those manually segmented, from the Landsat-8 image, 6 July 2021, 06:58:26. (<b>c</b>) Difference between the detected pixels (<b>a</b>) and ground truth (<b>b</b>).</p>
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22 pages, 9248 KiB  
Article
Developing a Comprehensive Oil Spill Detection Model for Marine Environments
by Farkhod Akhmedov, Rashid Nasimov and Akmalbek Abdusalomov
Remote Sens. 2024, 16(16), 3080; https://doi.org/10.3390/rs16163080 - 21 Aug 2024
Cited by 1 | Viewed by 1873
Abstract
Detecting oil spills in marine environments is crucial for avoiding environmental damage and facilitating rapid response efforts. In this study, we propose a robust method for oil spill detection leveraging state-of-the-art (SOTA) deep learning techniques. We constructed an extensive dataset comprising images and [...] Read more.
Detecting oil spills in marine environments is crucial for avoiding environmental damage and facilitating rapid response efforts. In this study, we propose a robust method for oil spill detection leveraging state-of-the-art (SOTA) deep learning techniques. We constructed an extensive dataset comprising images and frames extracted from video sourced from Google, significantly augmenting the dataset through frame extraction techniques. Each image is meticulously labeled to ensure high-quality training data. Utilizing the Yolov8 segmentation model, we trained our oil spill detection model to accurately identify and segment oil spills in ocean environments. K-means and Truncated Linear Stretching algorithms are combined with trained model weight to increase model detection accuracy. The model demonstrated exceptional performance, yielding high detection accuracy and precise segmentation capabilities. Our results indicate that this approach is highly effective for real-time oil spill detection, offering a promising tool for environmental monitoring and disaster management. In training metrics, the model reached over 97% accuracy in 100 epochs. In evaluation, model achieved its best detection rates by 94% accuracy in F1, 93.9% accuracy in Precision, and 95.5% [email protected] accuracy in Recall curves. Full article
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<p>YOLO-v8 architecture. The design integrates a modified CSP Darknet53 framework, where the CSPLayer from YOLOv5 is substituted with the C2F module. To speed up computation, an SPPF module is utilized for pooling features into a standardized map. Each convolution module incorporates a batch normalization (BN) layer and SiLU activation.</p>
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<p>Proposed oil spill detection approach flowchart.</p>
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<p>Internet source oil spill image examples.</p>
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<p>Video frame generated image example with diverse scenarios.</p>
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<p>Lookalike images in ocean environment.</p>
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<p>Image annotation using LabelMe.</p>
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<p>Image processing example in single image case.</p>
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<p>RGB color change before and after image processing.</p>
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<p>Example detections while model training with oil spill images.</p>
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<p>Example detection while model validating with oil spill images.</p>
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<p>Data distribution with class match.</p>
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<p>Confusion matrix (<b>a</b>) and collegram (<b>b</b>).</p>
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<p>Model training and validation losses, metrics with comparative mAP scores.</p>
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<p>Line curve representation of metrics.</p>
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<p>Oil spill detection test results.</p>
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16 pages, 5724 KiB  
Article
Automatic Identification of Sunken Oil in Homogeneous Information Perturbed Environment through Fusion Image Enhancement with Convolutional Neural Network
by Jinfeng Cao, Mingzhong Gao, Jihong Guo, Haichun Hao, Yongjun Zhang, Peng Liu and Nan Li
Sustainability 2024, 16(15), 6665; https://doi.org/10.3390/su16156665 - 4 Aug 2024
Viewed by 923
Abstract
With the development of the marine oil industry, leakage accidents are one of the most serious problems threatening maritime and national security. The spilt crude oil can float and sink in the water column, posing a serious long-term threat to the marine environment. [...] Read more.
With the development of the marine oil industry, leakage accidents are one of the most serious problems threatening maritime and national security. The spilt crude oil can float and sink in the water column, posing a serious long-term threat to the marine environment. High-frequency sonar detection is currently the most efficient method for identifying sunken oil. However, due to the complicated environment of the deep seabed and the interference of the sunken oil signals with homogeneous information, sonar detection data are usually difficult to interpret, resulting in low efficiency and a high failure rate. Previous works have focused on features designed by experts according to the detection environments and the identification of sunken oil targets regardless of the feature extraction step. To automatically identify sunken oil targets without a prior knowledge of the complex seabed conditions during the image acquisition process for sonar detection, a systematic framework is contrived for identifying sunken oil targets that combines image enhancement with a convolutional neural network (CNN) classifier for the final decision on sunken oil targets examined in this work. Case studies are conducted using datasets obtained from a sunken oil release experiment in an outdoor water basin. The experimental results show that (i) the method can effectively distinguish between the sunken oil target, the background, and the interference target; (ii) it achieved an identification accuracy of 83.33%, outperforming feature-based recognition systems, including SVM; and (iii) it provides important information about sunken oil such as the location of the leak, which is useful for decision-making in emergency response to oil spills at sea. This line of research offers a more robust and, above all, more objective option for the difficult task of automatically identifying sunken oils under complex seabed conditions. Full article
(This article belongs to the Section Waste and Recycling)
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<p>Fusion image enhancement using the CNN method.</p>
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<p>Gaussian filtering. I–IV are identified targets from Gaussian filtering results: (<b>a</b>) original image; (<b>b</b>) filtered image.</p>
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<p>Histogram equalization.</p>
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<p>Binary image result after applying threshold segmentation.</p>
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<p>Extraction of the edge of the target area.</p>
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<p>Extraction of the target area.</p>
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<p>Schematic diagram of experimental setup.</p>
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<p>Sonar detection image.</p>
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<p>Illustrative examples of cropped image samples. (<b>a</b>) Submerged oil; (<b>b</b>) interference targets; (<b>c</b>) background.</p>
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<p>Loss curves of training and validation sets during training.</p>
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<p>Comparison of filters (<b>a</b>) before training; (<b>b</b>) after training.</p>
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<p>Precision and recall rates for each category.</p>
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<p>Examples of identification results for test images. Targets marked in red boxes are identified sunken oil. Targets marked in yellow boxes are false alarms. Digits 1-4 are target numbers. (<b>a</b>) Original images; (<b>b</b>) identification results.</p>
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14 pages, 12697 KiB  
Communication
Deep Learning-Based Detection of Oil Spills in Pakistan’s Exclusive Economic Zone from January 2017 to December 2023
by Abdul Basit, Muhammad Adnan Siddique, Salman Bashir, Ehtasham Naseer and Muhammad Saquib Sarfraz
Remote Sens. 2024, 16(13), 2432; https://doi.org/10.3390/rs16132432 - 2 Jul 2024
Viewed by 1196
Abstract
Oil spillages on a sea’s or an ocean’s surface are a threat to marine and coastal ecosystems. They are mainly caused by ship accidents, illegal discharge of oil from ships during cleaning and oil seepage from natural reservoirs. Synthetic-Aperture Radar (SAR) has proved [...] Read more.
Oil spillages on a sea’s or an ocean’s surface are a threat to marine and coastal ecosystems. They are mainly caused by ship accidents, illegal discharge of oil from ships during cleaning and oil seepage from natural reservoirs. Synthetic-Aperture Radar (SAR) has proved to be a useful tool for analyzing oil spills, because it operates in all-day, all-weather conditions. An oil spill can typically be seen as a dark stretch in SAR images and can often be detected through visual inspection. The major challenge is to differentiate oil spills from look-alikes, i.e., low-wind areas, algae blooms and grease ice, etc., that have a dark signature similar to that of an oil spill. It has been noted over time that oil spill events in Pakistan’s territorial waters often remain undetected until the oil reaches the coastal regions or it is located by concerned authorities during patrolling. A formal remote sensing-based operational framework for oil spills detection in Pakistan’s Exclusive Economic Zone (EEZ) in the Arabian Sea is urgently needed. In this paper, we report the use of an encoder–decoder-based convolutional neural network trained on an annotated dataset comprising selected oil spill events verified by the European Maritime Safety Agency (EMSA). The dataset encompasses multiple classes, viz., sea surface, oil spill, look-alikes, ships and land. We processed Sentinel-1 acquisitions over the EEZ from January 2017 to December 2023, and we thereby prepared a repository of SAR images for the aforementioned duration. This repository contained images that had been vetted by SAR experts, to trace and confirm oil spills. We tested the repository using the trained model, and, to our surprise, we detected 92 previously unreported oil spill events within those seven years. In 2020, our model detected 26 oil spills in the EEZ, which corresponds to the highest number of spills detected in a single year; whereas in 2023, our model detected 10 oil spill events. In terms of the total surface area covered by the spills, the worst year was 2021, with a cumulative 395 sq. km covered in oil or an oil-like substance. On the whole, these are alarming figures. Full article
(This article belongs to the Special Issue Deep Learning for Satellite Image Segmentation)
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Graphical abstract

Graphical abstract
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<p>Our study area in the Arabian sea, showing the extent of Pakistan’s Area of Responsibility (AOR). It contains 240,000 km<sup>2</sup> of Exclusive Economic Zone and 50,000 km<sup>2</sup> of extended continental shelf. Background: Google Maps.</p>
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<p>The flowchart illustrates the steps followed for the processing of Ground Range Detected High-resolution (GRDH) Sentinel-1 acquisitions, including orbit correction, thermal noise removal, radiometric calibration, conversion to decibels, terrain correction and speckle filtering.</p>
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<p>Schematic representation of ReU-Net architecture for semantic segmentation. The encoder features a ResNet-101 backbone with a <math display="inline"><semantics> <mrow> <mn>7</mn> <mo>×</mo> <mn>7</mn> </mrow> </semantics></math> convolutional layer, two batch normalization layers, ReLU activation, max-pooling and 33 residual blocks. In the decoder, adhering to a UNet framework, multi-scale features are integrated via skip connections (shown in dark-blue color). The number presented on the <span class="html-italic">Res-x</span> blocks represents the number of residual blocks cascaded within. The functionalities of the residual block (<span class="html-italic">Res-B</span>) and convolutional block (<span class="html-italic">Conv-B</span>) are expanded at the bottom-right and bottom-left corners of the figure, respectively. Each layer’s function is color-coded as per the legend.</p>
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<p>Three SAR images (<b>left</b>) from 110 test SAR images, with ground truth masks (<b>center</b>) and predicted class labels (<b>right</b>) detected by ReU-Net. In columns 2 and 3, black color shows the sea surface, green color shows land area, cyan color shows an oil spill area, red color is assigned to look-alikes and brown color shows ships. The dataset was prepared by Krestenitis et al. [<a href="#B20-remotesensing-16-02432" class="html-bibr">20</a>] from the MKLab ITI-CERTH, Greece.</p>
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<p>Three SAR images (<b>top row</b>) from the test set prepared by acquiring imagery over the Arabian sea along with predicted class labels (<b>bottom row</b>) containing potential oil spills in Pakistan territorial waters. Black color shows sea surface, cyan color shows oil spill and brown color shows ships.</p>
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<p>Yearly breakdown of the oil spill incidents in Pakistan’s Exclusive Economic Zone (EEZ) from January 2017 to December 2023. Overall, 92 incidents were identified. The yearly figure for each year is stated above each bar.</p>
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<p>(<b>Top</b>): Spatial spread of the oil spills detected in Pakistan’s EEZ from January 2017 to December 2023. (<b>Bottom</b>): The size of the spills (in terms of their length) and their distance from the shoreline.</p>
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12 pages, 3531 KiB  
Communication
Experiment for Oil Spill Detection Based on Dual-Frequency QZSS Reflected Signals Using Drone-Borne GNSS-R
by Runqi Liu, Fan Gao, Cheng Jing, Xiao Li, Dongmei Song, Bin Wang, Huyu Sun, Yahui Kong, Zhenyao Zhong, Shuo Gu, Cong Yin and Weihua Bai
Remote Sens. 2024, 16(13), 2346; https://doi.org/10.3390/rs16132346 - 27 Jun 2024
Viewed by 838
Abstract
Oil spill detection plays an important role in marine environment protection. The technique of global navigation satellite system-reflectometry (GNSS-R) has the advantage of a short revisit time, which could help with timely cleanup of marine oil pollution. The conventional GNSS-R oil spill detection [...] Read more.
Oil spill detection plays an important role in marine environment protection. The technique of global navigation satellite system-reflectometry (GNSS-R) has the advantage of a short revisit time, which could help with timely cleanup of marine oil pollution. The conventional GNSS-R oil spill detection algorithm can resolve only the dielectric constant of oil based on power ratio measurements, while that of water cannot be realized. This is because the dielectric constant of water is much larger than that of oil such that the range of the equation used in the conventional algorithm is inadequate. To resolve this problem, we proposed a new algorithm containing a new equation with a larger scope, which has never been applied previously to GNSS-R oil spill detection. We derived a lookup method to resolve the dielectric constant of both oil and water. To validate our method, a drone-borne GNSS-R experiment based on dual-frequency QZSS reflection signals was conducted on 17 July 2023 using experimental pools simulating oil spills. Raw IF data in the L1 and L5 bands, collected using dual antennas and a data recorder, were processed using a software-defined receiver to deduce the power ratios and SNR of the GNSS signals. Results showed that the proposed algorithm is capable of resolving the dielectric constants of the reflected surface. In addition, the L5 signal was found to provide more detail and better contrast than the L1 C/A signal. Full article
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<p>Dielectric constant–reflectance plots computed using Equations (1) and (2). The function images are multivalued. For example, the reflectance of 0.7 in the figure corresponds to the two dielectric constants of Equation (1). A program was used to retain the portion of the dielectric constant in the range of 0.01~100 based on the actual dielectric constant of oil and water. The lower part of the curve starts with a dielectric constant of 0.01 and the upper part of the curve has a dielectric constant of 100. The two curves intersect at the coordinate origin, which has been magnified in the diagram.</p>
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<p>Basic principles in distinguishing oil and water.</p>
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<p>(<b>a</b>) The drone hovering above the experimental pools whose serial number is marked in the figure received a steady stream of data, (<b>b</b>) the reference station, and (<b>c</b>) the drone and its accessories.</p>
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<p>Geometric relationship between the drone, satellite, and reflecting surface. The arrow represents the direction of signal propagation.</p>
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<p>(<b>a</b>) Locations and heights of the drone, and (<b>b</b>) the trajectory of the reflection points and the corresponding height of the drone. The drone was in a hovering (moving) state when the distribution of the colored dots is dense (sparse). The ‘*’ represents the contours of theexperimental pools. <a href="#remotesensing-16-02346-f006" class="html-fig">Figure 6</a> and <a href="#remotesensing-16-02346-f007" class="html-fig">Figure 7</a> follow the same logic.</p>
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<p>Inversion diagram of the dielectric constant of (<b>a</b>) the L1 C/A signal and (<b>b</b>) the L5 signal.</p>
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<p>Inversion diagram of the SNR of (<b>a</b>) the L1 C/A signal and (<b>b</b>) the L5 signal.</p>
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<p>(<b>a</b>) Relationship between the dielectric constant and the flight height of the drone for the L1 C/A signal, (<b>b</b>) relationship between the SNR and the flight height of the drone for the L1 C/A signal, (<b>c</b>) relationship between the dielectric constant and the flight height of the drone for the L5 signal, and (<b>d</b>) relationship between the SNR and the flight height of the drone for the L5 signal.</p>
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