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Search Results (498)

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18 pages, 8217 KiB  
Article
Multi-Sensor Photoelectric Fire Alarm Device Implementation for Early Fire Detection in Campsites
by Wonjun Choi and Im Y. Jung
Appl. Sci. 2024, 14(21), 9965; https://doi.org/10.3390/app14219965 - 31 Oct 2024
Viewed by 445
Abstract
With the growing popularity of leisure activities such as camping and glamping, the incidence of fires at camping sites has increased. This study focuses on improving the effectiveness of photoelectric fire alarm devices by incorporating temperature and humidity data for early fire detection [...] Read more.
With the growing popularity of leisure activities such as camping and glamping, the incidence of fires at camping sites has increased. This study focuses on improving the effectiveness of photoelectric fire alarm devices by incorporating temperature and humidity data for early fire detection in confined spaces, such as campsites. This study proposes a novel multi-sensor fire alarm system that dynamically adjusts fire detection threshold values based on temperature and humidity data collected by unmanned automatic weather observation systems. The prototype, which was implemented using Raspberry Pi and multiple sensors, demonstrated approximately 20% faster fire detection speed than existing photoelectric fire alarm systems, as verified through experiments in a simulated camping environment. The proposed approach is expected to advance fire alarm systems, enabling faster and more accurate fire detection in diverse environments, particularly at campsites. Full article
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Figure 1
<p>Recent three-year fire incident statistics in campsites.</p>
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<p>CCTV footage of campsite fires [<a href="#B7-applsci-14-09965" class="html-bibr">7</a>].</p>
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<p>Sensors used in fire alarms.</p>
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<p>Linear regression between humidity and fire occurrence rate.</p>
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<p>Linear regression between temperature and fire occurrence rate.</p>
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<p>Multiple linear regression between temperature, humidity and fire occurrence rates.</p>
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<p>OLS linear regression results.</p>
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<p>Residual plot.</p>
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<p>Q–Q plot.</p>
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<p>Structure of the photoelectric fire detector of Taesanfire–Circuitry, Darkroom.</p>
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<p>Circuit diagram of the proposed multi-sensor photoelectric fire detector.</p>
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<p>Circuit configuration of the proposed multi-sensor photoelectric fire detector.</p>
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<p>Darkroom components for smoke detection by the proposed multi-sensor photoelectric fire detector.</p>
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<p>Arduino-light-photocell-CDS-light sensor.</p>
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<p>Temperature and humidity sensor, DHT11 and its inner structure.</p>
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<p>Fire alarm threshold update algorithm.</p>
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<p>Experimental Environment.</p>
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<p>Temperature variation data from DHT11.</p>
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<p>Humidity variation data from DHT11.</p>
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<p>Alarm time difference between the commercially available photoelectric fire detector and the proposed multi-sensor photoelectric fire detector.</p>
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19 pages, 5057 KiB  
Article
The Weathering of the Beech and Spruce Wood Impregnated with Pigmented Linseed Oil
by Fanni Fodor, Jakub Dömény, Péter György Horváth, Barbora Pijáková and Jan Baar
Coatings 2024, 14(11), 1374; https://doi.org/10.3390/coatings14111374 - 29 Oct 2024
Viewed by 542
Abstract
This research aimed to examine the effects of a deep impregnation technique (Royal process) and surface coating using a linseed oil-based product, enhanced with small amounts of brown and grey pigments, on the natural and artificial weathering of wood. The treated and reference [...] Read more.
This research aimed to examine the effects of a deep impregnation technique (Royal process) and surface coating using a linseed oil-based product, enhanced with small amounts of brown and grey pigments, on the natural and artificial weathering of wood. The treated and reference samples underwent natural weathering for five years and artificial weathering for 1900 h. Changes in color and surface roughness were assessed during weathering. For the artificially weathered samples, liquid water absorption was measured both before and after exposure. The impregnated and coated samples gradually lost their brown color, turning grey over time. More pronounced differences were observed during natural weathering, with the coated samples showing greater structural changes on the wood surface. In contrast, impregnated samples slowed down structural alterations compared to the reference samples. Both treatments effectively reduced water absorption before weathering, although this effect diminished after exposure. The treatments did not significantly impact the fire resistance of spruce and beechwood. Full article
(This article belongs to the Special Issue Wood Coatings: Formulation, Testing and Performance)
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Figure 1

Figure 1
<p>The depth of oil penetration in spruce (<b>above</b>) is smaller than that of beech (<b>below</b>) after impregnation. The figure shows longitudinal sections of four samples with a 20 mm thickness. The wood appears darker where the oil has penetrated.</p>
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<p>Surface discoloration of spruce (S, <b>left</b>) and beech (B, <b>right</b>) samples before and during exposure to natural weathering (from top to bottom 0 to 5 years). R—reference; IG—impregnated with grey oil; IB—impregnated with brown oil; CB—coated by brown oil.</p>
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<p>Surface discoloration of spruce (S) and beech (B) samples before and during irradiation (0–24–500–1900 h). R—reference; IG—impregnated with grey oil; IB—impregnated with brown oil; CB—coated by brown oil.</p>
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<p>Changes in lightness (<span class="html-italic">L</span>*), redness (<span class="html-italic">a</span>*), yellowness (<span class="html-italic">b</span>*), and total color difference (Δ<span class="html-italic">E</span>*) of spruce (S) and beech (B) samples during a 5-year weathering exposure. R—reference; IG—impregnated with grey oil; IB—impregnated with brown oil; CB—coated by brown oil.</p>
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<p>Color difference in treated samples (<math display="inline"><semantics> <mrow> <mo>∆</mo> <msubsup> <mrow> <mi>E</mi> </mrow> <mrow> <mi>y</mi> <mi>e</mi> <mi>a</mi> <mi>r</mi> </mrow> <mrow> <mi>*</mi> </mrow> </msubsup> </mrow> </semantics></math>) compared to the reference samples of spruce (S) and beech (B) during each year of natural weathering exposure. The actual color difference is compared to the reference sample’s color for the respective year. IG—impregnated with grey oil; IB—impregnated with brown oil; CB—coated by brown oil.</p>
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<p>Changes in lightness (<span class="html-italic">L</span>*), redness (<span class="html-italic">a</span>*), yellowness (<span class="html-italic">b</span>*), and total color difference (Δ<span class="html-italic">E</span>*) of spruce (S) and beech (B) samples during a 1900 h of artificial weathering. R—reference; IG—impregnated with grey oil; IB—impregnated with brown oil; CB—coated by brown oil.</p>
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<p>Mass change during water sorption and desorption process of spruce (S) and beech (B) samples. R—reference; IG—impregnated with grey oil; IB—impregnated with brown oil; CB—coated by brown oil.</p>
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<p>Water uptake of spruce (S) and beech (B) samples before and after artificial weathering. R—reference; IG—impregnated with grey oil; IB—impregnated with brown oil; CB—coated by brown oil.</p>
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31 pages, 16268 KiB  
Article
Effect of Biomass Burnings on Population Exposure and Health Impact at the End of 2019 Dry Season in Southeast Asia
by Hiep Duc Nguyen, Ho Quoc Bang, Nguyen Hong Quan, Ngo Xuan Quang and Tran Anh Duong
Atmosphere 2024, 15(11), 1280; https://doi.org/10.3390/atmos15111280 - 25 Oct 2024
Viewed by 477
Abstract
At the end of the dry season, from early March to early April each year, extensive agricultural biomass waste burnings occur throughout insular mainland Southeast Asia. During this biomass-burning period, smoke aerosols blanketed the whole region and were transported and dispersed by predominant [...] Read more.
At the end of the dry season, from early March to early April each year, extensive agricultural biomass waste burnings occur throughout insular mainland Southeast Asia. During this biomass-burning period, smoke aerosols blanketed the whole region and were transported and dispersed by predominant westerly and southwesterly winds to southern China, Taiwan, and as far southern Japan and the Philippines. The extensive and intense burnings coincided with some wildfires in the forests due to high temperatures, making the region one of the global hot spots of biomass fires. In this study, we focus on the effect of pollutants emitted from biomass burnings in March 2019 at the height of the burning period on the exposed population and their health impact. The Weather Research Forecast-Chemistry (WRF-Chem) model was used to predict the PM2.5 concentration over the simulating domain, and health impacts were then assessed on the exposed population in the four countries of Southeast Asia, namely Thailand, Laos, Cambodia, and Vietnam. Using the health impact based on log-linear concentration-response function and Integrated Exposure Response (IER), the results show that at the peak period of the burnings from 13 to 20 March 2019, Thailand experienced the highest impact, with an estimated 2170 premature deaths. Laos, Vietnam, and Cambodia followed, with estimated mortalities of 277, 565, and 315 deaths, respectively. However, when considering the impact per head of population, Laos exhibited the highest impact, followed by Thailand, Cambodia, and Vietnam. The results highlight the significant health impact of agricultural waste burnings in Southeast Asia at the end of the dry season. Hence, policymakers should take these into account to design measures to reduce the negative impact of widespread burnings on the exposed population in the region. Full article
(This article belongs to the Section Air Quality and Health)
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Figure 1
<p>Hot spots of biomass burnings over Southeast Asia as detected by MODIS onboard NASA Terra/Aqua satellites on some of the days when intense burnings occurred, 14 March 2019 (<b>a</b>), 16 March 2019 (<b>b</b>), 18 March 2019 (<b>c</b>), and 20 March 2019 (<b>d</b>). Smoke from fires covered most of SEA in Burma, Thailand, Laos, Cambodia, and southern Vietnam, while cloud (white) covered southern China, north and central Vietnam on these four days. The orange lines are satellite paths with time (in UTC) labelled on the line path while the dark patches are missing satellite coverage (source: NASA Worldview <a href="https://worldview.earthdata.nasa.gov/" target="_blank">https://worldview.earthdata.nasa.gov/</a> (accessed on 19 October 2024)).</p>
Full article ">Figure 1 Cont.
<p>Hot spots of biomass burnings over Southeast Asia as detected by MODIS onboard NASA Terra/Aqua satellites on some of the days when intense burnings occurred, 14 March 2019 (<b>a</b>), 16 March 2019 (<b>b</b>), 18 March 2019 (<b>c</b>), and 20 March 2019 (<b>d</b>). Smoke from fires covered most of SEA in Burma, Thailand, Laos, Cambodia, and southern Vietnam, while cloud (white) covered southern China, north and central Vietnam on these four days. The orange lines are satellite paths with time (in UTC) labelled on the line path while the dark patches are missing satellite coverage (source: NASA Worldview <a href="https://worldview.earthdata.nasa.gov/" target="_blank">https://worldview.earthdata.nasa.gov/</a> (accessed on 19 October 2024)).</p>
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<p>(<b>a</b>) Domain configuration of WRF-Chem and (<b>b</b>) topography of the domain with Truong Son Mountain range along the border of Laos and Vietnam and the location of the main cities in the region.</p>
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<p>PM<sub>2.5</sub> hourly emission (μg/m<sup>2</sup>/s) from biomass burnings in peninsular Southeast Asia on 14 March 2019 at 16:00 UTC as derived from FINN (<b>left</b>) and PM<sub>2.5</sub> daily anthropogenic emission (μg/m<sup>2</sup>/s) on 14 March 2019 as derived from EDGAR-HTAP emission dataset (<b>right</b>). Note the scale difference between the biomass burning emission and the anthropogenic emission.</p>
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<p>Population distribution in peninsular SEA (Vietnam, Thailand, Laos, and Cambodia). The two largest populated countries are Vietnam and Thailand, where population densities are highest in the metropolitan centres of Bangkok, Ho Chi Minh City, and Hanoi.</p>
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<p>Predicted AOD from WRF-Chem model on 17 March 2019 00:00 UTC and the location of AERONET sites where AOD measurements are used to validate the model (<b>above</b>) [<a href="#B9-atmosphere-15-01280" class="html-bibr">9</a>]. Similar to the predicted AOD validation at sites in [<a href="#B9-atmosphere-15-01280" class="html-bibr">9</a>], validation at the AERONET site in Fang is shown (<b>below</b>).</p>
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<p>The predicted surface wind field and ground concentration of PM<sub>2.5</sub> (μg/m<sup>3</sup>) over the simulation domain on 13, 15, 17, and 19 March 2019 at 16:00 UTC (<b>a</b>–<b>d</b>).</p>
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<p>The predicted surface wind field and ground concentration of PM<sub>2.5</sub> (μg/m<sup>3</sup>) over the simulation domain on 13, 15, 17, and 19 March 2019 at 16:00 UTC (<b>a</b>–<b>d</b>).</p>
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<p>PM<sub>2.5</sub> prediction for 13–20 March 2019 from WRF-Chem simulation with only anthropogenic emission (base case).</p>
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<p>PM<sub>2.5</sub> prediction for 13–20 March 2019 from WRF-Chem simulation with only anthropogenic emission (base case).</p>
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<p>The spatial distribution of daily PM<sub>2.5</sub> concentration for each of the six days (from 14 to 19 March 2019).</p>
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<p>Gridded mortality (persons) in SEA due to biomass burning on 13–20 March 2019 based on the Integrated Exposure Response (IER) method.</p>
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<p>Gridded mortality (persons) in SEA due to biomass burning on 13–20 March 2019 based on the Integrated Exposure Response (IER) method.</p>
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<p>Emission of CO, Black Carbon (BC), NO<sub>2</sub> and Ethane (C<sub>2</sub>H<sub>6</sub>) from biomass burnings at burning sites on 14 March 2019 at 16:00 UTC. The burning sites correspond to the hot spots, as shown in <a href="#atmosphere-15-01280-f001" class="html-fig">Figure 1</a>.</p>
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<p>Anthropogenic emission of CO, SO<sub>2</sub>, NH<sub>3</sub> and NO<sub>2</sub> in (moles/km<sup>2</sup>/hour) on 14 March 2019.</p>
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<p>The plumes of spatial distribution of daily PM<sub>2.5</sub> concentration for each of the six days (from 14 to 19 March 2019).</p>
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<p>The plumes of spatial distribution of daily PM<sub>2.5</sub> concentration for each of the six days (from 14 to 19 March 2019).</p>
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<p>Gridded mortality (persons) in SEA due to the biomass burning on 13–20 March 2019 based on log-linear concentration response method.</p>
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<p>Gridded mortality (persons) in SEA due to the biomass burning on 13–20 March 2019 based on log-linear concentration response method.</p>
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24 pages, 8975 KiB  
Article
Improving a WRF-Based High-Impact Weather Forecast System for a Northern California Power Utility
by Richard L. Carpenter, Taylor A. Gowan, Samuel P. Lillo, Scott J. Strenfel, Arthur. J. Eiserloh, Evan J. Duffey, Xin Qu, Scott B. Capps, Rui Liu and Wei Zhuang
Atmosphere 2024, 15(10), 1244; https://doi.org/10.3390/atmos15101244 - 18 Oct 2024
Viewed by 1564
Abstract
We describe enhancements to an operational forecast system based on the Weather Research and Forecasting (WRF) model for the prediction of high-impact weather events affecting power utilities, particularly conditions conducive to wildfires. The system was developed for Pacific Gas and Electric Corporation (PG&E) [...] Read more.
We describe enhancements to an operational forecast system based on the Weather Research and Forecasting (WRF) model for the prediction of high-impact weather events affecting power utilities, particularly conditions conducive to wildfires. The system was developed for Pacific Gas and Electric Corporation (PG&E) to forecast conditions in Northern and Central California for critical decision-making such as proactively de-energizing selected circuits within the power grid. WRF forecasts are routinely produced on a 2 km grid, and the results are used as input to wildfire fuel moisture, fire probability, wildfire spread, and outage probability models. This forecast system produces skillful real-time forecasts while achieving an optimal blend of model resolution and ensemble size appropriate for today’s computational resources afforded to utilities. Numerous experiments were performed with different model settings, grid spacing, and ensemble configuration to develop an operational forecast system optimized for skill and cost. Dry biases were reduced by leveraging a new irrigation scheme, while wind skill was improved through a novel approach involving the selection of Global Ensemble Forecast System (GEFS) members used to drive WRF. We hope that findings in this study can help other utilities (especially those with similar weather impacts) improve their own forecast system. Full article
(This article belongs to the Section Atmospheric Techniques, Instruments, and Modeling)
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<p>Topography of WRF outer domain and location of two nested domains. Grid spacings are 18, 6, and 2 km, respectively.</p>
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<p>WRF nested grids of 0.67 km grid spacing (shaded) that can be launched on demand during critical weather events. Each grid is 215 × 215 km.</p>
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<p>Average annual number of Diablo wind events over PG&amp;E’s service territory derived from the POMMS v3 31-year (1990–2020) reanalysis.</p>
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<p>Irrigation fraction (range 0 to 1) in the WRF Noah–MP scheme on the 2 km grid.</p>
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<p>Stations used in the validation.</p>
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<p>NCEP Global Data Assimilation System (GDAS) analysis of (<b>a</b>) 500 hPa geopotential heights (10 dam contour interval) and wind barbs, and (<b>b</b>) sea level pressure (2 hPa contour interval) and 10 m wind barbs, with areas of simulated composite radar reflectivity ≥ 20 dBZ filled, valid 27 October 2019 at 12:00 UTC. Each full wind barb represents 10 knots.</p>
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<p>As in <a href="#atmosphere-15-01244-f006" class="html-fig">Figure 6</a>, except valid 19 January 2021 at 12:00 UTC.</p>
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<p>As in <a href="#atmosphere-15-01244-f006" class="html-fig">Figure 6</a>, except valid 13 July 2021 at 12:00 UTC.</p>
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<p>As in <a href="#atmosphere-15-01244-f006" class="html-fig">Figure 6</a>, except valid 7 September 2022 at 00:00 UTC.</p>
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<p>As in <a href="#atmosphere-15-01244-f006" class="html-fig">Figure 6</a>, except valid 21 February 2023 at 18:00 UTC.</p>
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<p>As in <a href="#atmosphere-15-01244-f006" class="html-fig">Figure 6</a>, except valid 21 March 2023 at 12:00 UTC.</p>
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<p>Validation of experiments for all cases and observing networks combined. Variables shown are (<b>a</b>) all wind speeds, (<b>b</b>) wind speeds ≥ 5 m s<sup>−1</sup>, (<b>c</b>) wind speeds ≥ 10 m s<sup>−1</sup>, (<b>d</b>) temperature, and (<b>e</b>) vapor pressure deficit.</p>
Full article ">Figure 12 Cont.
<p>Validation of experiments for all cases and observing networks combined. Variables shown are (<b>a</b>) all wind speeds, (<b>b</b>) wind speeds ≥ 5 m s<sup>−1</sup>, (<b>c</b>) wind speeds ≥ 10 m s<sup>−1</sup>, (<b>d</b>) temperature, and (<b>e</b>) vapor pressure deficit.</p>
Full article ">Figure 12 Cont.
<p>Validation of experiments for all cases and observing networks combined. Variables shown are (<b>a</b>) all wind speeds, (<b>b</b>) wind speeds ≥ 5 m s<sup>−1</sup>, (<b>c</b>) wind speeds ≥ 10 m s<sup>−1</sup>, (<b>d</b>) temperature, and (<b>e</b>) vapor pressure deficit.</p>
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16 pages, 7320 KiB  
Article
Use of Low-Cost Sensors to Study Atmospheric Particulate Matter Concentrations: Limitations and Benefits Discussed through the Analysis of Three Case Studies in Palermo, Sicily
by Filippo Brugnone, Luciana Randazzo and Sergio Calabrese
Sensors 2024, 24(20), 6621; https://doi.org/10.3390/s24206621 - 14 Oct 2024
Viewed by 631
Abstract
The paper discusses the results of the concentrations of atmospheric particulate matter, in the PM2.5 and PM10 fractions, acquired by two low-cost sensors. The research was carried out from 1 July 2023 to 30 June 2024, in Palermo, Sicily. The results [...] Read more.
The paper discusses the results of the concentrations of atmospheric particulate matter, in the PM2.5 and PM10 fractions, acquired by two low-cost sensors. The research was carried out from 1 July 2023 to 30 June 2024, in Palermo, Sicily. The results obtained from two systems equipped with the same sensor model were compared. Excellent linear correlation was observed between the results, with differences in measurements falling within instrumental accuracy. Two instruments equipped with different sensors, models Novasense SDS011 and Plantower PMSA003, were placed at the same site. These were complemented by a weather station to measure meteorological parameters. Upon comparing the atmospheric particulate matter concentrations measured by the two instruments, it was observed that there was a good linear correlation for PM2.5 and a poor linear correlation for PM10. Additionally, the PMSA003 sensor appeared to consistently record higher concentrations than the SDS011 sensor. During periods influenced by natural sources and/or anthropogenic activities at the regional and/or local scale, i.e., the dispersal of Saharan sands, forest fires, and local events using fireworks, abnormal concentrations of atmospheric particulate matter were detected. Despite the inherent limitations in precision and accuracy, both low-cost instruments were able to identify periods with abnormal concentrations of atmospheric particulate matter, regardless of their source or type. Full article
(This article belongs to the Special Issue Feature Papers in Remote Sensors 2024)
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<p>Location of the study area, Base map: Google Earth. Coordinate system: WGS84 EPSG 3857. Made with Quantum Gis v. 3.36.3 “Maidenhead”, distributed under the GNU General Public License.</p>
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<p>Inovafit SDS011 (<b>a</b>) and Davis Instruments Corporation “AirLink” (<b>b</b>) air quality monitoring systems, and the Davis Instruments Corporation “Vantage Pro2” weather station (<b>c</b>) installed on the roof of the “Emilio Segré” building in “Via Archirafi no. 36” (Dipartimento di Scienze della Terra e del Mare, Università degli Studi di Palermo).</p>
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<p>(<b>a</b>) Values of atmospheric temperature (°C) and (<b>b</b>) relative humidity (%) measured by the three different instruments from 01 July 2023 to 30 June 2024: Davis Instruments Corporation “Vantage Pro2” (red), PMSA003 (green), SDS011 (blue). (<b>c</b>) Temperature differences (°C) between SDS011 and Davis Instruments Corporation “Vantage Pro2” (blue), and between PMSA003 and Davis Instruments Corporation “Vantage Pro2” (green). The dotted line represents the reference of the measured temperature values (°C) of the Davis Instruments Corporation “Vantage Pro2” weather station.</p>
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<p>Correlation of PM<sub>2.5</sub> (<b>a</b>) and PM<sub>10</sub> (<b>b</b>) concentration measurements between two different SDS011 sensors (01_SDS011 and 02_SDS011). The solid lines are the 1:1 ratio between the two different sensor readings.</p>
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<p>Correlation of PM<sub>2.5</sub> (<b>a</b>) and PM<sub>10</sub> (<b>b</b>) concentration measurements by SDS011 and PMSA003 sensors considering data from the entire sampling period (July 2023–June 2024). The solid thick lines are the 1:1 ratio between the two sensor readings. The blue dotted line represents the linear correlation line between the measurements of the two sensors.</p>
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<p>Temperature (°C), Relative Humidity (%), and Rainfall (L m<sup>−2</sup>) (<b>a</b>) measured by the Davis Instruments Corporation “Vantage Pro2”, PM<sub>2.5</sub> (<b>b</b>) and PM<sub>10</sub> (<b>c</b>) hourly arithmetic average concentrations (μg m<sup>−3</sup>) measured by the SDS011 (blue lines) and by the PMSA003 (green lines), between 15 August 2023 and 30 September 2023 in Palermo. The yellow-shaded area indicates the dispersion period of Saharan sand at the end of August 2023. The red-shaded area indicates the dispersion period of Saharan sand associated with the dispersion of ash from fires at the end of September 2023.</p>
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<p>Satellite image of Sicily taken by the satellite Moderate Resolution Imaging Spectroradiometer (MODIS)—Visible Infrared Imaging Radiometer Suite (VIIRS)—NASA S-NPP and NOAA20, on 22 September 2023. In opaque white, clouds of water vapor are visible. In semi-transparent white, dispersed in a south-east/north-west direction, are visible the ash clouds generated by the forest fires that affected various areas of northern Sicily on 22 September 2023.</p>
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<p>Correlation of PM<sub>2.5</sub> (<b>a</b>) and PM<sub>10</sub> (<b>b</b>) hourly median concentration measurements by SDS011 and PMSA003 sensors from 15 August 2023 to 30 September 2023 in Palermo. The solid thick lines are the 1:1 ratio between the two sensor readings. The blue dotted line represents the linear correlation line between the measurements of the two sensors.</p>
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<p>Hourly Temperature (°C), Relative Humidity (%), and Rainfall (L m<sup>−2</sup>) values measured by the Davis Instruments Corporation “Vantage Pro2” (<b>a</b>), and PM<sub>2.5</sub> (<b>b</b>) and PM<sub>10</sub> (<b>c</b>) 15 min arithmetic average concentrations (μg m<sup>−3</sup>) measured by the SDS011 (blue lines) and by the PMSA003 (green lines), respectively, between 25 December 2023 and 6 January 2024 in Palermo. The cyan-shaded area indicates the firework shows period.</p>
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<p>Correlation of PM<sub>2.5</sub> (<b>a</b>) and PM<sub>10</sub> (<b>b</b>) 12 h median concentration measurements by SDS011 and PMSA003 sensors from 25 December 2023 to 6 January 2024 in Palermo. The solid thick lines are the 1:1 ratio between the two sensor readings. The thin solid lines define the instrumental accuracy range (±10 μg m<sup>−3</sup>). The blue dotted line represents the linear correlation line between the measurements of the two sensors.</p>
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13 pages, 2116 KiB  
Article
Dead Fuel Moisture Content Reanalysis Dataset for California (2000–2020)
by Angel Farguell, Jack Ryan Drucker, Jeffrey Mirocha, Philip Cameron-Smith and Adam Krzysztof Kochanski
Fire 2024, 7(10), 358; https://doi.org/10.3390/fire7100358 - 9 Oct 2024
Viewed by 551
Abstract
This study presents a novel reanalysis dataset of dead fuel moisture content (DFMC) across California from 2000 to 2020 at a 2 km resolution. Utilizing a data assimilation system that integrates a simplified time-lag fuel moisture model with 10-h fuel moisture observations from [...] Read more.
This study presents a novel reanalysis dataset of dead fuel moisture content (DFMC) across California from 2000 to 2020 at a 2 km resolution. Utilizing a data assimilation system that integrates a simplified time-lag fuel moisture model with 10-h fuel moisture observations from remote automated weather stations (RAWS) allowed predictions of 10-h fuel moisture content by our method with a mean absolute error of 0.03 g/g compared to the widely used Nelson model, with a mean absolute error prediction of 0.05 g/g. For context, the values of DFMC in California are commonly between 0.05 g/g and 0.30 g/g. The presented product provides gridded hourly moisture estimates for 1-h, 10-h, 100-h, and 1000-h fuels, essential for analyzing historical fire activity and understanding climatological trends. The methodology presented here demonstrates significant advancements in the accuracy and robustness of fuel moisture estimates, which are critical for fire forecasting and management. Full article
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<p>Diagram outlining the FMDA system redesigned for the DFMC reanalysis product.</p>
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<p>Scatter plots of observed and estimated fuel moisture (black dots), kernel density estimate (KDE) (blue shading), linear fit (in a least-squares sense) to the data points (blue dashed line) and perfect fit (black dashed line) for the year 2018 comparing observed fuel moisture to (<b>a</b>) TSM with the training set, (<b>b</b>) TSM with the testing set, (<b>c</b>) DFMC reanalysis product with the train set, (<b>d</b>) DFMC reanalysis product with the test set, and (<b>e</b>) Nelson model with all the data.</p>
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<p>Time series of (<b>a</b>) the error in the fuel moisture estimates from the Nelson model (purple line), TSM (green line), and the dead fuel moisture content (DFMC) reanalysis product (blue line), (<b>b</b>) the number of available observations for the state of California, and (<b>c</b>) a Boolean variable that is equal to 1 for the periods with a number of observations fewer than 50.</p>
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<p>Mean absolute error of estimated 10 h dead fuel moisture at RAWS locations for the TSM, our DFMC reanalysis product, and the Nelson model. The purple arrow illustrates a station where DFMC reanalysis product outperforms the TSM by maintaining similar results than Nelson.</p>
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<p>Rate of spread differences and relative ROS differences for varying wind speeds and fuel moisture content values, as a result of increasing fuel moisture content by 0.02 g/g for fuel category 1 (short grass).</p>
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15 pages, 7130 KiB  
Article
Insights into Boreal Forest Disturbance from Canopy Stability Index
by Brendan Mackey, Sonia Hugh, Patrick Norman, Brendan M. Rogers and Dominick Dellasala
Land 2024, 13(10), 1644; https://doi.org/10.3390/land13101644 - 9 Oct 2024
Viewed by 579
Abstract
The world’s forests are being increasingly disturbed from exposure to the compounding impacts of land use and climate change, in addition to natural disturbance regimes. Boreal forests have a lower level of deforestation compared to tropical forests, and while they have higher levels [...] Read more.
The world’s forests are being increasingly disturbed from exposure to the compounding impacts of land use and climate change, in addition to natural disturbance regimes. Boreal forests have a lower level of deforestation compared to tropical forests, and while they have higher levels of natural disturbances, the accumulated impact of forest management for commodity production coupled with worsening fire weather conditions and other climate-related stressors is resulting in ecosystem degradation and loss of biodiversity. We used satellite-based time-series analysis of two canopy indices—canopy photosynthesis and canopy water stress—to calculate an index that maps the relative stability of forest canopies in the Canadian provinces of Ontario and Quebec. By drawing upon available spatial time-series data on logging, wildfire, and insect infestation impacts, we were able to attribute the causal determinants of areas identified as having unstable forest canopy. The slope of the two indices that comprise the stability index also provided information as to where the forest is recovering from prior disturbances. The stability analyses and associated spatial datasets are available in an interactive web-based mapping app. that can be used to map disturbed forest canopies and the attribution of disturbances to human or natural causes. This information can assist decision-makers in identifying areas that are potentially ecologically degraded and in need of restoration and those stable areas that are a priority for protection. Full article
(This article belongs to the Section Landscape Ecology)
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<p>The analytical workflow used in this study. The two main analysis stages are shown on the left-hand side of the figure: the stability mapping stage (<b>a</b>); and the identifying disturbance factors stage (<b>b</b>). A description of each step in the workflow is given in the center, and the computer program or programming language used is given on the right.</p>
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<p>The analytical workflow for the main steps in the calculation of the forest canopy stability index.</p>
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<p>The two variables used to spatially stratify pixels for calculating the stability index are (<b>a</b>) forest cover type and (<b>b</b>) growing season group.</p>
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<p>Stability Index for forests of Ontario and Quebec and boreal zone extents [<a href="#B19-land-13-01644" class="html-bibr">19</a>].</p>
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<p>Relative influence of each variable on instability for boreal forests—all drivers. Relative influence is a measure indicating the relative importance of each variable in training the GBM model.</p>
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<p>Partial dependence and ICE plots for boreal forest—all drivers. The boxplot and black lines for TWI show the ICE values, and the distribution of the predicted response variable for each observation as we vary each predictor variable in the model. For the TWI ICE values, the values are centered on the first point of the PDP value. The red dot and red line for TWI represent the pdp value, and the half-violin plot (blue) shows the density of the training data.</p>
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<p>Ablation study for boreal forest—all drivers. (<b>a</b>) RMSE values for the trained data and the predicted RMSE values with the test data. (<b>b</b>) Bar graph representation of the ablation RMSE values, where the vertical line corresponds with the RMSE values of the original model without variable removal. Any of the RMSE values that are lower than the original model (the all row) perform better when the variable is removed from the model.</p>
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<p>Pixel drill for a location in this study area showing the time series for fPAR and SIWSI, the two-component indices of the forest canopy stability index. Satellite images for a selection of years over the time series are also shown. In this example, the areas experienced two natural disturbance events at the start (fire) and end (insect) of the time period. The slopes of the two indices (red lines) indicate that the forest canopy has been recovering.</p>
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<p>Pixel drill for a location in this study area showing the time series for fPAR and SIWSI, the two-component indices of the forest canopy instability index. Satellite images for a selection of years over the time series are also shown. In this example, the areas experienced a logging event at the end of the time series. The slopes of the two indices (red lines) indicate that the forest canopy has not yet recovered.</p>
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18 pages, 12123 KiB  
Article
Simulation of Fire Occurrence Based on Historical Data in Future Climate Scenarios and Its Practical Verification
by Mingyu Wang, Liqing Si, Feng Chen, Lifu Shu, Fengjun Zhao and Weike Li
Fire 2024, 7(10), 346; https://doi.org/10.3390/fire7100346 - 28 Sep 2024
Viewed by 714
Abstract
Forest fire is one of the dominant disturbances in the forests of Heilongjiang Province, China, and is one of the most rapid response predictors that indicate the impact of climate change on forests. This study calculated the Canadian FWI (Fire Weather Index) and [...] Read more.
Forest fire is one of the dominant disturbances in the forests of Heilongjiang Province, China, and is one of the most rapid response predictors that indicate the impact of climate change on forests. This study calculated the Canadian FWI (Fire Weather Index) and its components from meteorological record over past years, and a linear model was built from the monthly mean FWI and monthly fire numbers. The significance test showed that fire numbers and FWI had a very pronounced correlation, and monthly mean FWI was suitable for predicting the monthly fire numbers in this region. Then FWI and its components were calculated from the SRES (IPCC Special Report on Emission Scenarios) A2 and B2 climatic scenarios, and the linear model was rebuilt to be suitable for the climatic scenarios. The results indicated that fire numbers would increase by 2.98–129.97% and −2.86–103.30% in the A2 and B2 climatic scenarios during 2020–2090, respectively. The monthly variation tendency of the FWI components is similar in the A2 and B2 climatic scenarios. The increasing fire risk is uneven across months in these two climatic scenarios. The monthly analysis showed that the FFMC (Fine Fuel Moisture Code) would increase dramatically in summer, and the decreasing precipitation in summer would contribute greatly to this tendency. The FWI would increase rapidly from the spring fire season to the autumn fire season, and the FWI would have the most rapid increase in speed in the spring fire season. DMC (Duff Moisture Code) and DC (Drought Code) have relatively balanced rates of increasing from spring to autumn. The change in the FWI in this region is uneven in space as well. In early 21st century, the FWI of the north of Heilongjiang Province would increase more rapidly than the south, whereas the FWI of the middle and south of Heilongjiang Province would gradually catch up with the increasing speed of the north from the middle of 21st century. The changes in the FWI across seasons and space would influence the fire management policy in this region, and the increasing fire numbers and variations in the FWI scross season and space suggest that suitable development of the management of fire sources and forest fuel should be conducted. Full article
(This article belongs to the Special Issue Forest Fuel Treatment and Fire Risk Assessment)
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<p>Location of actual weather stations and scenarios grid points in Heilongjiang Province.</p>
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<p>Monthly variation of fire number and FWI.</p>
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<p>Linear regression of monthly fire number and monthly mean FWI (Significance level F = 2.0293 × 10<sup>−18</sup>).</p>
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<p>Annual change of meteorological factors in Heilongjiang (2020–2100).</p>
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<p>Change of FWI system component factors in Heilongjiang (2020–2100).</p>
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<p>Annual change rate of monthly FWI system components in Heilongjiang (2020–2100).</p>
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<p>Annual change of fire numbers in Heilongjiang (2020–2100).</p>
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<p>Rate of change in the number of forest fires per decade (%).</p>
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<p>Spatial pattern of change rate of FWI(%).</p>
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<p>Spatial pattern of change rate of FWI(%).</p>
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21 pages, 5335 KiB  
Article
Deep Learning Approach for Wildland Fire Recognition Using RGB and Thermal Infrared Aerial Image
by Rafik Ghali and Moulay A. Akhloufi
Fire 2024, 7(10), 343; https://doi.org/10.3390/fire7100343 - 27 Sep 2024
Viewed by 922
Abstract
Wildfires cause severe consequences, including property loss, threats to human life, damage to natural resources, biodiversity, and economic impacts. Consequently, numerous wildland fire detection systems were developed over the years to identify fires at an early stage and prevent their damage to both [...] Read more.
Wildfires cause severe consequences, including property loss, threats to human life, damage to natural resources, biodiversity, and economic impacts. Consequently, numerous wildland fire detection systems were developed over the years to identify fires at an early stage and prevent their damage to both the environment and human lives. Recently, deep learning methods were employed for recognizing wildfires, showing interesting results. However, numerous challenges are still present, including background complexity and small wildfire and smoke areas. To address these challenging limitations, two deep learning models, namely CT-Fire and DC-Fire, were adopted to recognize wildfires using both visible and infrared aerial images. Infrared images detect temperature gradients, showing areas of high heat and indicating active flames. RGB images provide the visual context to identify smoke and forest fires. Using both visible and infrared images provides a diversified data for learning deep learning models. The diverse characteristics of wildfires and smoke enable these models to learn a complete visual representation of wildland fires and smoke scenarios. Testing results showed that CT-Fire and DC-Fire achieved higher performance compared to baseline wildfire recognition methods using a large dataset, which includes RGB and infrared aerial images. CT-Fire and DC-Fire also showed the reliability of deep learning models in identifying and recognizing patterns and features related to wildland smoke and fires and surpassing challenges, including background complexity, which can include vegetation, weather conditions, and diverse terrain, detecting small wildfire areas, and wildland fires and smoke variety in terms of size, intensity, and shape. CT-Fire and DC-Fire also reached faster processing speeds, enabling their use for early detection of smoke and forest fires in both night and day conditions. Full article
(This article belongs to the Section Fire Science Models, Remote Sensing, and Data)
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<p>The proposed architecture of DC-Fire. P1 and P present the predicted probabilities of the input aerial image belonging to the non-fire and fire class.</p>
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<p>The proposed architecture of CT-Fire. L1 and L refer the predicted probabilities of the input aerial image belonging to the fire or non-fire class.</p>
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<p>FLAME2 dataset example. (<b>Top</b>): RGB non-fire images; (<b>Bottom</b>): Their corresponding IR non-fire images.</p>
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<p>FLAME2 dataset example. (<b>Top</b>): RGB fire images. (<b>Bottom</b>): Their corresponding IR fire images.</p>
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<p>Loss curves for the proposed DC-Fire and CT-Fire during training and validation steps.</p>
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<p>Confusion matrix of both DC-Fire and CT-Fire using both IR and RGB images (both models obtained the same results).</p>
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<p>Classification results of DC-Fire and CT-Fire models using RGB fire images.</p>
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<p>Classification results of DC-Fire and CT-Fire models using RGB non-fire images.</p>
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<p>Classification results of DC-Fire and CT-Fire models using IR fire images.</p>
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<p>Classification results of DC-Fire and CT-Fire models using IR non-fire images.</p>
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22 pages, 8353 KiB  
Article
The Short-Term Impacts of the 2017 Portuguese Wildfires on Human Health and Visibility: A Case Study
by Diogo Lopes, Isilda Cunha Menezes, Johnny Reis, Sílvia Coelho, Miguel Almeida, Domingos Xavier Viegas, Carlos Borrego and Ana Isabel Miranda
Fire 2024, 7(10), 342; https://doi.org/10.3390/fire7100342 - 26 Sep 2024
Viewed by 773
Abstract
The frequency of extreme wildfire events (EWEs) is expected to increase due to climate change, leading to higher levels of atmospheric pollutants being released into the air, which could cause significant short-term impacts on human health (both for the population and firefighters) and [...] Read more.
The frequency of extreme wildfire events (EWEs) is expected to increase due to climate change, leading to higher levels of atmospheric pollutants being released into the air, which could cause significant short-term impacts on human health (both for the population and firefighters) and on visibility. This study aims to gain a better understanding of the effects of EWEs’ smoke on air quality, its short-term impacts on human health, and how it reduces visibility by applying a modelling system to the Portuguese EWEs of October 2017. The Weather Research and Forecasting Model was combined with a semi-empirical fire spread algorithm (WRF-SFIRE) to simulate particulate matter smoke dispersion and assess its impacts based on up-to-date numerical approaches. Hourly simulated particulate matter values were compared to hourly monitored values, and the WRF-SFIRE system demonstrated accuracy consistent with previous studies, with a correlation coefficient ranging from 0.30 to 0.76 and an RMSE varying between 215 µg/m3 and 418 µg/m3. The estimated daily particle concentration levels exceeded the European air quality limit value, indicating a potential strong impact on human health. Health indicators related to exposure to particles were estimated, and their spatial distribution showed that the highest number of hospital admissions (>300) during the EWE, which occurred downwind of the fire perimeters, were due to the combined effect of high smoke pollution levels and population density. Visibility reached its worst level at night, when dispersion conditions were poorest, with the entire central and northern regions registering poor visibility levels (with a visual range of less than 2 km). This study emphasises the use of numerical models to predict, with high spatial and temporal resolutions, the population that may be exposed to dangerous levels of air pollution caused by ongoing wildfires. It offers valuable information to the public, civil protection agencies, and health organisations to assist in lessening the impact of wildfires on society. Full article
(This article belongs to the Section Fire Social Science)
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<p>The locations of the Portuguese areas (i.e., Seia, Lousã, Oliveira do Hospital, Sertã, Leiria, Quiaios, and Vouzela) affected by the EWEs on 15 and 16 October 2017 as well as the Portuguese borders (the north and central regions and Alentejo).</p>
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<p>The spatial distribution (4 km × 4 km) of the daily average PM<sub>10</sub> (<b>a</b>) and PM<sub>2.5</sub> concentrations (<b>b</b>) between 15 and 16 October 2017. The values measured by the Portuguese air quality monitoring network are represented by small coloured circles.</p>
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<p>The spatial distribution (4 km × 4 km) of hospital admissions in Portugal for respiratory (<b>a</b>) and cardiovascular (<b>b</b>) diseases due to PM<sub>2.5</sub> levels caused by the EWEs (15 and 16 October 2017).</p>
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<p>Daily distribution of visibility classes for WRF-SFIRE grid cells between 15 and 16 October 2017.</p>
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<p>The spatial distribution (4 km × 4 km) of the visibility classes at 12:00 on 15 October (<b>a</b>) and 1:00 on 16 October 2017 (<b>b</b>), with visibility based on the pollutant concentrations from the model’s first layer (up to 2000 m above ground.).</p>
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<p>The timeline (start and end) of the analysed EWEs (i.e., Seia, Lousã, Oliveira do Hospital, Sertã, Quiaios, Leiria, and Vouzela) from 15 to 16 October 2017.</p>
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<p>A flowchart illustrating this study’s methodology.</p>
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<p>The spatial distribution of the population (<b>a</b>) and firefighter teams (<b>b</b>) between 15 and 16 October 2017.</p>
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<p>The temporal variations in the numbers of firefighters (<b>a</b>), aerial firefighting aircraft (<b>b</b>), and support material (<b>c</b>) in each EWE (Note: aerial firefighting aircraft is zero for all analysed period at Oliveira do Hospital, Quiaios and Vouzela).</p>
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<p>The temporal variations in the numbers of firefighters (<b>a</b>), aerial firefighting aircraft (<b>b</b>), and support material (<b>c</b>) in each EWE (Note: aerial firefighting aircraft is zero for all analysed period at Oliveira do Hospital, Quiaios and Vouzela).</p>
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21 pages, 8374 KiB  
Article
Response of Fuel Characteristics, Potential Fire Behavior, and Understory Vegetation Diversity to Thinning in Platycladus orientalis Forest in Beijing, China
by Min Gao, Sifan Chen, Aoli Suo, Feng Chen and Xiaodong Liu
Forests 2024, 15(9), 1667; https://doi.org/10.3390/f15091667 - 22 Sep 2024
Viewed by 589
Abstract
Objective: Active fuel management operations, such as thinning, can minimize extreme wildfire conditions while preserving ecosystem services, including maintaining understory vegetation diversity. However, the appropriate thinning intensity for balancing the above two objectives has not been sufficiently studied. Methods: This study was conducted [...] Read more.
Objective: Active fuel management operations, such as thinning, can minimize extreme wildfire conditions while preserving ecosystem services, including maintaining understory vegetation diversity. However, the appropriate thinning intensity for balancing the above two objectives has not been sufficiently studied. Methods: This study was conducted to assess the impact of various thinning intensities (light thinning, LT, 15%; moderate thinning, MT, 35%; heavy thinning, HT, 50%; and control treatment, CK) on fuel characteristics, potential fire behavior, and understory vegetation biodiversity in Platycladus orientalis forest in Beijing using a combination of field measurements and fire behavior simulations (BehavePlus 6.0.0). Results: A significant reduction in surface and canopy fuel loads with increasing thinning intensity, notably reducing CBD to below 0.1 kg/m3 under moderate thinning, effectively prevented the occurrence of active crown fires, even under extreme weather conditions. Additionally, moderate thinning enhanced understory species diversity, yielding the highest species diversity index compared to other treatments. Conclusions: These findings suggest that moderate thinning (35%) offers an optimal balance, substantially reducing the occurrence of active crown fires while promoting biodiversity. Therefore, it is recommended to carry out moderate thinning in the study area. Forest managers can leverage this information to devise technical strategies that simultaneously meet fire prevention objectives and enhance understory vegetation species diversity in areas suitable for thinning-only treatments. Full article
(This article belongs to the Special Issue Fire Ecology and Management in Forest—2nd Edition)
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<p>Location of the study site in Haidian District, Beijing, China.</p>
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<p>Standard branch diagram of <span class="html-italic">P. orientalis</span> canopy. Note: H = tree height, CL = crown length, H<sub>base</sub> = canopy base height, d= branch basal diameter.</p>
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<p>The process and result of fire type generation in BehavePlus 6.0.0. Note: Surface = surface fire; Torching = passive crown fire; Conditional Crown = active crown fire possible if the fire transitions to the overstory; Crowning = active crown fire.</p>
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<p>Mean surface fuel loads and depth under the four thinning intensity treatments at different times after thinning. Note: (<b>a</b>–<b>c</b>): downed and dead woody fuel loads; (<b>d</b>,<b>e</b>): live fuel loads; (<b>f</b>,<b>g</b>): litter leaves fuel load; (<b>h</b>): litter depth; (<b>i</b>): fuel bed depth. Different uppercase letters represent significant differences among thinning intensities (<span class="html-italic">p</span> &lt; 0.05).</p>
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<p>Mean canopy fuel load (<b>a</b>) and canopy bulk density (<b>b</b>) under different thinning intensities at three time points after thinning. Different uppercase letters represent significant differences among thinning intensities (<span class="html-italic">p</span> &lt; 0.05).</p>
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<p>Potential surface fire behavior indicators of <span class="html-italic">P. orientalis</span> stand under four thinning intensities. Note: (<b>a</b>,<b>d</b>,<b>g</b>): surface fire spread rate under three thinning years; (<b>b</b>,<b>e</b>,<b>h</b>): surface flame length under three thinning years; (<b>c</b>,<b>f</b>,<b>i</b>): heat per unit area under three thinning years.</p>
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<p>Potential crown fire behavior indicators of <span class="html-italic">P. orientalis</span> stand under four thinning intensities. Note: (<b>a</b>,<b>d</b>,<b>g</b>): crown flame length under three thinning years; (<b>b</b>,<b>e</b>,<b>h</b>): crown fireline intensity under three thinning years; (<b>c</b>,<b>f</b>,<b>i</b>): heat per unit area under three thinning years.</p>
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<p>Potential surface fire behavior indicators of <span class="html-italic">P. orientalis</span> stand under four thinning intensities. Note: (<b>A</b>,<b>D</b>,<b>G</b>): surface fireline intensity; (<b>B</b>,<b>E</b>,<b>H</b>): critical surface fireline intensity; (<b>C</b>,<b>F</b>,<b>I</b>): heat per unit area.</p>
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<p>Critical crown fire spread rate, crown fire spread rate, and the active ratio of <span class="html-italic">P. orientalis</span>.</p>
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16 pages, 38278 KiB  
Communication
A Case Study of the Possible Meteorological Causes of Unexpected Fire Behavior in the Pantanal Wetland, Brazil
by Flavio T. Couto, Filippe L. M. Santos, Cátia Campos, Carolina Purificação, Nuno Andrade, Juan M. López-Vega and Matthieu Lacroix
Earth 2024, 5(3), 548-563; https://doi.org/10.3390/earth5030028 - 18 Sep 2024
Viewed by 806
Abstract
This study provides insights into large fires in the Pantanal by analyzing the atmospheric conditions that influenced the rapid fire evolution between 13 and 14 November 2023, when fire fronts spread rapidly, leading to critical situations for firefighters. The observation-based analysis helped us [...] Read more.
This study provides insights into large fires in the Pantanal by analyzing the atmospheric conditions that influenced the rapid fire evolution between 13 and 14 November 2023, when fire fronts spread rapidly, leading to critical situations for firefighters. The observation-based analysis helped us to identify some characteristics of the fire’s evolution and the meteorological conditions in the region. Furthermore, two simulations were run with the Meso-NH model, which was configured with horizontal resolutions of 2.5 km and 5 km. The fire behavior, characterized by satellite observations, revealed periods with a sudden increase in active fire numbers. High temperatures and low relative humidity in the region characterized the fire weather conditions. The simulations confirmed the critical fire condition, showing the benefits of increasing the resolution of numerical models for the Pantanal region. The convection-resolving simulation at 2.5 km showed the repeated development of gust fronts in the late afternoon and early evening. This study highlights this dynamic that, coupled with intense surface wind gusts, was crucial for the intensification of the fire spread and unexpected behavior. This study is a first step toward better understanding fire dynamics in the Pantanal through atmospheric modeling, and it can support strategies for firefighting in the region. Full article
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<p>Study region: (<b>a</b>) model configuration covering the Pantanal wetland region representing EXP1 domain with 2.5 km horizontal resolution, with the orography data obtained from the Shuttle Radar Topography Mission (SRTM) database. The red “x” symbol indicates the fire location and black “stars” denote the weather stations; (<b>b</b>) Sentinel-2 10 m land use/land cover for 2023 produced by Impact Observatory and Esri [<a href="#B41-earth-05-00028" class="html-bibr">41</a>].</p>
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<p>Hourly active fire number (AFN) distribution between 0600 UTC on 12 November and 1800 UTC on 15 November 2023, from GOES-16 satellite. The blue dashed-line boxes, called PHASE I, PHASE II, and PHASE III represent the periods with the highest AFN values. Moreover, the green dashed-line box indicates the period simulated by the Meso-NH model.</p>
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<p>(<b>a</b>) Spatial distribution of active fire number from NOAA-20 satellite between 12 and 15 November 2023; (<b>b</b>) MODIS corrected reflectance image on 12 November 2023 obtained from worldview on 12 November 2023 at 1800 UTC; source: [<a href="#B60-earth-05-00028" class="html-bibr">60</a>].</p>
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<p>Comparison between model (EXP1 and EXP2) and observation for the 72 h of simulation: (<b>a</b>–<b>c</b>) air temperature at 2 m; (<b>d</b>–<b>f</b>) relative humidity at 2 m; (<b>g</b>–<b>i</b>) wind gusts at 10 m.</p>
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<p>Air temperature at 2 m (unit: °C) simulated at 2.5 km resolution [EXP1]: (<b>a</b>) 12 November 2023 at 1800 UTC, (<b>b</b>) 13 November 2023 at 1900 UTC, (<b>c</b>) 14 November 2023 at 1800 UTC. The black contour line represents the Pantanal international boundary.</p>
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<p>Relative humidity at 2 m (unit: %) simulated with 2.5 km resolution [EXP1]: (<b>a</b>) 12 November 2023 at 1800 UTC, (<b>b</b>) 13 November 2023 at 1900 UTC, (<b>c</b>) 14 November 2023 at 1800 UTC. The black contour line represents the Pantanal international boundary.</p>
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<p>Wind gusts (colored, unit: m.s<sup>−1</sup>) and wind direction at 10 m (arrows) simulated at 2.5 km resolution [EXP1] (<b>a</b>–<b>d</b>) PHASE I; (<b>e</b>–<b>h</b>) PHASE II; (<b>i</b>–<b>l</b>) PHASE III. The black contour line represents the Pantanal international boundary.</p>
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<p>Wind gusts (colored areas, unit: m.s<sup>−1</sup>) and wind direction at 10 m (arrows) from EXP2 with 5 km resolution (<b>a</b>) PHASE I: 0000 UTC on 13 November 2023, (<b>b</b>) PHASE II: 2000 UTC on 13 November 2023, and (<b>c</b>) PHASE III: 2000 UTC on 14 November 2023.</p>
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<p>Difference of wind gust at 10 m between EXP1 and EXP2: (<b>a</b>) PHASE I: 0000 UTC on 13 November 2023, (<b>b</b>) PHASE II: 2000 UTC on 13 November 2023, and (<b>c</b>) PHASE III: 2000 UTC on 14 November 2023.</p>
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<p>Schematic diagram showing the PERIODS identified in the wind gusts field: (<b>a</b>) PERIOD I with weaker wind gusts over the Pantanal during the night and early morning; (<b>b</b>) PERIOD II presents moderate wind gusts; (<b>c</b>) PERIOD III represents the gust fronts, in particular propagating southward, as indicated from the notation time (t), t + 1 h and t + 2 h.</p>
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13 pages, 3621 KiB  
Article
Wildfire Burnt Area and Associated Greenhouse Gas Emissions under Future Climate Change Scenarios in the Mediterranean: Developing a Robust Estimation Approach
by Tim van der Schriek, Konstantinos V. Varotsos, Anna Karali and Christos Giannakopoulos
Fire 2024, 7(9), 324; https://doi.org/10.3390/fire7090324 - 17 Sep 2024
Viewed by 872
Abstract
Wildfires burn annually over 400,000 ha in Mediterranean countries. By the end of the 21st century, wildfire Burnt Area (BA) and associated Green House Gas (GHG) emissions may double to triple due to climate change. Regional projections of future BA are urgently required [...] Read more.
Wildfires burn annually over 400,000 ha in Mediterranean countries. By the end of the 21st century, wildfire Burnt Area (BA) and associated Green House Gas (GHG) emissions may double to triple due to climate change. Regional projections of future BA are urgently required to update wildfire policies. We present a robust methodology for estimating regional wildfire BA and GHG emissions under future climate change scenarios in the Mediterranean. The Fire Weather Index, selected drought indices, and meteorological variables were correlated against BA/GHG emissions data to create area-specific statistical projection models. State-of-the-art regional climate models (horizontal resolution: 12 km), developed within the EURO-CORDEX initiative, simulated data under three climate change scenarios (RCP2.6, RCP4.5, and RCP8.5) up to 2070. These data drove the statistical models to estimate future wildfire BA and GHG emissions in three pilot areas in Greece, Montenegro, and France. Wildfire BA is projected to increase by 20% to 130% up to 2070, depending on the study area and climate scenario. The future expansion of fire-prone areas into the north Mediterranean and mountain environments is particularly alarming, given the large biomass present here. Fire-smart landscape management may, however, greatly reduce the projected future wildfire BA and GHG increases. Full article
(This article belongs to the Special Issue Effects of Climate Change on Fire Danger)
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<p>Location of the study areas (1. Luberon-Lure, SE France; 2. Prokletije/Komovi, SE Montenegro; 3. Chania province, W Crete, Greece).</p>
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<p>Flowchart of the methodological approach.</p>
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<p>Chania province: future BA (“M” = mean, and “Δ” = difference, compared to control period).</p>
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<p>Chania province: future emissions (“M” = mean, and “Δ” = difference, compared to control period).</p>
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<p>Montenegro: future BA (“M” = mean, and “Δ” = difference, compared to control period).</p>
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<p>Montenegro: future emissions (“M” = mean, and “Δ” = difference, compared to control period).</p>
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<p>Luberon-Lure: future BA (“M” = mean, and “Δ” = difference, compared to control period).</p>
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<p>Luberon-Lure: future emissions (“M” = mean, and “Δ” = difference, compared to control period).</p>
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22 pages, 985 KiB  
Article
Synergistic Impacts of Climate Change and Wildfires on Agricultural Sustainability—A Greek Case Study
by Stavros Kalogiannidis, Dimitrios Kalfas, Maria Paschalidou and Fotios Chatzitheodoridis
Climate 2024, 12(9), 144; https://doi.org/10.3390/cli12090144 - 14 Sep 2024
Viewed by 1646
Abstract
Climate change and wildfire effects have continued to receive great attention in recent times due to the impact they render on the environment and most especially to the field of agriculture. The purpose of this study was to assess the synergistic impacts of [...] Read more.
Climate change and wildfire effects have continued to receive great attention in recent times due to the impact they render on the environment and most especially to the field of agriculture. The purpose of this study was to assess the synergistic impacts of climate change and wildfires on agricultural sustainability. This study adopted a cross-sectional survey design based on the quantitative research approach. Data were collected from 340 environmental experts using an online questionnaire. The results showed that extreme weather events such as heavy rains or extreme droughts negatively influence agricultural sustainability in Europe. The results showed that disruptions in ecosystems caused by climate change have a significant positive impact on agricultural sustainability in Europe. Furthermore, forest regeneration after wildfires showed statistically significant positive influence on agricultural sustainability in Europe. The economic impact of fire on crops, cattle, and farms can be estimated. This information can be used to develop and plan agricultural regions near fire-prone areas; choose the best, most cost-effective, and longest-lasting cultivar; and limit fire risk. It is also clear that increased wildfire smoke negatively affects agricultural sustainability. Full article
(This article belongs to the Special Issue Climate Adaptation Ways for Smallholder Farmers)
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<p>The role of climate in agricultural production.</p>
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<p>Aspects of agricultural sustainability in Europe.</p>
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21 pages, 21587 KiB  
Article
SAPERI: An Emergency Modeling Chain for Simulating Accidental Releases of Pollutants into the Atmosphere
by Bianca Tenti, Massimiliano Romana, Giuseppe Carlino, Rossella Prandi and Enrico Ferrero
Atmosphere 2024, 15(9), 1095; https://doi.org/10.3390/atmos15091095 - 9 Sep 2024
Viewed by 537
Abstract
Timely forecast of atmospheric pollutants fallout due to accidental fires can provide decision-makers with useful information for effective emergency response, for planning environmental monitoring and for conveying essential alerts to the population to minimize health risks. The SAPERI project (Accelerated simulation of accidental [...] Read more.
Timely forecast of atmospheric pollutants fallout due to accidental fires can provide decision-makers with useful information for effective emergency response, for planning environmental monitoring and for conveying essential alerts to the population to minimize health risks. The SAPERI project (Accelerated simulation of accidental releases in the atmosphere on heterogeneous platforms—from its Italian initials) implements a modeling chain to quickly supply evidence about the dispersion of pollutants accidentally released in the atmosphere, even in the early stages of the emergency when full knowledge of the incident details is missing. The SAPERI modeling chain relies on SPRAY-WEB, a Lagrangian particle dispersion model openly shared for research purposes, parallelized on a GPU to take advantage of local or cloud computing resources and interfaced with open meteorological forecasts made available by the Meteo Italian SupercompuTing PoRtAL (MISTRAL) consortium over Italy. The operational model provides a quantitative and qualitative estimate of the impact of the emergency event by means of a maximum ground level concentration and a footprint map. In this work, the SAPERI modeling chain is tested in a real case event that occurred in Beinasco (Torino, Italy) in December 2021, mimicking its use with limited or missing local input data as occurs when an alert message is first issued. An evaluation of the meteorology forecast is carried out by comparing the wind and temperature fields obtained from MISTRAL with observations from weather stations. The concentrations obtained from the dispersion model are then compared with the observations at three air quality monitoring stations impacted by the event. Full article
(This article belongs to the Special Issue Development in Atmospheric Dispersion Modelling)
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<p>SAPERI modeling chain flow chart: in blue, blocks concerning the user interface; in red, raw data needed by the model; in orange, data processors and in green, the chain core dispersion model.</p>
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<p>Default time modulation of emissions as processed by SAPEMI on the basis of input data.</p>
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<p>Aerial picture of Torino (Italy) with source location (red dot), meteorological (yellow dots) and air quality (blue dots) stations (source: the Italian geo-cartographic portal).</p>
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<p>Maximum ground level concentration field (<b>left</b>) and footprint map (<b>right</b>) for benzene as simulated in the first run (12–14 December). Concentration levels in <math display="inline"><semantics> <mrow> <mi mathvariant="sans-serif">μ</mi> <mi mathvariant="normal">g</mi> <mspace width="4pt"/> <msup> <mi mathvariant="normal">m</mi> <mrow> <mo>−</mo> <mn>3</mn> </mrow> </msup> </mrow> </semantics></math>. The coordinate reference system of the x- and y-axes is the UTM 32.</p>
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<p>Maximum ground-level concentration field (<b>left</b>) and footprint map (<b>right</b>) for benzene as simulated in the second run (13–15 December). Concentration levels in <math display="inline"><semantics> <mrow> <mi mathvariant="sans-serif">μ</mi> <mi mathvariant="normal">g</mi> <mspace width="4pt"/> <msup> <mi mathvariant="normal">m</mi> <mrow> <mo>−</mo> <mn>3</mn> </mrow> </msup> </mrow> </semantics></math>. The coordinate reference system of the x- and y-axes is the UTM 32.</p>
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<p>Maximum ground level concentration field (<b>left</b>) and footprint map (<b>right</b>) for benzene as simulated in the third run (14–16 December). Concentration levels in <math display="inline"><semantics> <mrow> <mi mathvariant="sans-serif">μ</mi> <mi mathvariant="normal">g</mi> <mspace width="4pt"/> <msup> <mi mathvariant="normal">m</mi> <mrow> <mo>−</mo> <mn>3</mn> </mrow> </msup> </mrow> </semantics></math>. The coordinate reference system of the x- and y-axes is the UTM 32.</p>
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<p>Maximum ground level concentration field (<b>left</b>) and footprint map (<b>right</b>) for benzene as simulated in the fourth run (15–17 December). Concentration levels in <math display="inline"><semantics> <mrow> <mi mathvariant="sans-serif">μ</mi> <mi mathvariant="normal">g</mi> <mspace width="4pt"/> <msup> <mi mathvariant="normal">m</mi> <mrow> <mo>−</mo> <mn>3</mn> </mrow> </msup> </mrow> </semantics></math>. The coordinate reference system of the x- and y-axes is the UTM 32.</p>
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<p>An example of the temperature and wind fields at 00:00 of 12/12/2021 from the Mistral run 12–14 December.</p>
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<p>Temperature (<b>top</b>), wind speed (<b>middle</b>) and wind direction (<b>bottom</b>) comparisons between COSMO-2I forecasts and observations from the Torino Consolata station. Each row corresponds to a different day of the event, from the <math display="inline"><semantics> <mrow> <mn>12</mn> <mi>th</mi> </mrow> </semantics></math> (<b>top</b>) to the <math display="inline"><semantics> <mrow> <mn>16</mn> <mi>th</mi> </mrow> </semantics></math> (<b>bottom</b>). Grey lines and dots are the measured values, colored lines and dots are the model data; each color corresponds to a different model run.</p>
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<p>Temperature (<b>top</b>), wind speed (<b>middle</b>) and wind direction (<b>bottom</b>) comparisons between COSMO-2I forecasts and observations from the Alenia station. Each row corresponds to a different day of the event, from the <math display="inline"><semantics> <mrow> <mn>12</mn> <mi>th</mi> </mrow> </semantics></math> (<b>top</b>) to the <math display="inline"><semantics> <mrow> <mn>16</mn> <mi>th</mi> </mrow> </semantics></math> (<b>bottom</b>). Grey lines and dots are the measured values, colored lines and dots are the model data; each color corresponds to a different model run.</p>
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<p>Temperature (<b>top</b>), wind speed (<b>middle</b>) and wind direction (<b>bottom</b>) comparisons between COSMO-2I forecasts and observations from the Gorini station. Each row corresponds to a different day of the event, from the <math display="inline"><semantics> <mrow> <mn>12</mn> <mi>th</mi> </mrow> </semantics></math> (<b>top</b>) to the <math display="inline"><semantics> <mrow> <mn>16</mn> <mi>th</mi> </mrow> </semantics></math> (<b>bottom</b>). Grey lines and dots are the measured values, colored lines and dots are the model data; each color corresponds to a different model run.</p>
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<p>qq-plot of the observed and modeled benzene hourly concentration for the air quality stations of Beinasco (TRM)-Aldo Mei (<b>a</b>), Torino-Lingotto (<b>b</b>) and Torino-Rubino (<b>c</b>). Dots are original values, crosses are the normalized values and red lines are the best-fit lines.</p>
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<p>Normalized concentration trends for the four simulations (colored dots) compared with measurements of the air quality stations (grey dots) of Beinasco (TRM)-Aldo Mei (<b>a</b>), Torino-Lingotto (<b>b</b>) and Torino-Rubino (<b>c</b>).</p>
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<p>Scatter plot of the observed and normalized model concentrations of benzene for the air quality stations of Beinasco (TRM)-Aldo Mei (<b>a</b>), Torino-Lingotto (<b>b</b>) and Torino-Rubino (<b>c</b>). Red dotted lines represent the factor of two.</p>
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<p>Dioxins mean concentration: model output and measurement values at Garelli kindergarten in Beinasco. Concentrations expressed as <math display="inline"><semantics> <mrow> <mi>fg</mi> <mspace width="4pt"/> <mi mathvariant="normal">I</mi> <mo>−</mo> <mi>TEQ</mi> <mspace width="4pt"/> <msup> <mi mathvariant="normal">m</mi> <mrow> <mo>−</mo> <mn>3</mn> </mrow> </msup> </mrow> </semantics></math>.</p>
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