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20 pages, 27951 KiB  
Article
Wetland Carbon Dynamics in Illinois: Implications for Landscape Architectural Practice
by Bo Pang and Brian Deal
Sustainability 2024, 16(24), 11184; https://doi.org/10.3390/su162411184 - 20 Dec 2024
Viewed by 436
Abstract
Wetlands play a crucial role in carbon sequestration. The integration of wetland carbon dynamics into landscape architecture, however, has been challenging, mainly due to gaps between scientific knowledge and landscape practice norms. While the carbon performance of different wetland types is well established [...] Read more.
Wetlands play a crucial role in carbon sequestration. The integration of wetland carbon dynamics into landscape architecture, however, has been challenging, mainly due to gaps between scientific knowledge and landscape practice norms. While the carbon performance of different wetland types is well established in the ecological sciences literature, our study pioneers the translation of this scientific understanding into actionable landscape design guidance. We achieve this through a comprehensive, spatially explicit analysis of wetland carbon dynamics using 2024 National Wetlands Inventory data and other spatial datasets. We analyze carbon flux rates across 13 distinct wetland types in Illinois to help quantify useful information related to designing for carbon outcomes. Our analysis reveals that in Illinois, bottomland forests function as primary carbon sinks (709,462 MtC/year), while perennial deepwater rivers act as significant carbon emitters (−2,573,586 MtC/year). We also identify a notable north–south gradient in sequestration capacity, that helps demonstrate how regional factors influence wetland and other stormwater management design strategies. The work provides landscape architects with evidence-based parameters for evaluating carbon sequestration potential in wetland design decisions, while also acknowledging the need to balance carbon goals with other ecosystem services. This research advances the profession’s capacity to move beyond generic sustainable design principles toward quantifiable climate-responsive solutions, helping landscape architects make informed decisions about wetland type selection and placement in the context of climate change mitigation. Full article
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<p>Carbon sequestration patterns in Illinois. Map showing net carbon flux rates (MtC/year) across Illinois wetlands in 2024. Dark blue areas indicate the highest carbon sequestration (23.76 to 191.5 MtC/year), while red areas show the highest carbon emissions (−131,500 to −11,470 MtC/year). Note: County boundaries are shown in gray.</p>
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<p>Wetland classification in northeast Illinois. Spatial distribution of wetland types showing the diversity of wetland ecosystems across northeast Illinois. Bottomland forests (dark green) form corridors along major river systems, with deep water systems (dark blue), shallow marshes (light green), and scrub–shrub wetlands (olive green) distributed throughout the region.</p>
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<p>Carbon sequestration patterns in northeast Illinois. Net carbon flux rates (MtC/year) across northeast Illinois wetlands. Dark blue areas indicate the highest carbon sequestration (23.76 to 191.5 MtC/year), corresponding primarily to bottomland forest corridors along major rivers. Red and orange areas show the highest carbon emissions (−131,500 to −11,470 MtC/year), typically associated with deep water river systems. The pattern reveals significant spatial variation between urbanized areas and surrounding landscapes.</p>
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<p>Illinois wetland carbon sequestration excluding open water systems (2024). Analysis of 1,279,362 acres of non-open water wetlands, collectively sequestering 840,770 MtC/year. The highest sequestration rates (3.06–191.52 MtC/year) are concentrated along major river corridors and in bottomland forests.</p>
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<p>Illinois wetland carbon sequestration excluding lakes and rivers (2024). Analysis of terrestrial wetlands sequestering 758,159 MtC/year across 1,442,633 acres. The highest sequestration values (1.71–191.52 MtC/year) are concentrated in northeastern Illinois and southern portions of the state.</p>
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27 pages, 3310 KiB  
Article
Evaluation of Correction Algorithms for Sentinel-2 Images Implemented in Google Earth Engine for Use in Land Cover Classification in Northern Spain
by Iyán Teijido-Murias, Marcos Barrio-Anta and Carlos A. López-Sánchez
Forests 2024, 15(12), 2192; https://doi.org/10.3390/f15122192 - 12 Dec 2024
Viewed by 774
Abstract
This study examined the effect of atmospheric, topographic, and Bidirectional Reflectance Distribution Function (BRDF) corrections of Sentinel-2 images implemented in Google Earth Engine (GEE) for use in land cover classification. The study was carried out in an area of complex orography in northern [...] Read more.
This study examined the effect of atmospheric, topographic, and Bidirectional Reflectance Distribution Function (BRDF) corrections of Sentinel-2 images implemented in Google Earth Engine (GEE) for use in land cover classification. The study was carried out in an area of complex orography in northern Spain and made use of the Spanish National Forest Inventory plots and other systematically located plots to cover non-forest classes. A total of 2991 photo-interpreted ground plots and 15 Sentinel-2 images, acquired in summer at a spatial resolution of 10–20 m per pixel, were used for this purpose. The overall goal was to determine the optimal level of image correction in GEE for subsequent use in time series analysis of images for accurate forest cover classification. Particular attention was given to the classification of cover by the major commercial forest species: Eucalyptus globulus, Eucalyptus nitens, Pinus pinaster, and Pinus radiata. The Second Simulation of the Satellite Signal in the Solar Spectrum (Py6S) algorithm, used for atmospheric correction, provided the best compromise between execution time and image size, in comparison with other algorithms such as Sentinel-2 Level 2A Processor (Sen2Cor) and Sensor Invariant Atmospheric Correction (SIAC). To correct the topographic effect, we tested the modified Sun-canopy-sensor topographic correction (SCS + C) algorithm with digital elevation models (DEMs) of three different spatial resolutions (90, 30, and 10 m per pixel). The combination of Py6S, the SCS + C algorithm and the high-spatial resolution DEM (10 m per pixel) yielded the greatest precision, which demonstrated the need to match the pixel size of the image and the spatial resolution of the DEM used for topographic correction. We used the Ross-Thick/Li-Sparse-Reciprocal BRDF to correct the variation in reflectivity captured by the sensor. The BRDF corrections did not significantly improve the accuracy of the land cover classification with the Sentinel-2 images acquired in summer; however, we retained this correction for subsequent time series analysis of the images, as we expected it to be of much greater importance in images with larger solar incidence angles. Our final proposed dataset, with image correction for atmospheric (Py6S), topographic (SCS + C), and BRDF (Ross-Thick/Li-Sparse-Reciprocal BRDF) effects and a DEM of spatial resolution 10 m per pixel, yielded better goodness-of-fit statistics than other datasets available in the GEE catalogue. The Sentinel-2 images currently available in GEE are therefore not the most accurate for constructing land cover classification maps in areas with complex orography, such as northern Spain. Full article
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<p>Workflow adopted in this study to analyze different combinations of Sentinel-2 imagery corrections. In Algorithm_AT00B, Algorithm_ is the name or abbreviation of the algorithm used, A denotes “atmospheric correction”, T “topographic correction”, the number 00 refers to the spatial resolution of the digital elevation model (DEM) (90, 30, and 10 m per pixel, respectively) and B refers to “application of BRDF correction”. The datasets are shown in three different colours: datasets available in the GEE repository, in blue, the dataset developed in Sentinel Application Platform—SNAP 11.0.0 and uploaded in GEE assets, in purple; and the Level 1 C datasets derived from the GEE platform, in orange. In all cases, the Random Forest algorithm was used for fitting each processing dataset.</p>
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<p>Overview of (<b>a</b>) the location of the study area overlapping the Spanish National Forest Inventory plots used in this study, (<b>b</b>) Sentinel-2 granules for the study area, and (<b>c</b>) location of the region of interest in northern Spain. WGS 84/UTM zone 29N (EPSG: 32629).</p>
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<p>Visual comparison into the 4 datasets.</p>
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<p>Box plots of the overall accuracy (Accuracy) of the whole land cover classification corresponding to different levels of S2 image processing: absence of atmospheric, topographic, or BRDF correction (1C), atmospheric correction with the Sen2Cor algorithm and topographic correction with the Sen2Cor algorithm with DEM of 90 m per pixel (S2C_AT90) and atmospheric correction with the Py6S algorithm, topographic correction with the SCS + C algorithm with DEM of 10 m per pixel and the BRDF correction (Py6S_AT10B). The letters at the top of the box indicate the results of Tukey’s HSD multiple comparison test (different letters indicate significant differences between the difference levels of database processing and/or correction algorithms used).</p>
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15 pages, 3712 KiB  
Article
Root Biomass Allocation and Carbon Sequestration in Urban Landscaping Tree Species in South Korea
by Tae Kyung Yoon, Seungmin Lee, Seonghun Lee, Jeong-Min Lee, Yowhan Son and Sangjin Lee
Forests 2024, 15(12), 2104; https://doi.org/10.3390/f15122104 - 27 Nov 2024
Viewed by 640
Abstract
The quantification of urban tree biomass allocation has primarily relied on estimations using allometric equations (AEs) developed for nondestructive harvest methods. However, the lack of harvest-based AEs that account for belowground biomass, nutrient concentration, and annual growth rates poses challenges in accurately quantifying [...] Read more.
The quantification of urban tree biomass allocation has primarily relied on estimations using allometric equations (AEs) developed for nondestructive harvest methods. However, the lack of harvest-based AEs that account for belowground biomass, nutrient concentration, and annual growth rates poses challenges in accurately quantifying the greenhouse gas inventory for urban land uses. In this study, we aimed to develop AEs using a log-transformed linear model for eight urban landscaping tree species, taking into account belowground biomass. We purchased 117 urban landscaping trees from tree farms in South Korea and investigated their biomass fractions, carbon and nutrient concentrations, and annual growth rate using a destructive method. We also developed AEs for different tree compartments using diameter at breast height as an independent variable. The AEs obtained exhibited high suitability, as evidenced by their high R2 values (0.853–0.982 and 0.806–0.923 for aboveground and belowground biomass, respectively). The mean belowground biomass fraction across the different species was approximately 30%, suggesting that urban trees could allocate more belowground biomass than forest trees. Conversely, carbon and nitrogen concentrations varied significantly across species and compartments, and the mean annual carbon sequestration rate was 3.96 kg C year−1 tree−1. Therefore, the application of the AEs for urban trees may enhance the accuracy of the national greenhouse gas inventory for the settlement sector. Full article
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<p>Biomass allometric equations for the compartments of eight urban landscaping tree species in central South Korea.</p>
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<p>Biomass fractions in different tree compartments. The effect of the diameter at breast height (DBH) on the biomass distribution ratio was tested using a mixed-effect model (<span class="html-italic">Biomass ratio</span> ~ <span class="html-italic">DBH</span> + <span class="html-italic">Species</span>). The <span class="html-italic">p</span> and <span class="html-italic">R</span><sup>2</sup> values of the model are presented in each panel. <a href="#forests-15-02104-t0A1" class="html-table">Table A1</a> provides descriptive statistics for biomass distribution ratios according to tree species.</p>
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<p>Root biomass fraction distribution between urban and forest trees. The values obtained in the present study, which investigated urban landscaping trees in South Korea, were compared to those reported based on a global tree dataset (Ledo et al. [<a href="#B38-forests-15-02104" class="html-bibr">38</a>]) and a South Korean forest tree dataset (Son et al. [<a href="#B39-forests-15-02104" class="html-bibr">39</a>]). Data from the global tree dataset and this study were analyzed at the individual tree level, whereas data from forest trees in South Korea were available at the species level. Trees from the global dataset with a diameter at breast height (DBH) between 5 to 25 cm were extracted to account for the size-dependent variation in root biomass allocation. An error bar indicates a standard error.</p>
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<p>Annual carbon sequestration rates during the last five years according to species (<b>a</b>) and diameter at breast height (<b>b</b>). Inter-species differences in annual carbon sequestration rate were tested via analysis of covariance (<span class="html-italic">Annual carbon uptake rate</span> ~ <span class="html-italic">Species</span> + <span class="html-italic">DBH</span>). The different letters in the box represent significant mean differences, determined via Tukey’s HSD test.</p>
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<p>(<b>a</b>) The trees were uprooted using an excavator. Roots can be either underharvested due to uncollected roots remaining in the soil or overmeasured due to attached soil on the root samples. To minimize these sampling errors, (<b>b</b>) the soil around the excavated tree was excavated as widely and deeply as possible, and all tap and lateral secondary roots that remained in the soil were manually excavated; (<b>c</b>) the soil attached to the roots was removed by shaking and scraping as thoroughly as possible.</p>
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49 pages, 45431 KiB  
Article
Concepts Towards Nation-Wide Individual Tree Data and Virtual Forests
by Matti Hyyppä, Tuomas Turppa, Heikki Hyyti, Xiaowei Yu, Hannu Handolin, Antero Kukko, Juha Hyyppä and Juho-Pekka Virtanen
ISPRS Int. J. Geo-Inf. 2024, 13(12), 424; https://doi.org/10.3390/ijgi13120424 - 26 Nov 2024
Viewed by 1699
Abstract
Individual tree data could offer potential uses for both forestry and landscape visualization but has not yet been realized on a large scale. Relying on 5 points/m2 Finnish national laser scanning, we present the design and implementation of a system for producing, [...] Read more.
Individual tree data could offer potential uses for both forestry and landscape visualization but has not yet been realized on a large scale. Relying on 5 points/m2 Finnish national laser scanning, we present the design and implementation of a system for producing, storing, distributing, querying, and viewing individual tree data, both in a web browser and in a game engine-mediated interactive 3D visualization, “virtual forest”. In our experiment, 3896 km2 of airborne laser scanning point clouds were processed for individual tree detection, resulting in over 100 million trees detected, but the developed technical infrastructure allows for containing 10+ billion trees (a rough number of log-sized trees in Finland) to be visualized in the same system. About 92% of trees wider than 20 cm in diameter at breast height (corresponding to industrial log-size trees) were detected using national laser scanning data. Obtained relative RMSE for height, diameter, volume, and biomass (stored above-ground carbon) at individual tree levels were 4.5%, 16.9%, 30.2%, and 29.0%, respectively. The obtained RMSE and bias are low enough for operational forestry and add value over current area-based inventories. By combining the single-tree data with open GIS datasets, a 3D virtual forest was produced automatically. A comparison against georeferenced panoramic images was performed to assess the verisimilitude of the virtual scenes, with the best results obtained from sparse grown forests on sites with clear landmarks. Both the online viewer and 3D virtual forest can be used for improved decision-making in multifunctional forestry. Based on the work, individual tree inventory is expected to become operational in Finland in 2026 as part of the third national laser scanning program. Full article
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<p>The area for which the ITD was performed with coordinates for the corner points given in ETRS-TM35FIN. The location of the virtual forest test site (within the ITD area) is denoted as red dot. The utilized sample plots of the SCAN FOREST research infrastructure are located in the same area as the virtual forest test site, on an approx 5 by 5 km area. Background map © National Land Survey of Finland.</p>
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<p>The chosen test area, with dimensions of 1 by 1 km, with coordinates for the corner points given in ETRS-TM35FIN. Background map © National Land Survey of Finland.</p>
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<p>Overview of the software components applied.</p>
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<p>A pipeline for rendering raster map tiles into an image pyramid.</p>
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<p>The terrain area is divided into a grid of bounding boxes (white) that receive in scene initiation their individual tree counts from the server. The user’s (top left) current view is visualized by the frustum. The real time tree loading sequence has finalized the green outlined boxes while blue ones are currently being loaded and magenta ones wait in the stack.</p>
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<p>Found tree counts for both 2D and 3D methods as a function of DBH classes, compared to the reference.</p>
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<p>Relative bias (%) and relative RMSE (%) of attribute estimation as a function of DBH classes for trees over 20 cm in DBH, given for height (H), diameter (DBH), volume (V) and above ground biomass (AGB).</p>
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<p>Relative bias (%) and relative RMSE (%) of attribute estimation as a function of tree species for trees over 20 cm in DBH, given for height (H), diameter (DBH), volume (V), and above ground biomass (AGB).</p>
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<p>Individual trees drawn on the map with the following color codes: pine = brown, spruce = green and deciduous tree = yellow. The taller the tree, the darker the color of the circle marker. By clicking the tree, the most important characteristics of the tree, such as the species, height, diameter, volume, and biomass, are given in the info box.</p>
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<p>The user has selected a property on the map to query statistical data of the trees belonging to the property. The property has been selected by placing a blue marker on the map after which the boundaries of the selected property have become highlighted with blue color. The topographic map underneath the trees was obtained from the API of the National Land Survey of Finland. Individual trees drawn on the map with the following color codes: pine = brown, spruce = green and deciduous tree = yellow. The taller the tree, the darker the color of the circle marker.</p>
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<p>Dashboard visualizing the statistics of the trees from the selected area. Height and DBH histograms of the trees in the selected area are displayed on the right in addition to an estimation of the amount of carbon dioxide the trees have absorbed during their lifespan. Descriptive statistics for key attributes, such as mean diameter, total volume, biomass, basal area and the number of stems per hectare, have been presented on the left with tables in addition to an estimation of the value of the forest.</p>
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<p>User querying tree properties while filtering the virtual environment to show only trees less than 15 m tall.</p>
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<p>User querying tree properties while filtering the virtual environment to hide birches.</p>
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<p>Test site F on site (<b>left</b>) and as virtual scene (<b>right</b>). Correctly represented dominant trees almost begin to function as landmarks.</p>
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<p>Test site P on site (<b>left</b>) and as virtual scene (<b>right</b>). Absence of smaller trees in the virtual scene, species errors, and position errors of leaning trees lead to poor visual correspondence between the real and virtual forest. The waterbody and road however act as potential landmarks.</p>
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<p>Legend used in all comparison image pairs in this Appendix.</p>
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<p>Test site A, a mixed-species forest by the river flowing into a lake, showing the virtual scene (<b>top</b>) and on-site image (<b>bottom</b>). GNSS Position (TM-GK35FIN): N = 6,786,021 E = 398,869.</p>
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<p>Test site B, an uneven-aged mixed-species forest around a ditch and a forest road, showing the virtual scene (<b>top</b>) and on-site image (<b>bottom</b>). GNSS Position (TM-GK35FIN): N = 6,785,854 E = 398,919.</p>
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<p>Test site C, an open field in the middle of a mixed forest, showing the virtual scene (<b>top</b>) and on-site image (<b>bottom</b>). GNSS Position (TM-GK35FIN): N = 6,785,778 E = 399,079.</p>
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<p>Test site D, a hilly full-grown spruce forest, showing the virtual scene (<b>top</b>) and on-site image (<b>bottom</b>). GNSS Position (TM-GK35FIN): N = 6,785,759 E = 398,994.</p>
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<p>Test site E, a hilly pine forest growing also young spruces, showing the virtual scene (<b>top</b>) and on-site image (<b>bottom</b>). GNSS Position (TM-GK35FIN): N = 6,785,700 E = 398,893.</p>
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<p>Test site F, a thinned pine forest, showing the virtual scene (<b>top</b>) and on-site image (<b>bottom</b>). GNSS Position (TM-GK35FIN): N = 6,785,537 E = 398,805.</p>
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<p>Test site G, a full-grown spruce forest, showing the virtual scene (<b>top</b>) and on-site image (<b>bottom</b>). GNSS Position (TM-GK35FIN): N = 6,785,617 E = 398,869.</p>
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<p>Test site H, a pine-forest next to an overflown lake, showing the virtual scene (<b>top</b>) and on-site image (<b>bottom</b>). GNSS Position (TM-GK35FIN): N = 6,785,783 E = 399,513.</p>
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<p>Test site I, a stony hill in a pine forest, showing the virtual scene (<b>top</b>) and on-site image (<b>bottom</b>). GNSS Position (TM-GK35FIN): N = 6,785,688 E = 399,538.</p>
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<p>Test site J, a young thinned spruce forest on a slope, showing the virtual scene (<b>top</b>) and on-site image (<b>bottom</b>). GNSS Position (TM-GK35FIN): N = 6,785,686 E = 399,364.</p>
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<p>Test site K, a forest road going through a mixed species forest, showing the virtual scene (<b>top</b>) and on-site image (<b>bottom</b>). GNSS Position (TM-GK35FIN): N = 6,785,579 E = 399,550.</p>
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<p>Test site L, large glacially deposited rocks on a pine forest, showing the virtual scene (<b>top</b>) and on-site image (<b>bottom</b>). GNSS Position (TM-GK35FIN): N = 6,785,523 E = 399,537.</p>
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<p>Test site M, an opening in a dense young spruce forest, showing the virtual scene (<b>top</b>) and on-site image (<b>bottom</b>). GNSS Position (TM-GK35FIN): N = 6,785,548 E = 399,603.</p>
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<p>Test site N, an old abandoned field surrounded by mixed-species forests, showing the virtual scene (<b>top</b>) and on-site image (<b>bottom</b>). GNSS Position (TM-GK35FIN): N = 6,785,416 E = 399,275.</p>
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<p>Test site O, a paved road running between overflowing lakes with dead trees, showing the virtual scene (<b>top</b>) and on-site image (<b>bottom</b>). GNSS Position (TM-GK35FIN): N = 6,785,774 E = 399,163.</p>
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<p>Test site P, a river bank with a forest road and mixed species forest, showing the virtual scene (<b>top</b>) and on-site image (<b>bottom</b>). GNSS Position (TM-GK35FIN): N = 6,785,883 E = 398,913.</p>
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21 pages, 21195 KiB  
Article
Mapping the Future: Climate-Induced Changes in Aboveground Live-Biomass Carbon Density Across Mexico’s Coniferous Forests
by Carmela Sandoval-García, Jorge Méndez-González, Flores Andrés, Eulalia Edith Villavicencio-Gutiérrez, Fernando Paz-Pellat, Celestino Flores-López, Eladio Heriberto Cornejo-Oviedo, Alejandro Zermeño-González, Librado Sosa-Díaz, Marino García-Guzmán and José Ángel Villarreal-Quintanilla
Forests 2024, 15(11), 2032; https://doi.org/10.3390/f15112032 - 18 Nov 2024
Viewed by 1845
Abstract
Climate variations in temperature and precipitation significantly impact forest productivity. Precipitation influences the physiology and growth of species, while temperature regulates photosynthesis, respiration, and transpiration. This study developed bioclimatic models to assess how climate change will affect the carbon density of aboveground biomass [...] Read more.
Climate variations in temperature and precipitation significantly impact forest productivity. Precipitation influences the physiology and growth of species, while temperature regulates photosynthesis, respiration, and transpiration. This study developed bioclimatic models to assess how climate change will affect the carbon density of aboveground biomass (cdAGB) in Mexico’s coniferous forests for 2050 and 2070. We used cdAGB data from the National Forest and Soils Inventory (INFyS) of Mexico and 19 bioclimatic variables from WorldClim ver. 2.0. The best predictors of cdAGB were obtained using machine learning techniques with the “caret” library in R. The model was trained with 80% of the data and validated with the remaining 20% using Generalized Linear Models (GLMs). Current cdAGB prediction maps were generated using the best predictors. Future cdAGB was calculated with the average of three general circulation models (GCMs) of future climate projections from the Coupled Model Intercomparison Project Phase 5 (CMIP5), under four Representative Concentration Pathways (RCPs): 2.6, 4.5, 6.0, and 8.5 W/m2. The results indicate cdAGB losses in all climate scenarios, reaching up to 15 Mg C ha−1, and could occur under the RCP 8.5 scenario by 2070 in the central region of the country. Temperature-related variables are more important than precipitation variables. Bioclimatic variables can explain up to 20% of the total variance in cdAGB. The temperature in the study area is expected to increase by 2.66 °C by 2050 and 3.36 °C by 2070, while precipitation is expected to fluctuate by ±10% relative to the current values, which could geographically redistribute the cdAGB of the country’s coniferous forests. These findings underscore the need for forest management to focus not only on biodiversity conservation but also on the carbon storage capacity of these ecosystems. Full article
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<p>Study area in the global context (<b>left</b>) and regional context (<b>right</b>).</p>
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<p>Distribution of sites from the National Forest and Soil Inventory (2009–2012): stratum I (<b>a</b>), stratum II (<b>b</b>), and stratum III (<b>c</b>). The size of the circles and the color gradient indicate the values of carbon density in the aboveground live biomass (Mg C ha<sup>−1</sup>).</p>
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<p>Prediction of current carbon density of aboveground live biomass in Mexican conifer forests through bioclimatic models: stratum I (<b>a</b>), stratum II (<b>b</b>), and stratum III (<b>c</b>). Circle size and color gradient indicate values of carbon density of aboveground live biomass (Mg C ha<sup>−1</sup>).</p>
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<p>Changes in carbon density of aboveground live biomass in Mexican conifer forests under the RCP 2.6 to 8.5 scenarios (<b>a</b>–<b>d</b>) for the years 2050 and 2070 (<b>e</b>–<b>h</b>) in stratum I. Colored areas represent 40 km radius buffers around each INFyS site; uncolored areas correspond to other vegetation types different from conifer forests.</p>
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<p>Changes in carbon density of aboveground live biomass in Mexican conifer forests under the RCP 2.6 to 8.5 scenarios (<b>a</b>–<b>d</b>), for the years 2050 and 2070 (<b>e</b>–<b>h</b>) in stratum II. Colored areas represent 40 km radius buffers around each INFyS site; uncolored areas correspond to other vegetation types different from conifer forests.</p>
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<p>Changes in the carbon density of aboveground live biomass in Mexican conifer forests under the RCP 2.6 to 8.5 scenarios (<b>a</b>–<b>d</b>) for the years 2050 and 2070 (<b>e</b>–<b>h</b>) in stratum III. Colored areas represent 40 km radius buffers around each INFyS site; uncolored areas correspond to other vegetation types different from conifer forests.</p>
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<p>Wilcoxon test for comparing medians of the current variable with each climate scenario, in strata I (<b>a</b>,<b>b</b>), II (<b>c</b>,<b>d</b>), and III (<b>e</b>,<b>f</b>). Bio 05: Max Temperature of Warmest Month (°C); Bio 10: Mean Temperature of Warmest Quarter (°C); Bio 12: Annual Precipitation (mm); Bio 13: Precipitation of Wettest Month (mm); Bio 18: Precipitation of Warmest Quarter (mm). Significance levels: ns (Not significant), * (Significant at 0.05%), ** (Significant at 1%), *** (Significant at 0.1%), **** (Significant at 0.01%).</p>
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<p>Estimated uncertainty (standard error) of carbon density of aboveground live biomass in Mexican conifer forests, for strata I (<b>a</b>), II (<b>b</b>), and III (<b>c</b>) under RCP 85 and for the year 2070.</p>
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23 pages, 2713 KiB  
Article
Incorporating Forest Mapping-Related Uncertainty into the Error Propagation of Wall-to-Wall Biomass Maps: A General Approach for Large and Small Areas
by Hassan C. David, Alexander C. Vibrans, Rorai P. Martins-Neto, Ana Paula Dalla Corte and Sylvio Péllico Netto
Remote Sens. 2024, 16(22), 4295; https://doi.org/10.3390/rs16224295 - 18 Nov 2024
Viewed by 721
Abstract
The sources of uncertainty in wall-to-wall AGB maps propagate from the tree to pixel, but uncertainty due to forest cover mapping is rarely incorporated into the error propagation process. This study aimed to (1) elaborate an analytical procedure to incorporate forest-mapping-related uncertainty into [...] Read more.
The sources of uncertainty in wall-to-wall AGB maps propagate from the tree to pixel, but uncertainty due to forest cover mapping is rarely incorporated into the error propagation process. This study aimed to (1) elaborate an analytical procedure to incorporate forest-mapping-related uncertainty into the error propagation from plot and pixel predictions; (2) develop a stratified estimator with a model-assisted estimator for small and large areas; and (3) estimate the effect of ignoring the mapping uncertainty on the confidence intervals (CIs) for totals. Data consist of a subset of the Brazilian national forest inventory (NFI) database, comprising 75 counties that, once aggregated, served as strata for the stratified estimator. On-ground data were gathered from 152 clusters (plots) and remotely sensed data from Landsat-8 scenes. Four major contributions are highlighted. First, we describe how to incorporate forest-mapping-related uncertainty into the CIs of any forest attribute and spatial resolution. Second, stratified estimators perform better than non-stratified estimators for forest area estimation when the response variable is forest/non-forest. Comparing our stratified estimators, this study indicated greater precision for the stratified estimator than for the regression estimator. Third, using the ratio estimator, we found evidence that the simple field plot information provided by the NFI clusters is sufficient to estimate the proportion forest for large regions as accurately as remote-sensing-based methods, albeit with less precision. Fourth, ignoring forest-mapping-related uncertainty erroneously narrows the CI width as the estimate of proportion forest area decreases. At the small-area level, forest-mapping-related uncertainty led to CIs for total AGB as much as 63% wider in extreme cases. At the large-area level, the CI was 5–7% wider. Full article
(This article belongs to the Special Issue Remote Sensing of Carbon Fluxes and Stocks II)
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<p>Distribution of clusters within the study area following the NFI regular 20 km <span class="html-italic">×</span> 20 km grid. Black lines represent county boundaries.</p>
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<p>Analytical procedure for propagating errors in forest AGB mapping.</p>
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<p>Illustration of the NFI cluster overlapping a 30 m spatial resolution satellite image.</p>
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<p>Relationship between predicted vs. observed plot AGB. Blackline is the 1:1 relation. Data are from the validation dataset (15% from the total).</p>
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<p>Spatial distribution of forest AGB in Mg ha<sup>−1</sup> stocked in the study area and counties. Numbers 1–10 rank the 10 most biomass-stocked counties.</p>
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<p>Differences while estimating confidence intervals for AGB (in Mg) with and without adding the forest-mapping-related uncertainty. Markers represent the 75 counties (small areas).</p>
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17 pages, 2835 KiB  
Article
A Study on the Growth Model of Natural Forests in Southern China Under Climate Change: Application of Transition Matrix Model
by Xiangjiang Meng, Zhengrui Ma, Ying Xia, Jinghui Meng, Yuhan Bai and Yuan Gao
Forests 2024, 15(11), 1947; https://doi.org/10.3390/f15111947 - 5 Nov 2024
Viewed by 713
Abstract
This study establishes a climate-sensitive transition matrix growth model and predicts forest growth under different carbon emission scenarios (representative concentration pathways RCP2.6, RCP4.5, and RCP8.5) over the next 40 years. Data from the Eighth (2013) and Ninth (2019) National Forest Resource Inventories in [...] Read more.
This study establishes a climate-sensitive transition matrix growth model and predicts forest growth under different carbon emission scenarios (representative concentration pathways RCP2.6, RCP4.5, and RCP8.5) over the next 40 years. Data from the Eighth (2013) and Ninth (2019) National Forest Resource Inventories in Chongqing and climate data from Climate AP are utilized. The model is used to predict forest growth and compare the number of trees, basal area, and stock volume under different climate scenarios. The results show that the climate-sensitive transition matrix growth model has high accuracy. The relationships between the variables and forest growth, mortality, and recruitment correspond to natural succession and growth. Although the number of trees, basal area, and stock volume do not differ significantly for different climate scenarios, the forest has sufficient seedling regeneration and large-diameter trees. The growth process aligns with succession, with pioneer species being replaced by climax species. The proposed climate-sensitive transition matrix growth model fills the gap in growth models for natural secondary forests in Chongqing and is an accurate method for predicting forest growth. The model can be used for long-term prediction of forest stands to understand future forest growth trends and provide reliable references for forest management. Forest growth can be predicted for different harvesting intensities to determine the optimal intensity to guide natural forest management in Chongqing City. The results of this study can help formulate targeted forest management policies to deal more effectively with climate change and promote sustainable forest health. Full article
(This article belongs to the Special Issue Estimation and Monitoring of Forest Biomass and Fuel Load Components)
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<p>Distribution of sample plots in Chongqing City.</p>
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<p>The initial diameter distribution (2018) and the simulated diameter distributions after 40 years under different climate scenarios (RCP 2.6, RCP 4.5, and RCP 8.5).</p>
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<p>The diameter distribution over the next 40 years.</p>
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<p>The change in forest stand volume under different climate scenarios (RCP 2.6, RCP 4.5, RCP 8.5) over the next 40 years.</p>
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13 pages, 1297 KiB  
Article
Tree Height–Diameter Model of Natural Coniferous and Broad-Leaved Mixed Forests Based on Random Forest Method and Nonlinear Mixed-Effects Method in Jilin Province, China
by Qigang Xu, Fan Yang, Sheng Hu, Xiao He and Yifeng Hong
Forests 2024, 15(11), 1922; https://doi.org/10.3390/f15111922 - 31 Oct 2024
Viewed by 752
Abstract
Objective: The purpose of this article was to use the Random Forest method and nonlinear mixed-effects method to develop a model for determining tree height–diameter at breast height (DBH) for a natural coniferous and broad-leaved mixed forest in Jilin Province and to compare [...] Read more.
Objective: The purpose of this article was to use the Random Forest method and nonlinear mixed-effects method to develop a model for determining tree height–diameter at breast height (DBH) for a natural coniferous and broad-leaved mixed forest in Jilin Province and to compare the advantages and disadvantages of the two methods to provide a basis for forest management practice. Method: Based on the Chinese national forest inventory data, the Random Forest method and nonlinear mixed-effects method were used to develop a tree height–DBH model for a natural coniferous and broad-leaved mixed forest in Jilin Province. Results: The Random Forest method performed well on both the fitting set and validation set, with an R2 of 0.970, MAE of 0.605, and RMSE of 0.796 for the fitting set and R2 of 0.801, MAE of 1.44 m, and RMSE of 1.881 m for the validation set. Compared with the nonlinear mixed-effects method, the Random Forest model improved R2 by 33.83%, while the MAE and RMSE decreased by 67.74% and 66.44%, respectively, in the fitting set; the Random Forest model improved R2 by 9.88%, while the MAE and RMSE decreased by 14.38% and 12.05%, respectively, in the validation set. Conclusions: The tree height–DBH model constructed based on the Random Forest method had higher prediction accuracy for a natural coniferous and broad-leaved mixed forest in Jilin Province and had stronger adaptability for higher-dimensional data, which can be used for tree height prediction in the study area. Full article
(This article belongs to the Special Issue Estimation and Monitoring of Forest Biomass and Fuel Load Components)
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<p>The workflow employed in this study to quantify the tree heights using NLME method and Random Forest method.</p>
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<p>Residuals for tree height–diameter models (NLME model; Random Forest model).</p>
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18 pages, 2131 KiB  
Article
Bamboo Forests: Unleashing the Potential for Carbon Abatement and Local Income Improvements
by Jiaming Xu, Shen Tan, Han Wang, Xin Zhang and Yifeng Hong
Forests 2024, 15(11), 1907; https://doi.org/10.3390/f15111907 - 29 Oct 2024
Viewed by 844
Abstract
Bamboo forests exhibit a unique efficient growth pattern that makes them invaluable in reducing atmospheric CO2 levels. Additionally, bamboo forests offer a diverse range of products, thus holding the potential to bolster local income. Despite these benefits, the comprehensive assessment of bamboo [...] Read more.
Bamboo forests exhibit a unique efficient growth pattern that makes them invaluable in reducing atmospheric CO2 levels. Additionally, bamboo forests offer a diverse range of products, thus holding the potential to bolster local income. Despite these benefits, the comprehensive assessment of bamboo forests’ potential in both carbon abatement and improving local income enhancement has been hindered by the absence of a detailed bamboo biomass map. In this study, we address this gap by amalgamating a bamboo aboveground biomass (AGB) map covering three prominent producing provinces in southern China, utilizing multi-source remote sensing datasets. The results not only demonstrate a satisfactory consistency with China’s Ninth National Forest Inventory but also provide a more detailed spatial distribution. Based on this AGB estimation, we project an approximately threefold potential increase in annual bamboo culm harvest from existing bamboo forests. This represents a significant opportunity for expanding carbon abatement efforts, elevating local income levels, and facilitating the production of bamboo-derived biofuels. Furthermore, the adoption of an optimized management strategy has the potential to further enhance bamboo production. This study generates the first high-resolution bamboo AGB map and underscores the substantial potential of China’s bamboo forests in contributing to carbon sequestration and improving local income. The favorable income generated for local residents can serve as a compelling incentive for the implementation of sustainable forest management practices, offering a promising pathway toward achieving carbon-related objectives within the forestry sector and providing necessary support for forestry designation projects. Full article
(This article belongs to the Special Issue Ecological Research in Bamboo Forests)
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<p>Workflow of (<b>a</b>) this study, (<b>b</b>) AGB estimation, and (<b>c</b>) potential evaluation. The LGBM (light gradient boosting machine) algorithm is employed for AGB fitting. The details of the optimized management scenario refer to Gu et al. [<a href="#B19-forests-15-01907" class="html-bibr">19</a>].</p>
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<p>Position of the study area and spatial distribution of the field samples. The bamboo map in the background is from Qi et al. [<a href="#B4-forests-15-01907" class="html-bibr">4</a>] with 30 m resolution. The position of Anji county and AGB samples are labeled in the figure.</p>
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<p>Comparison of estimated bamboo AGB by the LGBM against field observation. The fitting function and statistical metrics are labeled in the figure. MAE represents the mean absolute error; RMSE represents the root mean square error.</p>
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<p>Spatial distribution of bamboo AGB in three provinces. The bamboo AGB and area for each province in this study are labeled in black, while the data suggested by the Ninth National Forest Inventory are labeled in blue.</p>
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<p>Spatial distribution of annual bamboo potential in (<b>a</b>) producing culms, (<b>b</b>) producing biofuels, and (<b>c</b>) providing local income. The province-scale potential is labeled in this figure. The border of cities is represented by a grey line and the border of provinces is labeled by a black line.</p>
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<p>Proportion of major bamboo products in Zhejiang province for 2020.</p>
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19 pages, 5207 KiB  
Article
Enhancing the Precision of Forest Growing Stock Volume in the Estonian National Forest Inventory with Different Predictive Techniques and Remote Sensing Data
by Temitope Olaoluwa Omoniyi and Allan Sims
Remote Sens. 2024, 16(20), 3794; https://doi.org/10.3390/rs16203794 - 12 Oct 2024
Viewed by 879
Abstract
Estimating forest growing stock volume (GSV) is crucial for forest growth and resource management, as it reflects forest productivity. National measurements are laborious and costly; however, integrating satellite data such as optical, Synthetic Aperture Radar (SAR), and airborne laser scanning (ALS) with National [...] Read more.
Estimating forest growing stock volume (GSV) is crucial for forest growth and resource management, as it reflects forest productivity. National measurements are laborious and costly; however, integrating satellite data such as optical, Synthetic Aperture Radar (SAR), and airborne laser scanning (ALS) with National Forest Inventory (NFI) data and machine learning (ML) methods has transformed forest management. In this study, random forest (RF), support vector regression (SVR), and Extreme Gradient Boosting (XGBoost) were used to predict GSV using Estonian NFI data, Sentinel-2 imagery, and ALS point cloud data. Four variable combinations were tested: CO1 (vegetation indices and LiDAR), CO2 (vegetation indices and individual band reflectance), CO3 (LiDAR and individual band reflectance), and CO4 (a combination of vegetation indices, individual band reflectance, and LiDAR). Across Estonia’s geographical regions, RF consistently delivered the best performance. In the northwest (NW), the RF model achieved the best performance with the CO3 combination, having an R2 of 0.63 and an RMSE of 125.39 m3/plot. In the southwest (SW), the RF model also performed exceptionally well, achieving an R2 of 0.73 and an RMSE of 128.86 m3/plot with the CO4 variable combination. In the northeast (NE), the RF model outperformed other ML models, achieving an R2 of 0.64 and an RMSE of 133.77 m3/plot under the CO4 combination. Finally, in the southeast (SE) region, the best performance was achieved with the CO4 combination, yielding an R2 of 0.70 and an RMSE of 21,120.72 m3/plot. These results underscore RF’s precision in predicting GSV across diverse environments, though refining variable selection and improving tree species data could further enhance accuracy. Full article
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<p>Cluster network (<b>a</b>) of the Estonia NFI permanent and temporary plot (2018–2022); Cartogram of the elevation model of the land cover (<b>b</b>).</p>
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<p>Methodology flowchart for this study.</p>
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<p>Scatter plot of observed vs. predicted GSV values for the validation plots using the best predictive model. The symbols * and ** represent the CO3 and CO4 combinations, respectively. (<b>a</b>), (<b>b</b>), (<b>c</b>), and (<b>d</b>) denote the random forest-based models for the northwest, southwest, northeast, and southeast regions, respectively.</p>
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<p>Scatter plot of observed vs. predicted GSV values for the validation plots using the best predictive model. The symbols * and ** represent the CO3 and CO4 combinations, respectively. (<b>a</b>), (<b>b</b>), (<b>c</b>), and (<b>d</b>) denote the random forest-based models for the northwest, southwest, northeast, and southeast regions, respectively.</p>
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<p>Variable important plot using the best predictive model. Where (<b>a</b>), (<b>b</b>), (<b>c</b>), and (<b>d</b>) denote the random forest-based models for the northwest, southwest, northeast, and southeast regions, respectively.</p>
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17 pages, 5872 KiB  
Article
Prediction Models and Feature Importance Analysis for Service State of Tunnel Sections Based on Machine Learning
by Debo Zhao, Yujia Yang, Chengyong Cao and Bin Liu
Appl. Sci. 2024, 14(20), 9167; https://doi.org/10.3390/app14209167 - 10 Oct 2024
Viewed by 1127
Abstract
The evaluation of tunnel service conditions is a core problem in the maintenance of tunnel structures during their life cycles. To address this problem, machine learning algorithms were applied to the National Tunnel Inventory (NTI) database of the Federal Highway Administration of the [...] Read more.
The evaluation of tunnel service conditions is a core problem in the maintenance of tunnel structures during their life cycles. To address this problem, machine learning algorithms were applied to the National Tunnel Inventory (NTI) database of the Federal Highway Administration of the United States to predict the service states of the structural, civil, and non-structural sections of a tunnel, respectively. The results indicate that ensemble learning algorithms such as Light Gradient Boosting Machine (LGBM) and Random Forest outperform Support Vector Machine, Multi-Layer Perceptron, Decision Tree, and K-Nearest Neighbor in solving imbalanced classification problems presented in the NTI database. The machine learning models established using the LGBM algorithm exhibited prediction accuracies of 90.9%, 96.4%, and 77.3% for the structural, civil, and non-structural sections, respectively. The importance sorting of features influencing the tunnel’s service state was then performed based on the LGBM model, revealing that the features with a significant impact on the service states of the structural, civil, and non-structural sections are service time, tunnel length and width, geographic position (longitude and latitude), minimum vertical clearance, annual average daily traffic (AADT), and annual average daily truck traffic (AADTT). Data-driven LGBM models identified human factors such as AADT and AADTT as key features influencing the service states of tunnels’ structural sections, and these factors should be taken into consideration in further research to elucidate the potential physical mechanisms. Full article
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<p>Distribution of tunnel features in the NTI database (2020): (<b>a</b>) tunnel lengths (unit: meters), (<b>b</b>) tunnel service time (unit: years), and (<b>c</b>) annual average daily traffic (unit: vehicles).</p>
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<p>Distribution of tunnels’ geographic locations.</p>
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<p>A schematic diagram of the LGBM algorithm solving classification problems.</p>
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<p>A comparison of the evaluation metrics: (<b>a</b>) structural section; (<b>b</b>) civil section; and (<b>c</b>) non-structural section.</p>
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<p>Confusion matrices and Receiver Operating Characteristic (ROC) curves for LGBM models: (<b>a</b>) structural section; (<b>b</b>) civil section; and (<b>c</b>) non-structural section.</p>
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<p>The feature importance rankings and SHAP rankings (top 20) for the (<b>a</b>) structural; (<b>b</b>) civil; and (<b>c</b>) non-structural sections.</p>
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<p>The feature importance rankings and SHAP rankings (top 20) for the (<b>a</b>) structural; (<b>b</b>) civil; and (<b>c</b>) non-structural sections.</p>
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<p>Accident types versus traffic accidents [<a href="#B27-applsci-14-09167" class="html-bibr">27</a>].</p>
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<p>Illustration of structural damage accelerating long-term performance degradation.</p>
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22 pages, 7805 KiB  
Article
Machine Learning Approach for Local Atmospheric Emission Predictions
by Alessandro Marongiu, Gabriele Giuseppe Distefano, Marco Moretti, Federico Petrosino, Giuseppe Fossati, Anna Gilia Collalto and Elisabetta Angelino
Air 2024, 2(4), 380-401; https://doi.org/10.3390/air2040022 - 3 Oct 2024
Viewed by 1131
Abstract
This paper presents a novel machine learning methodology able to extend the results of detailed local emission inventories to larger domains where emission estimates are not available. The first part of this work consists in the development of an emission inventory of elemental [...] Read more.
This paper presents a novel machine learning methodology able to extend the results of detailed local emission inventories to larger domains where emission estimates are not available. The first part of this work consists in the development of an emission inventory of elemental carbon (EC), black carbon (BC), organic carbon (OC), and levoglucosan (LG) obtained from the detailed emission estimates available from the Project LIFE PREPAIR for the Po Basin in north Italy. The emissions of these chemical species in combination with particulate primary emissions and gaseous precursors are very important information in source apportionment and in the impact assessment of the different emission sources in air quality. To gain a better understanding of the origins of atmospheric pollution, it is possible to combine measurements with emission estimates for the particulate matter fractions known as EC, BC, OC, and LG. To identify the sources of emissions, it is usual practice to use the ratio of the measured EC, OC, TC (Total Carbon), and LG. The PREPAIR emission estimates and these new calculations are then used to train the Random Forest (RF) algorithm, considering a large array of local variables, such as taxes, the characteristics of urbanization and dwellings, the number of employees detailed for economic activities, occupation levels and land cover. The outcome of the comparison of the predictions of the machine learning implemented model (ML) with the estimates obtained for the same areas by two independent methods, local disaggregation of the national emission inventory and Copernicus Air Modelling Service (CAMS) emissions estimates, is extremely encouraging and confirms it also as a promising approach in terms of effort saving. The implemented modelling approach identifies the most important variables affecting the spatialization of different pollutants in agreement with the main emission source characteristics and is suitable for harmonization of the results of different local emission inventories with national emission reporting. Full article
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<p>Characterization of the Po Basin study area, with emphasis on urbanized area, road networks, and topographical features.</p>
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<p>Processes for local and national emission inventories in Italy (adapted from SNPA 2016 [<a href="#B38-air-02-00022" class="html-bibr">38</a>]).</p>
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<p>Spatial distribution of total OC emissions (<b>a</b>), non-industrial combustion (<b>b</b>) and road transport (<b>c</b>).</p>
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<p>Spatial distribution of total BC emission (<b>a</b>), non-industrial combustion (<b>b</b>) and road transport (<b>c</b>).</p>
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<p>Comparison of Emissions in Italian Provinces. ML calculation (_RF), Top-down of the National Emission Inventory (_NIR) and CAMS Emissions (_CAMS).</p>
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<p>Emission density maps for PM<sub>2.5</sub>, OC, BC and LG estimated for Italy by ML propagation of the Po Basin inventories (t/km<sup>2</sup>).</p>
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<p>Emission density maps for PM<sub>2.5</sub>, OC, BC and LG estimated for Italy by ML propagation of the Po Basin inventories (t/km<sup>2</sup>).</p>
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<p>NASA Worldview (<b>left</b>) and PM<sub>10</sub> emission map calculated by ML (<b>right</b>).</p>
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14 pages, 3976 KiB  
Article
Generic and Specific Models for Volume Estimation in Forest and Savanna Phytophysiognomies in Brazilian Cerrado
by Yanara Ferreira de Souza, Eder Pereira Miguel, Adriano José Nogueira Lima, Álvaro Nogueira de Souza, Eraldo Aparecido Trondoli Matricardi, Alba Valéria Rezende, Joberto Veloso de Freitas, Hallefy Junio de Souza, Kennedy Nunes Oliveira, Maria de Fátima de Brito Lima and Leonardo Job Biali
Plants 2024, 13(19), 2769; https://doi.org/10.3390/plants13192769 - 3 Oct 2024
Viewed by 907
Abstract
The Cerrado has high plant and vertebrate diversity and is an important biome for conserving species and provisioning ecosystem services. Volume equations in this biome are scarce because of their size and physiognomic diversity. This study was conducted to develop specific volumetric models [...] Read more.
The Cerrado has high plant and vertebrate diversity and is an important biome for conserving species and provisioning ecosystem services. Volume equations in this biome are scarce because of their size and physiognomic diversity. This study was conducted to develop specific volumetric models for the phytophysiognomies Gallery Forest, Dry Forest, Forest Savannah, and Savannah Woodland, a generic model and a model for Cerrado forest formation. Twelve 10 m × 10 m (100 m²) (National Forest Inventory) plots were used for each phytophysiognomy at different sites (regions) of the Federal District (FD) where trees had a diameter at breast height (DBH; 1.30 m) ≥5 cm in forest formations and a diameter at base height (Db; 0.30 m) ≥5 cm in savanna formations. Their diameters and heights were measured, they were cut and cubed, and the volume of each tree was obtained according to the Smalian methodology. Linear and nonlinear models were adjusted. Criteria for the selection of models were determined using correlation coefficients, the standard error of the estimates, and a graphical analysis of the residues. They were later validated by the chi-square test. The resultant models indicated that fit by specific phytophysiognomy was ideal; however, the generic and forest formation models exhibited similar performance to specific models and could be used in extensive areas of the Cerrado, where they represent a high potential for generalization. To further increase our understanding, similar research is recommended for the development of specific and generic models of the total volume in Cerrado areas. Full article
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<p>Venn diagram illustrating species sharing and exclusivity for different phytophysiognomies.</p>
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<p>Residual dispersal (<b>a</b>), observed and predicted values (<b>b</b>) and distribution of error classes (<b>c</b>) for Gallery Forest model (6).</p>
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<p>Residual dispersal (<b>a</b>), observed and predicted values (<b>b</b>) and distribution of error classes (<b>c</b>) for the Dry Forest model (3).</p>
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<p>Residual dispersal (<b>a</b>), observed and predicted values (<b>b</b>) and distribution of error classes (<b>c</b>) for the model (6) of Forest Savannah.</p>
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<p>Residual dispersal (<b>a</b>), observed and predicted values (<b>b</b>) and distribution of error classes (<b>c</b>) for the model (4) of Savannah Woodland.</p>
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<p>Residual dispersal (<b>a</b>), observed and predicted values (<b>b</b>) and distribution of error classes (<b>c</b>) for model (6) of generic model.</p>
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<p>Residual dispersal (<b>a</b>), observed and predicted values (<b>b</b>) and distribution of error classes (<b>c</b>) for the model (4) of Forest Formation.</p>
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<p>Location of sampling points of the different phytophysiognomies, Brazil.</p>
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15 pages, 2732 KiB  
Article
Allometric Models of Aboveground Biomass in Mangroves Compared with Those of the Climate Action Reserve Standard Applied in the Carbon Market
by Carlos Roberto Ávila-Acosta, Marivel Domínguez-Domínguez, César Jesús Vázquez-Navarrete, Rocío Guadalupe Acosta-Pech and Pablo Martínez-Zurimendi
Resources 2024, 13(9), 129; https://doi.org/10.3390/resources13090129 - 17 Sep 2024
Viewed by 1509
Abstract
The standardized methods used in carbon markets require measurement of the biomass and carbon stored in trees, which can be quantified through allometric equations. The objective of this study was to analyze aboveground biomass estimates with allometric models in three mangrove species and [...] Read more.
The standardized methods used in carbon markets require measurement of the biomass and carbon stored in trees, which can be quantified through allometric equations. The objective of this study was to analyze aboveground biomass estimates with allometric models in three mangrove species and compare them with those used by the Climate Action Reserve (CAR) standard. The mangrove forest in Tabasco, Mexico, was certified with the Forest Protocol for Mexico Version 2.0 (FPM) of the CAR standard. Allometric equations for mangrove species were reviewed to determine the most suitable equation for the calculation of biomass. The predictions of the allometric equations of the FPM were analyzed with data from Tabasco from the National Forest and Soil Inventory 2015–2020, and the percentages of trees within the ranges of diameters of the FPM equations were determined. The FPM equations generated higher biomass values for Rhizophora mangle and lower values for Avicennia germinans than the seven equations with which they were compared. In the mangrove swamp of Ejido Úrsulo Galván, Tabasco, 81.8% of the biomass of A. germinans, 34.4% of Laguncularia racemosa and 24.0% of R. mangle were within the diameter range of the FPM equations, and in Tabasco, 28.5% of A. germinans, 16.7% of L. racemosa and 5.7% of R. mangle were within the diameter range. For A. germinans and R. mangle, we recommend using the equation that considers greater maximum diameters. The allometric equations of the FPM do not adequately predict a large percentage of the biomass. Full article
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<p>Predictions of the allometric equation of Smith and Whelan [<a href="#B16-resources-13-00129" class="html-bibr">16</a>] were applied to <span class="html-italic">A. germinans</span> and compared with the predictions of equations developed by other authors. Source of the equations: Smith y Whelan (2006) [<a href="#B16-resources-13-00129" class="html-bibr">16</a>], Day et al. (1987) [<a href="#B9-resources-13-00129" class="html-bibr">9</a>], Fromard et al. (1998) [<a href="#B18-resources-13-00129" class="html-bibr">18</a>], Imbert and Rollet (1989) [<a href="#B17-resources-13-00129" class="html-bibr">17</a>], Yepes et al. (2016) [<a href="#B22-resources-13-00129" class="html-bibr">22</a>], Komiyama et al. (2005) [<a href="#B4-resources-13-00129" class="html-bibr">4</a>], Chave et al. (2005) [<a href="#B20-resources-13-00129" class="html-bibr">20</a>].</p>
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<p>Predictions of the allometric equation of Day et al. [<a href="#B9-resources-13-00129" class="html-bibr">9</a>] were applied to <span class="html-italic">L. racemosa</span> and compared with the predictions of equations developed by other authors. Source of the equations: Day et al. (1987) [<a href="#B9-resources-13-00129" class="html-bibr">9</a>], Smith y Whelan (2006) [<a href="#B16-resources-13-00129" class="html-bibr">16</a>], Fromard et al. (1998) [<a href="#B18-resources-13-00129" class="html-bibr">18</a>], Imbert and Rollet (1989) [<a href="#B17-resources-13-00129" class="html-bibr">17</a>], Medeiros and Sampaio (2008) [<a href="#B21-resources-13-00129" class="html-bibr">21</a>], Komiyama et al. (2005) [<a href="#B4-resources-13-00129" class="html-bibr">4</a>], Chave et al. (2005) [<a href="#B20-resources-13-00129" class="html-bibr">20</a>].</p>
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<p>Predictions of the allometric equation of Day et al. [<a href="#B9-resources-13-00129" class="html-bibr">9</a>] were applied to <span class="html-italic">R. mangle</span> and compared with the predictions of equations developed by other authors. Source of the equations: Day et al. (1987) [<a href="#B9-resources-13-00129" class="html-bibr">9</a>], Smith y Whelan (2006) [<a href="#B16-resources-13-00129" class="html-bibr">16</a>], Fromard et al. (1998) [<a href="#B18-resources-13-00129" class="html-bibr">18</a>], Imbert and Rollet (1989) [<a href="#B17-resources-13-00129" class="html-bibr">17</a>], Gomes and Schaeffer-Novelli (2005) [<a href="#B19-resources-13-00129" class="html-bibr">19</a>], Yepes et al. (2016) [<a href="#B22-resources-13-00129" class="html-bibr">22</a>], Medeiros and Sampaio (2008) [<a href="#B21-resources-13-00129" class="html-bibr">21</a>], Komiyama et al. (2005) [<a href="#B4-resources-13-00129" class="html-bibr">4</a>], Chave et al. (2005) [<a href="#B20-resources-13-00129" class="html-bibr">20</a>].</p>
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<p>Biomass of <span class="html-italic">A. germinans</span> obtained via different allometric equations within the ranges of diameters. The solid line represents the biomass obtained at 21.5 cm in diameter according to the Smith and Whelan equation [<a href="#B16-resources-13-00129" class="html-bibr">16</a>]. Source of the equations: Smith y Whelan (2006) [<a href="#B16-resources-13-00129" class="html-bibr">16</a>], Day et al. (1987) [<a href="#B9-resources-13-00129" class="html-bibr">9</a>], Fromard et al. (1998) [<a href="#B18-resources-13-00129" class="html-bibr">18</a>], Imbert and Rollet (1989) [<a href="#B17-resources-13-00129" class="html-bibr">17</a>], Yepes et al. (2016) [<a href="#B22-resources-13-00129" class="html-bibr">22</a>], Komiyama et al. (2005) [<a href="#B4-resources-13-00129" class="html-bibr">4</a>], Chave et al. (2005) [<a href="#B20-resources-13-00129" class="html-bibr">20</a>].</p>
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<p>Biomass of <span class="html-italic">L. racemosa</span> obtained with various allometric equations within the ranges of diameters. The solid line represents the biomass obtained at a diameter of 10 cm via the equation of Day et al. [<a href="#B9-resources-13-00129" class="html-bibr">9</a>]. Source of the equations: Day et al. (1987) [<a href="#B9-resources-13-00129" class="html-bibr">9</a>], Smith y Whelan (2006) [<a href="#B16-resources-13-00129" class="html-bibr">16</a>], Fromard et al. (1998) [<a href="#B18-resources-13-00129" class="html-bibr">18</a>], Imbert and Rollet (1989) [<a href="#B17-resources-13-00129" class="html-bibr">17</a>], Medeiros and Sampaio (2008) [<a href="#B21-resources-13-00129" class="html-bibr">21</a>], Komiyama et al. (2005) [<a href="#B4-resources-13-00129" class="html-bibr">4</a>], Chave et al. (2005) [<a href="#B20-resources-13-00129" class="html-bibr">20</a>].</p>
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<p>Biomass of <span class="html-italic">R. mangle</span> obtained with various allometric equations within the ranges of diameters. The solid line represents the biomass obtained at a diameter of 10 cm via the equation of Day et al. [<a href="#B9-resources-13-00129" class="html-bibr">9</a>]. Source of the equations: Day et al. (1987) [<a href="#B9-resources-13-00129" class="html-bibr">9</a>], Smith y Whelan (2006) [<a href="#B16-resources-13-00129" class="html-bibr">16</a>], Fromard et al. (1998) [<a href="#B18-resources-13-00129" class="html-bibr">18</a>], Imbert and Rollet (1989) [<a href="#B17-resources-13-00129" class="html-bibr">17</a>], Gomes and Schaeffer-Novelli (2005) [<a href="#B19-resources-13-00129" class="html-bibr">19</a>], Yepes et al. (2016) [<a href="#B22-resources-13-00129" class="html-bibr">22</a>], Medeiros and Sampaio (2008) [<a href="#B21-resources-13-00129" class="html-bibr">21</a>], Komiyama et al. (2005) [<a href="#B4-resources-13-00129" class="html-bibr">4</a>], Chave et al. (2005) [<a href="#B20-resources-13-00129" class="html-bibr">20</a>].</p>
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<p>Average diameters of <span class="html-italic">A. germinans</span>, <span class="html-italic">L. racemosa</span> and <span class="html-italic">R. mangle</span> according to the National Forest and Soil Inventory 2015–2020 CONAFOR for Tabasco.</p>
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19 pages, 5511 KiB  
Article
Biomass Equations and Carbon Stock Estimates for the Southeastern Brazilian Atlantic Forest
by Tatiana Dias Gaui, Vinicius Costa Cysneiros, Fernanda Coelho de Souza, Hallefy Junio de Souza, Telmo Borges Silveira Filho, Daniel Costa de Carvalho, José Henrique Camargo Pace, Graziela Baptista Vidaurre and Eder Pereira Miguel
Forests 2024, 15(9), 1568; https://doi.org/10.3390/f15091568 - 6 Sep 2024
Viewed by 1233
Abstract
Tropical forests play an important role in mitigating global climate change, emphasizing the need for reliable estimates of forest carbon stocks at regional and global scales. This is essential for effective carbon management, which involves strategies like emission reduction and enhanced carbon sequestration [...] Read more.
Tropical forests play an important role in mitigating global climate change, emphasizing the need for reliable estimates of forest carbon stocks at regional and global scales. This is essential for effective carbon management, which involves strategies like emission reduction and enhanced carbon sequestration through forest restoration and conservation. However, reliable sample-based estimations of forest carbon stocks require accurate allometric equations, which are lacking for the rainforests of the Atlantic Forest Domain (AFD). In this study, we fitted biomass equations for the three main AFD forest types and accurately estimated the amount of carbon stored in their above-ground biomass (AGB) in Rio de Janeiro state, Brazil. Using non-destructive methods, we measured the total wood volume and wood density of 172 trees from the most abundant species in the main remnants of rainforest, semideciduous forest, and restinga forest in the state. The biomass and carbon stocks were estimated with tree-level data from 185 plots obtained in the National Forest Inventory conducted in Rio de Janeiro. Our locally developed allometric equations estimated the state’s biomass stocks at 70.8 ± 5.4 Mg ha−1 and carbon stocks at 35.4 ± 2.7 Mg ha−1. Notably, our estimates were more accurate than those obtained using a widely applied pantropical allometric equation from the literature, which tended to overestimate biomass and carbon stocks. These findings can be used for establishing a baseline for monitoring carbon stocks in the Atlantic Forest, especially in the context of the growing voluntary carbon market, which demands more consistent and accurate carbon stock estimations. Full article
(This article belongs to the Section Forest Ecology and Management)
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Figure 1

Figure 1
<p>Geographic location of the sites where data were collected. Triangles represent sites where aboveground biomass data were collected: Rainforest (RAF; green triangles), Semideciduous Forest (SF; yellow triangles), and Restinga Forest (RF; blue triangles), in the Atlantic Forest of Rio de Janeiro state (Brazil). Circles represent sampling units of the National Forest Inventory conducted in Rio de Janeiro (NFI-RJ; red dots). Data from the NFI-RJ were used to plan the biomass sampling design and estimate the total above-ground biomass stocks of the state’s forest cover.</p>
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<p>Conceptual diagram summarizing (<b>a</b>) data collection, (<b>b</b>) model selection and validation, and (<b>c</b>) biomass estimation for the entire Rio de Janeiro state. DBH = diameter at breast height, MSH = mid-stem height, AGB = predicted aboveground biomass (Mg), Ht = total tree height (m), RAF = Rainforest, SF = Semideciduous Forest, RF = Restinga Forest.</p>
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<p>Equivalence test (regression-based TOST using Bootstrap) for comparing means or similarities between field-measured biomass and the estimates produced by the forest-specific, local-generic, and pantropical equations. The analyses were based on biomass samples taken from 172 trees measured on site: (<b>a</b>) Distribution of AGB values across the different equations for measured trees on site. There were no significant differences (<span class="html-italic">p</span>-value &gt; 0.01) between the observed values (measured on site) and those obtained using either local-generic equations or the forest-specific, though there was a significant difference when compared to values based on pantropical equation. The letters “a” and “b” represent the statistically significant difference between the treatments. (<b>b</b>) Relationship between AGB estimated based on specific equation per forest types and measured AGB. (<b>c</b>) Relationship between AGB estimated from the generic equation and measured AGB. (<b>d</b>) Relationship between AGB estimated from the pantropical equation and measured AGB. (<b>e</b>) Relationship between AGB estimated from pantropical equation and AGB estimated based on specific equation per forest types. (<b>f</b>) Relationship between AGB estimated from pantropical equation and AGB estimated from a generic equation for all forest types. (<b>g</b>) Relationship between AGB estimated from generic equation for all forest types and AGB estimated based on specific equation per forest types. RMSEs are expressed as the percentage of mean square value (PRMSE).</p>
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<p>Equivalence test (regression-based TOST using Bootstrap) to compare means or similarities between the estimates generated by the forest-specific, local-generic, and pantropical equations. The analyses were based on field-measured biomass samples from 185 plots. (<b>a</b>) Distribution of AGB values across the different equations: Generic equation for all forest types, pantropical equation, and specific allometric equation for all forest types. Both AGBs estimated based on generic and specific per-forest types were significantly different for the pantropical equation. The letters “a” and “b” represent the statistically significant difference between the treatments. (<b>b</b>) Relationship between AGB estimated from the pantropical equation and AGB estimates based on specific equation per forest type. (<b>c</b>) Relationship between AGB estimated from the pantropical equation and AGB estimates from the generic equation. (<b>d</b>) AGB estimates from the generic equation and AGB estimates based on the specific equation per forest type. RMSEs are expressed as the percentage of mean square value (PRMSE).</p>
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