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18 pages, 3420 KiB  
Article
The Effect of Karst Carbonate Rock Dissolution on Nitrogen Metabolism Microorganisms and Their Functions in Paddy Soils
by Fengling Liu, Hu Wang, Bing Wang, Xu Mao, Jianbo Cheng, Chengwu Fan, Tengbing He and Tianling Fu
Land 2025, 14(3), 553; https://doi.org/10.3390/land14030553 - 6 Mar 2025
Abstract
Carbonate rock dissolution (CRD) in karst areas generates abundant ions, which contribute significantly to nitrogen (N) transformation in paddy ecosystems. However, little is known about the microbial mechanisms by which CRD ions (Ca2+, Mg2+, HCO3/CO3 [...] Read more.
Carbonate rock dissolution (CRD) in karst areas generates abundant ions, which contribute significantly to nitrogen (N) transformation in paddy ecosystems. However, little is known about the microbial mechanisms by which CRD ions (Ca2+, Mg2+, HCO3/CO32−, and OH-) regulate N balance. In this experiment, rice pot studies were conducted using karst soil (S1), karst soil with removed carbonate minerals (S2), non-karst soil (S3), and non-karst soil with additional carbonate minerals (S4). The effects of CRD on N-metabolizing microorganisms and functional genes in N metabolism were investigated using metagenomic sequencing technology. Six N metabolism pathways, including N fixation, nitrification, denitrification, dissimilatory nitrate reduction to ammonia (DNRA), assimilatory nitrate reduction to ammonia (ANRA), and complete nitrification (comammox) were revealed. Compared with S3, the relative abundance of the denitrification module (M00529) in S1 clearly increased by 1.52%. Additionally, compared to S3, the relative abundance of the complete nitrification (comammox) module (M00804) in S4 decreased by 0.66%. Proteobacteria and Anaeromyxobacter were significant contributors to variations in N metabolism. Key factors that influenced variations in N metabolism included Ca2+, Mg2+, and pH. This study explored the effects of CRD on N-metabolizing microorganisms and functions, which was of great significance to the N cycle in karst paddy ecosystems. Full article
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<p>Physical and chemical properties of paddy soils. Different lowercase letters represent significant differences between different groups (<span class="html-italic">p</span> &lt; 0.05). (ECa<sup>2+</sup> represents exchangeable Ca<sup>2+</sup>, EMg<sup>2+</sup> represents exchangeable Mg<sup>2+</sup>, TP represents total phosphorus, TN represents total nitrogen, NO<sub>3</sub><sup>−</sup>-N represents nitrate nitrogen, and NH<sub>4</sub><sup>+</sup>-N represents ammonia nitrogen).</p>
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<p>Taxonomy of N metabolism microorganisms in paddy soils. Relative abundance of microorganisms at the phylum level (<b>A</b>). Similarities and differences in the top 15 species-level microorganisms (<b>B</b>).</p>
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<p>Differences in N metabolism microorganisms in various paddy soils. PCoA analysis of microbial community structures (<b>A</b>). One-way ANOVA multi-group comparison of microbial species abundance (<b>B</b>). Fdr was used for multiple test correction of <span class="html-italic">p</span>-values. “*”, “**”, and “***” respectively represent 0.01 &lt; <span class="html-italic">p</span> ≤ 0.05, 0.001 &lt; <span class="html-italic">p</span> ≤ 0.01, and <span class="html-italic">p</span> ≤ 0.001.</p>
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<p>Microbial N cycle in paddy soils. Main key enzymes and related pathways of N metabolism (<b>A</b>). Relative abundance of N metabolism modules (<b>B</b>). Different lowercase letters represent significant differences between different groups (<span class="html-italic">p</span> &lt; 0.05).</p>
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<p>Microbial N cycle in paddy soils. Main key enzymes and related pathways of N metabolism (<b>A</b>). Relative abundance of N metabolism modules (<b>B</b>). Different lowercase letters represent significant differences between different groups (<span class="html-italic">p</span> &lt; 0.05).</p>
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<p>Relative abundance of N metabolism functional genes in paddy soils.</p>
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<p>The correlation between soil microorganisms and N metabolism function in different soils. Correlation network analysis between microorganisms and N metabolism functions (<b>A</b>). Contribution correlation between species and N metabolism functions (<b>B</b>).</p>
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<p>Pearson correlation heatmap between soil environmental factors and N metabolism functions. “*”, “**”, “***” and “****” respectively represent 0.01 &lt; <span class="html-italic">p</span> ≤ 0.05, 0.001&lt; <span class="html-italic">p</span> ≤ 0.01, <span class="html-italic">p</span> ≤ 0.001 and <span class="html-italic">p</span> ≤ 0.0001.</p>
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21 pages, 8129 KiB  
Article
Plants Drive Microbial Biomass and Composition but Not Diversity to Promote Ecosystem Multifunctionality in Karst Vegetation Restoration
by Yunlong Sun, Shu Zhang, Yueming Liang, Xuan Yu and Fujing Pan
Microorganisms 2025, 13(3), 590; https://doi.org/10.3390/microorganisms13030590 - 4 Mar 2025
Viewed by 81
Abstract
Natural restoration has emerged as a prominent approach in recent decades for the rehabilitation of degraded ecosystems globally. However, the specific changes and underlying mechanisms by natural restoration that influence the multifunctionality of karst ecosystems remain poorly understood. In this study, soil, litter, [...] Read more.
Natural restoration has emerged as a prominent approach in recent decades for the rehabilitation of degraded ecosystems globally. However, the specific changes and underlying mechanisms by natural restoration that influence the multifunctionality of karst ecosystems remain poorly understood. In this study, soil, litter, and fine root samples were collected from four chronosequence stages of vegetation restoration—grassland (G), shrubland (SH), shrub-tree land (ST), and forest (F)—within a karst ecosystem in Southwestern China. The aim was to evaluate the impacts of vegetation restoration on ecosystem multifunctionality using an averaging approach. The results demonstrated that the indices of C-cycling functionality, N-cycling functionality, P-cycling functionality, and total ecosystem multifunctionality increased as vegetation restoration progressed, along with plant diversity. The structure of plant, bacterial, and fungal communities varied across different stages of vegetation restoration, exhibiting the highest microbial diversity indices in the SH stage. Additionally, the tightness and complexity of co-occurrence networks of bacteria and fungi increased with advancing vegetation restoration, and higher positive links were observed in fungi than bacteria. The four functional indices were significantly and positively correlated with increasing plant diversity, fine root and litter nutrient contents, fine root biomass, microbial biomass, fungal community, enzyme activities, and soil nutrient contents but not with bacterial and fungal diversities. Furthermore, Random Forest model results revealed that plants exerted a significantly greater influence on ecosystem multifunctionality compared to other factors. It is plausible that plants influence soil microbial biomass, fungal community and co-occurrence networks, enzyme activities, and nutrient levels through the input of root and litter nutrients rather than by altering microbial diversity to enhance karst ecosystem multifunctionality. Therefore, initiatives to increase plant diversity are beneficial for sustainable ecological restoration management in the karst regions of Southwestern China. Full article
(This article belongs to the Special Issue Soil Microbial Carbon/Nitrogen/Phosphorus Cycling)
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<p>Map of the four stages of vegetation restoration in Guilin, Southwestern China.</p>
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<p>Soil, fine root, litter nutrient and enzyme activities across advancing vegetation restorations. C-cycling parameters: Root-C (<b>a</b>), C contents of fine root; Litter-C (<b>b</b>), C contents of litter; MBC (<b>c</b>), microbial biomass C; SOC (<b>d</b>), soil organic carbon; and βG (<b>e</b>), β-Glucosidase activity. N-cycling parameters: Root-N (<b>f</b>), N contents of fine root; Litter-N (<b>g</b>), N contents of litter; MBN (<b>h</b>), microbial biomass N; TN (<b>i</b>), soil total N; NH<sub>4</sub><sup>+</sup>-N (<b>j</b>), ammonium N; NO<sub>3</sub><sup>−</sup>-N (<b>p</b>), nitrate N; NAG (<b>q</b>), β-1,4-N-acetylglucosaminidase activity; and LAP (<b>r</b>), leucine aminopeptidase activity. P-cycling parameters: Root-P (<b>k</b>), P contents of fine root; Litter-P (<b>l</b>), P contents of litter; MBP (<b>m</b>), microbial biomass P; TP (<b>n</b>), soil total P; AP (<b>o</b>), soil available P; ACP (<b>s</b>), acid phosphatase; ALP (<b>t</b>), alkaline phosphatase; and grassland (G), shrubland (SH), shrub-tree land (ST), and forest (F). Different letters mean significant differences (<span class="html-italic">p</span> &lt; 0.05).</p>
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<p>The patterns of C-cycling functional (<b>a</b>), N-cycling functional (<b>b</b>), P-cycling functional (<b>c</b>), and total multifunctionality (<b>d</b>) indices across advancing vegetation restorations. Different letters mean significant differences (<span class="html-italic">p</span> &lt; 0.05).</p>
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<p>The diversity indices of plants, bacteria, and fungi across advancing vegetation restorations. Plant Shannon (<b>a</b>), the Shannon–Wiener index of plants; Plant Simpson (<b>b</b>), the Simpson index of plants; Plant Pielou (<b>c</b>), the Pielou index of plants; bacterial Shannon (<b>d</b>), the Shannon–Wiener index of bacteria; bacterial Simpson (<b>e</b>), the Simpson index of bacteria; bacterial OTUs (<b>f</b>); bacterial Chao1 (<b>g</b>); fungal Shannon (<b>h</b>), the Shannon–Wiener index of fungi; and fungal Simpson (<b>i</b>), the Simpson index of fungi; fungi OTUs (<b>j</b>); fungi Chao1 (<b>k</b>). Different letters mean significant differences (<span class="html-italic">p</span> &lt; 0.05).</p>
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<p>Community structures of plants, bacteria, and fungi across advancing vegetation restorations.</p>
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<p>Relative abundances at genus level of plants (<b>a</b>), bacteria (<b>b</b>), and fungi (<b>c</b>) across advancing vegetation restorations.</p>
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<p>Co-occurrence network models of bacteria (<b>a</b>) and fungi (<b>b</b>) at order level across advancing vegetation restorations. The red line indicates positive relation, and the green line indicates negative relation.</p>
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<p>Ecosystem multifunctionality indices related to plant, microbial, and soil factors. C-cycling, C-cycling functional index; N-cycling, N-cycling functional index; P-cycling, P-cycling functional index; Total, total multifunctionality index. Plant Shannon, Shannon–Wiener index of plants; Plant Simpson, Simpson index of plants; Plant Pielou, Pielou index of plants; bacterial Shannon, Shannon–Wiener index of bacteria; bacterial Simpson, Simpson index of bacteria; fungal Shannon, Shannon–Wiener index of fungi; and fungal Simpson, Simpson index of fungi. Root-C, C contents of fine root; Litter-C, C contents of litter; MBC, microbial biomass C; SOC, soil organic carbon; and βG, β-Glucosidase activity. Root-N, N contents of fine root; Litter-N, N contents of litter; MBN, microbial biomass N; TN, soil total N; NH<sub>4</sub><sup>+</sup>-N, ammonium N; NO<sub>3</sub><sup>−</sup>-N, nitrate N; NAG, β-1,4-N-acetylglucosaminidase activity; and LAP, leucine aminopeptidase activity. Root-P, P contents of fine root; Litter-P, P contents of litter; MBP, microbial biomass P; TP, soil total P; AP, soil available P; ACP, acid phosphatase; and ALP, alkaline phosphatase. ** <span class="html-italic">p</span> &lt; 0.01; * <span class="html-italic">p</span> &lt; 0.05.</p>
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<p>The changes in C-cycling functional (<b>a</b>), N-cycling functional (<b>b</b>), P-cycling functional (<b>c</b>), and total multifunctionality (<b>d</b>) indices are importantly ranked by plant, microbial, and soil factors. MSE is the mean square error, and the percentage of variations in MSE is used to estimate the relative importance of the measured variables. Green indicates the significant explanatory variables, while yellow denotes the non-significant explanatory variables. ** <span class="html-italic">p</span> &lt; 0.01; * <span class="html-italic">p</span> &lt; 0.05.</p>
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<p>Structural equation model results show that the influence path on soil C-cycling functional (<b>a</b>), N-cycling functional (<b>b</b>), P-cycling functional (<b>c</b>), and total multifunctional (<b>d</b>) indices. The parameters of these models: (<b>a</b>) X<sub>2</sub> = 1.741, degrees of freedom = 3, n = 19, CFI = 0.977, AGFI = 0.724, <span class="html-italic">p</span> = 0.628, RMSEA = 0.000; (<b>b</b>) X<sub>2</sub> = 1.741, degrees of freedom = 3, n = 19, CFI = 0.977, AGFI = 0.724, <span class="html-italic">p</span> = 0.628, RMSEA = 0.000; (<b>c</b>) X<sub>2</sub> = 1.741, degrees of freedom = 3, n = 19, CFI = 0.977, AGFI = 0.724, <span class="html-italic">p</span> = 0.628, RMSEA = 0.000; and (<b>d</b>) X<sub>2</sub> = 1.798, degrees of freedom = 4, n = 19, CFI = 0.976, AGFI = 0.786, <span class="html-italic">p</span> = 0.773, RMSEA = 0.000. Blue represents negative impact, red represents positive impact. ---, <span class="html-italic">p</span> ≥ 0.05, * <span class="html-italic">p</span> &lt; 0.05, ** <span class="html-italic">p</span> &lt; 0.01, *** <span class="html-italic">p</span> &lt; 0.001.</p>
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17 pages, 8809 KiB  
Article
Soil Respiration Characteristics and Karst Carbon Sink Potential in Woodlands and Grasslands
by Ning Zhang, Qiong Xiao, Yongli Guo, Fajia Chen, Pingan Sun, Ying Miao and Cheng Zhang
Forests 2025, 16(3), 424; https://doi.org/10.3390/f16030424 - 26 Feb 2025
Viewed by 178
Abstract
The weathering of carbonate rocks consumes significant amounts of soil CO2, contributing to both direct source reduction and to the enhancement of carbon sinks. This process holds substantial potential as a carbon sink, making it a critical strategy for achieving carbon [...] Read more.
The weathering of carbonate rocks consumes significant amounts of soil CO2, contributing to both direct source reduction and to the enhancement of carbon sinks. This process holds substantial potential as a carbon sink, making it a critical strategy for achieving carbon neutrality and mitigating climate change. However, the control mechanisms for the reverse assessment of karst carbon sinks, with soil CO2 as the core at the input end of karstification, are unclear. By comparing soil respiration and its δ13C values between karst and non-karst regions, we analyzed the impact of karstification on soil respiration. In this study, we examined the karst grassland (KG), woodland (KW), and non-karst woodland (NKW) in the karst region with identical climate conditions as the research subject, analyzing the differences in soil respiration rate (RS), flux (SRF), and isotope δ13C under different land-use types, and comparing them with the non-karst region to reveal the carbon sink potential of karstification in reducing carbon emissions. The results showed that after the land-use change from KG to KW in the karst region, the annual mean values of the RS and SRF increased by 55.50% and 20.94%, respectively. Additionally, the annual mean values of the soil respiration contribution to carbonate weathering in KG were approximately 8.2% higher than those in KW. In contrast, the annual mean values of RS and SRF in KW were 25.14% and 41.80% lower than those in NKW, respectively. Furthermore, the soil respiration participation in carbonate weathering in KW was about 8.9% of that in NKW. Land use change can significantly influence karst carbon sinks, with the KG exhibiting the highest carbon sink capacity. Karst soils play a crucial role in reducing atmospheric CO2 levels and facilitating regional carbon neutralization. Therefore, the karst systems play a pivotal role in mitigating the “land use change term” (source term, ELUC) in the global carbon balance. Full article
(This article belongs to the Topic Karst Environment and Global Change)
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<p>Land use of study area and location of study sites.</p>
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<p>Changes in environmental factors and background levels of atmospheric CO<sub>2</sub> concentration. (<b>a</b>) Monthly variation in temperature. (<b>b</b>) Monthly variation in precipitation (<b>c</b>) Monthly variation in atmospheric CO<sub>2</sub> at KG. (<b>d</b>) Monthly variation in atmospheric CO<sub>2</sub> at KW. (<b>e</b>) Monthly variation in atmospheric CO<sub>2</sub> at NKW.</p>
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<p>Monthly Variation Trends and comparisons of RS in KG, KW, and NKW (<b>a</b>); Violin Plots of RS in KG, KW, and NKW During the Dry and Rainy Seasons (<b>b</b>).</p>
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<p>Monthly Trends of SRS in KG, KW, and NKW (<b>a</b>); Violin Plots of SFR for Different Land Use Types During the Dry and Rainy Seasons (<b>b</b>); Violin Plots of SFR for Karst and Non-Karst Areas During the Dry and Rainy Seasons (<b>c</b>).</p>
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<p>Temporal changes in the δ<sup>13</sup>C of headspace carbon dioxide within chambers during the 0–30 min period in KG, KW, and NKW. (<b>a</b>) Changes in δ<sup>13</sup>C for KG. (<b>b</b>) Changes in δ<sup>13</sup>C for KW. (<b>c</b>) Changes in δ<sup>13</sup>C for NKW.</p>
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<p>Trends and comparisons of δ<sup>13</sup>C values of soil respiration in KG, KW, and NKW.</p>
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<p>Comparison of weathering ratios of KG to KW and KW to NKW participating carbonates.</p>
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15 pages, 3717 KiB  
Article
Impact of Karst Rocky Desertification on N-Fixing Tree Species Root System and Bacteria
by Shuzhong Yu, Chunhui Guo and Xianyu Yao
Forests 2025, 16(3), 425; https://doi.org/10.3390/f16030425 - 26 Feb 2025
Viewed by 148
Abstract
The study aimed to investigate the effect of soil textural or soil mineral fraction substrates (loam and gravel) from karst desertification areas on the rhizospheric and root-associated bacterial community structure of Dalbergia odorifera (an N-fixing tree), using high-throughput sequencing techniques, based on treatment [...] Read more.
The study aimed to investigate the effect of soil textural or soil mineral fraction substrates (loam and gravel) from karst desertification areas on the rhizospheric and root-associated bacterial community structure of Dalbergia odorifera (an N-fixing tree), using high-throughput sequencing techniques, based on treatment methods of whole-root and two-chambered split-root systems. Further, this study determined the relative importance of the plant and substrate properties on the rhizospheric, non-rhizospheric and endospheric bacteria composition. The type of substrate exerts a significant influence on both rhizospheric and non-rhizospheric bacterial communities, whereas endophytic communities within the root system are predominantly determined by plant species rather than substrate type. The analysis revealed that endospheric bacterial diversity was considerably lower than that of rhizospheric and non-rhizospheric communities. Cluster analysis indicated that endospheric bacterial samples formed a distinct cluster, while rhizospheric and non-rhizospheric bacteria in the soil substrate grouped into one branch, and those in the gravel substrate formed another branch. In comparison to the gravel treatments, a reduced bacterial abundance was observed in the rhizosphere and non-rhizosphere of nitrogen-fixing plants in soil, potentially due to the interplay of lower nutrient availability and increased porosity in gravel treatments. Proteobacteria, which are involved in the nitrogen cycle, exhibited the highest abundance. In contrast, Acidobacteria, Firmicutes and other bacterial phyla involved in nutrient cycling demonstrated higher abundance, with their presence being more pronounced in extreme environments, such as gravel treatments, compared to soil substrates. These results suggest that nitrogen-fixing plants can respond to extreme environments by increasing bacterial abundance. The findings of this study provide a theoretical basis for the use of D. odorifera for ecosystem recovery and vegetation restoration. Full article
(This article belongs to the Section Forest Biodiversity)
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<p>Schematic representation of four treatments and three root zones, including endosphere, rhizosphere and non-rhizospheric zones; S: soil; R: rock; D: division.</p>
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<p>Horizontal histogram of the root-associated bacterial of <span class="html-italic">D. odorifera</span> at the genus level. Sample abbreviations in the figure: Re, grave-endosphere; Rr, gravel-rhizosphere; Rn, gravel-non-rhizosphere; SE, soil-endosphere; Sr: soil-rhizosphere; Sn: soil-non-rhizosphere (D, division; R, root; S, soil; e, endosphere; r, rhizosphere; n, non-rhizosphere).</p>
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<p>Phylogenetic analysis of the rhizospheric bacteria of <span class="html-italic">D. odorifera</span> (top 100). Sample Abbreviations in the figure: Re, gravel-endosphere; Rr, gravel-rhizosphere; Rn, gravel-non-rhizosphere; SE, soil-endosphere; Sr: soil-rhizosphere; Sn: soil-non-rhizosphere (D, division; R, root; S, soil; e, endosphere; r, rhizosphere; n, non-rhizosphere).</p>
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<p>Principal Component Analysis (PCA) analysis of root-associated bacteria of <span class="html-italic">D. odorifera</span>. Sample abbreviations in the figure: Re, gravel-endosphere; Rr, gravel-rhizosphere; Rn, gravel-non-rhizosphere; SE, soil-endosphere; Sr: soil-rhizosphere; Sn: soil-non-rhizosphere (D, division; R, root; S, soil; e, endosphere; r, rhizosphere; n, non-rhizosphere).</p>
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<p>Cluster analysis (phylum level) of root-associated bacteria of <span class="html-italic">D. odorifera</span>. Sample abbreviations in the figure: Re, gravel-endosphere; Rr, gravel-rhizosphere; Rn, gravel-non-rhizosphere; SE, soil-endosphere; Sr: soil-rhizosphere; Sn: soil-non-rhizosphere (D, division; R, root; S, soil; e, endosphere; r, rhizosphere; n, non-rhizosphere).</p>
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<p>RDA of the rhizospheric bacteria of <span class="html-italic">D. odorifera</span>. (<b>a</b>): phylum level, (<b>b</b>): genus level. O: Soil organic matter; C: Soil carbon; N: Nitrogen; P: Soil available phosphorus; K: Soil available kalium; W: soil water content.</p>
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19 pages, 3642 KiB  
Article
Nitrogen-Fixing Plants Enhance Soil Phosphorus Availability by Promoting Transformations Among Phosphorus Fractions in a Subtropical Karst Forest
by Yu Zhu, Zhizhuo Gao, Lijun Liu, Jie Li, Tongbin Zhu, Jiangming Ma, Thomas H. DeLuca and Min Duan
Forests 2025, 16(2), 360; https://doi.org/10.3390/f16020360 - 17 Feb 2025
Viewed by 341
Abstract
Nitrogen (N)-fixing plants are commonly employed in the restoration of degraded terrestrial ecosystems due to their ability to increase soil N capital and boost ecosystem productivity. Given the close coupling between N and phosphorus (P) in soil, the effects of N-fixing plants on [...] Read more.
Nitrogen (N)-fixing plants are commonly employed in the restoration of degraded terrestrial ecosystems due to their ability to increase soil N capital and boost ecosystem productivity. Given the close coupling between N and phosphorus (P) in soil, the effects of N-fixing plants on soil P fractions and availability in karst forests remain largely unexplored. Herein, we compared soil P pools, fractions, and availability in the rhizosphere and non-rhizosphere soils of N-fixing and non-N-fixing plants, and explored associated drivers, such as soil, microbial, and plant properties, in a subtropical karst forest. The results showed that the N-fixing plants increased total P, inorganic P, and available P in both the rhizosphere and non-rhizosphere soils. The nitrogen-fixing plants increased soil labile P (LP) and non-labile P (NLP), but decreased moderately labile P (MLP), particularly in the rhizosphere soils, due to transformations among different soil P fractions. Soil P fractions were primarily influenced by soil inorganic P, root and leaf N, and microbial biomass N in the N-fixing plant treatment, whereas soil inorganic P, dissolved organic carbon (DOC), and dissolved organic N (DON) were the key factors in the non-N-fixing plant treatment. Consequently, soil properties, microbial attributes, plant nutrients, and soil P fractions collectively exerted both direct and indirect effects to increase soil P availability in the N-fixing plant treatment. In contrast, soil P fractions directly and soil properties indirectly influenced soil P availability in the non-N-fixing plant treatment. Our results revealed the unique role of N-fixing plants in driving soil P availability in subtropical karst forests. These findings are essential for developing effective strategies for P nutrient management and guiding the selection of appropriate plant species for vegetation restoration in karst regions. Full article
(This article belongs to the Special Issue Climate Variation & Carbon and Nitrogen Cycling in Forests)
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<p>Soil total P (<b>a</b>), organic P (<b>b</b>), inorganic P (<b>c</b>), and available P (<b>d</b>) contents in rhizosphere and non-rhizosphere soils of N-fixing plants (n = 8) and non-N-fixing plants (n = 5) in a subtropical karst forest in China. Different lowercase and uppercase letters indicate significant differences between rhizosphere and non-rhizosphere soils for N-fixing and non-N-fixing plants, respectively (<span class="html-italic">p</span> &lt; 0.05), and * indicates significant differences between N-fixing and non-N-fixing plants for rhizosphere soil or non-rhizosphere soil at <span class="html-italic">p</span> &lt; 0.05.</p>
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<p>Soil P fractions in rhizosphere (<b>a</b>) and non-rhizosphere (<b>b</b>) soils of N-fixing plants (n = 8) and non-N-fixing plants (n = 5) in a subtropical karst forest in China. Asterisks indicate significant differences between N-fixing and non-N-fixing plants for each soil P fraction. *, **, and *** indicate significance levels at <span class="html-italic">p</span> &lt; 0.05, <span class="html-italic">p</span> &lt; 0.01, and <span class="html-italic">p</span> &lt; 0.001, respectively.</p>
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<p>Soil labile P (<b>a</b>), moderately labile P (<b>b</b>), and non-labile P (<b>c</b>) contents in rhizosphere and non-rhizosphere soils of N-fixing plants (n = 8) and non-N-fixing plants (n = 5) in a subtropical karst forest in China. Different lowercase and uppercase letters indicate significant differences between rhizosphere and non-rhizosphere soils for N-fixing and non-N-fixing plants, respectively (<span class="html-italic">p</span> &lt; 0.05), and * indicates significant differences between N-fixing and non-N-fixing plants for rhizosphere soil or non-rhizosphere soil at <span class="html-italic">p</span> &lt; 0.05.</p>
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<p>Soil microbial biomass carbon (<b>a</b>), microbial biomass nitrogen (<b>b</b>), and microbial biomass phosphorus (<b>c</b>) contents and alkaline phosphatase (<b>d</b>) activity in rhizosphere and non-rhizosphere soils of N-fixing plants (n = 8) and non-N-fixing plants (n = 5) in a subtropical karst forest in China. Different lowercase and uppercase letters indicate significant differences between rhizosphere and non-rhizosphere soils for N-fixing and non-N-fixing plants, respectively (<span class="html-italic">p</span> &lt; 0.05), and * indicates significant differences between N-fixing and non-N-fixing plants for rhizosphere soil or non-rhizosphere soil at <span class="html-italic">p</span> &lt; 0.05.</p>
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<p>Carbon (<b>a</b>), nitrogen (<b>b</b>), and phosphorus (c) contents in the leaves and roots of N-fixing plants (n = 8) and non-N-fixing plants (n = 5) in a subtropical karst forest in China. * indicates significant differences between N-fixing and non-N-fixing plants for each nutrient at <span class="html-italic">p</span> &lt; 0.05.</p>
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<p>Variation partitioning analysis (VPA) illustrating the unique contributions of soil properties, microbial properties, and plant nutrients to soil P fractions in N-fixing plants (<b>a</b>) and non-N-fixing plants (<b>b</b>) in a subtropical karst forest in China, and redundancy analysis (RDA) of soil P fractions in N-fixing plants (<b>c</b>) and non-N-fixing plants (<b>d</b>). The percentages shown in the VPA represent the proportion of variance in soil P fractions explained by each factor (or combination of factors), with the remaining variance attributed to the residual (unexplained) component. The red and blue lines in the RDA represent explanatory and response variables, respectively. LP, labile P; MLP, moderately labile P; NLP, non-labile P; IP, inorganic P; DOC, dissolved organic carbon; DN, dissolved nitrogen; MBN, microbial biomass nitrogen.</p>
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<p>Structural equation models (SEMs) revealing the multivariate effects of soil properties, microbial properties, plant nutrients, and soil P fractions on soil available P in N-fixing plants (<b>a</b>) and non-N-fixing plants (<b>b</b>) in a subtropical karst forest in China. Standardized total effects of variables from the SEMs are depicted for N-fixing plants (<b>c</b>) and non-N-fixing plants (<b>d</b>). The solid red and blue arrows indicate positive and negative pathways, respectively, while the dashed grey arrows represent pathways with no significant effect. The numbers next to the arrows are the standardized path coefficients. Asterisks (*, **, ***) denote significance levels at <span class="html-italic">p</span> &lt; 0.05, <span class="html-italic">p</span> &lt; 0.01, and <span class="html-italic">p</span> &lt; 0.001, respectively. The R<sup>2</sup> values displayed below the response variables show the proportion of variation explained by the relationships with other variables.</p>
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20 pages, 8523 KiB  
Article
Ecological Health Assessment of Karst Plateau Wetlands Based on Landscape Pattern Analysis
by Linjiang Yin, Weiquan Zhao, Yanmei Liao, Wei Li, Zulun Zhao and Liang Huang
Water 2025, 17(4), 537; https://doi.org/10.3390/w17040537 - 13 Feb 2025
Viewed by 379
Abstract
This study analyzed the changes in landscape patterns and the ecological health status of karst plateau wetlands, providing valuable insights into their conservation. Using land cover data from 1996 to 2021, DEM, and Landsat series satellite imagery, this study employed landscape ecology methods [...] Read more.
This study analyzed the changes in landscape patterns and the ecological health status of karst plateau wetlands, providing valuable insights into their conservation. Using land cover data from 1996 to 2021, DEM, and Landsat series satellite imagery, this study employed landscape ecology methods and the pressure–state–response (PSR) model framework. A regional landscape grid was constructed, and 13 indicators were selected to establish an ecological health evaluation system for karst plateau wetlands. This allowed us to explore the spatiotemporal change characteristics of the landscape pattern and the ecological health of karst plateau wetlands. The results showed that over a 25-year period, farmland, grassland, and construction land areas have increased, whereas forested land areas have decreased. Water bodies remained relatively stable but showed a trend of transitioning into grassland. Unused land showed no significant change. Landscape analysis indicated that grasslands experience the highest rate of fragmentation, complex shapes, and greater heterogeneity, whereas water bodies have the lowest fragmentation, more regular shapes, and lower heterogeneity. Other landscape types exhibited moderate characteristics. Overall, the landscape of the study area exhibited high fragmentation, specific patch aggregation, moderate patch density, and low diversity. A comprehensive ecological health evaluation revealed that the wetland health value remained at an “unhealthy” level from 1996 to 2021. Although there was a brief improvement in 2010, effective long-term recovery was not achieved. Spatially, the proportion of “diseased” areas peaked in 2006, and most grid zones remained in an “unhealthy” state over the years, with none reaching the “healthy” standard. These findings highlight the severe challenges faced by the wetland ecosystem. Full article
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<p>Schematic diagram of the study area.</p>
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<p>Temporal Sankey diagram of landscape-type transitions.</p>
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<p>Dominance indices of landscape patterns at the type level.</p>
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<p>Fragmentation index of landscape patterns at the type level.</p>
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<p>Distribution of landscape health diagnosis in various grid areas of wetlands.</p>
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31 pages, 5095 KiB  
Article
Stoichiometric Characteristics and Influencing Factors of Different Components of Karst Forest Plants at the Microtopography and Microhabitat Scale in Maolan National Nature Reserve, Guizhou, China
by Peng Wu, Hua Zhou, Wenjun Zhao, Guangneng Yang, Yingchun Cui, Yiju Hou, Chengjiang Tan, Ting Zhou and Fangjun Ding
Forests 2025, 16(2), 317; https://doi.org/10.3390/f16020317 - 11 Feb 2025
Viewed by 449
Abstract
The main dominant tree species of karst forest at the microtopography and the microhabitat scale were taken as the research object in this study, and the stoichiometric characteristics of different components and their influencing factors were analyzed in order to reveal the survival [...] Read more.
The main dominant tree species of karst forest at the microtopography and the microhabitat scale were taken as the research object in this study, and the stoichiometric characteristics of different components and their influencing factors were analyzed in order to reveal the survival strategy of karst forest plants in harsh habitats and their mechanism of adaptation to complex terrain. The results showed that the nutrient distribution among different components of the plant was closely related to its organizational structure and functional attributes. The microtopography had a significant effect on plant nutrient accumulation. However, the effect of the microhabitat on plant stoichiometric characteristics was relatively small. Different ecological factors had various regulatory effects on the stoichiometric characteristics of plant components, among which the specific leaf area (SLA) was the most critical biological factor affecting the stoichiometric characteristics of new leaves. Leaf dry matter content (LDMC) had the greatest effect on mature leaves, litter, and branches, and the trunks were mainly affected by plant species. There are synergistic tradeoffs between different plant components, and the interaction between each element mainly shows antagonistic and synergistic effects. Plants adapt to the changes in the karst microtopography and microhabitat by adjusting resource allocation and structural and functional traits. In the upslope, shady slope, and semi-shady slope regions and slopes above 25°, the plants adopted a conservative strategy. In depressions, on sunny slopes, and on flat land, as well as on slopes below 25°, the resource acquisition strategy was adopted. This is the result of the interaction of biological and abiotic factors, which reflects the resource acquisition and nutrient allocation strategies of plants in different habitats, and it is also an mechanism of adaptation to a complex and changeable environment. Full article
(This article belongs to the Special Issue Physiological Mechanisms of Plant Responses to Environmental Stress)
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<p>Diagram of plant sample locations. Numbers 1–51 represent each plant sample.</p>
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<p>The contents of C (<b>a</b>), N (<b>b</b>), P (<b>c</b>), K (<b>d</b>), Ca (<b>e</b>), and Mg (<b>f</b>) of various components of karst forest plants in different microhabitats. Different lowercase letters indicate a significant difference between different microhabitats among the same plant component (<span class="html-italic">p</span> &lt; 0.05). Different capital letters indicate significant differences among different components of plants in the same microhabitat (<span class="html-italic">p</span> &lt; 0.05). The absence of any uppercase or lowercase letters indicates that there is no significant difference between different plant components or different microhabitats (<span class="html-italic">p</span> &gt; 0.05).</p>
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<p>The contents of C (<b>a</b>), N (<b>b</b>), P (<b>c</b>), K (<b>d</b>), Ca (<b>e</b>), and Mg (<b>f</b>) of various components of karst forest plants at different slope positions. Different lowercase letters indicate a significant difference between different slope positions of the same plant component (<span class="html-italic">p</span> &lt; 0.05). Different capital letters indicate a significant difference among different components at the same slope position (<span class="html-italic">p</span> &lt; 0.05). The absence of any uppercase or lowercase letters indicates that there is no significant difference between different plant components or different slope positions (<span class="html-italic">p</span> &gt; 0.05).</p>
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<p>The contents of C (<b>a</b>), N (<b>b</b>), P (<b>c</b>), K (<b>d</b>), Ca (<b>e</b>), and Mg (<b>f</b>) of various components of karst forest plants on different slope aspects. Different lowercase letters indicate a significant difference between different slope aspects of the same plant component (<span class="html-italic">p</span> &lt; 0.05). Different capital letters indicate a significant difference among different components of the same slope aspect (<span class="html-italic">p</span> &lt; 0.05). The absence of any uppercase or lowercase letters indicates that there is no significant difference between different plant components or different slope aspects (<span class="html-italic">p</span> &gt; 0.05).</p>
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<p>The contents of C (<b>a</b>), N (<b>b</b>), P (<b>c</b>), K (<b>d</b>), Ca (<b>e</b>), and Mg (<b>f</b>) of various components of karst forest plants on different slope degrees. Different lowercase letters indicate a significant difference between different slope degrees of the same plant component (<span class="html-italic">p</span> &lt; 0.05). Different capital letters indicate significant differences among different components of the same slope degree (<span class="html-italic">p</span> &lt; 0.05). The absence of any uppercase or lowercase letters indicates that there is no significant difference between different plant components or different slope degrees (<span class="html-italic">p</span> &gt; 0.05).</p>
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<p>The C/N (<b>a</b>), C/P (<b>b</b>), C/K (<b>c</b>), N/P (<b>d</b>), N/K (<b>e</b>), K/P (<b>f</b>), and Ca/Mg (<b>g</b>) of various components of karst forest plants in different microhabitats. Different lowercase letters indicate a significant difference among different microhabitats of the same plant component (<span class="html-italic">p</span> &lt; 0.05). Different capital letters indicate significant differences among different components of plants in the same microhabitat (<span class="html-italic">p</span> &lt; 0.05). The absence of any uppercase or lowercase letters indicates that there is no significant difference between different plant components or different microhabitats (<span class="html-italic">p</span> &gt; 0.05).</p>
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<p>The C/N (<b>a</b>), C/P (<b>b</b>), C/K (<b>c</b>), N/P (<b>d</b>), N/K (<b>e</b>), K/P (<b>f</b>), and Ca/Mg (<b>g</b>) of various components of karst forest plants at different slope positions. Different lowercase letters indicate a significant difference between different slope positions of the same plant component (<span class="html-italic">p</span> &lt; 0.05). Different capital letters indicate a significant difference among different components at the same slope position (<span class="html-italic">p</span> &lt; 0.05). The absence of any uppercase or lowercase letters indicates that there is no significant difference between different plant components or different slope positions (<span class="html-italic">p</span> &gt; 0.05).</p>
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<p>The C/N (<b>a</b>), C/P (<b>b</b>), C/K (<b>c</b>), N/P (<b>d</b>), N/K (<b>e</b>), K/P (<b>f</b>), and Ca/Mg (<b>g</b>) of various components of karst forest plants on different slope aspects. Different lowercase letters indicate a significant difference between different slope aspects of the same plant component (<span class="html-italic">p</span> &lt; 0.05). Different capital letters indicate a significant difference among different components of the same slope aspect (<span class="html-italic">p</span> &lt; 0.05). The absence of any uppercase or lowercase letters indicates that there is no significant difference between different plant components or different slope aspects (<span class="html-italic">p</span> &gt; 0.05).</p>
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<p>The C/N (<b>a</b>), C/P (<b>b</b>), C/K (<b>c</b>), N/P (<b>d</b>), N/K (<b>e</b>), K/P (<b>f</b>), and Ca/Mg (<b>g</b>) of various components of karst forest plants on different slope degrees. Different lowercase letters indicate a significant difference between different slope degrees of the same plant component (<span class="html-italic">p</span> &lt; 0.05). Different capital letters indicate significant differences among different components of the same slope degree (<span class="html-italic">p</span> &lt; 0.05). The absence of any uppercase or lowercase letters indicated that there is no significant difference between different plant components or different slope degrees (<span class="html-italic">p</span> &gt; 0.05).</p>
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<p>RDA ordination diagram of stoichiometric characteristics of different components of plants and ecological factors. The numbers 1–5 represent the topographic factors altitude, slope, aspect, slope position, and microhabitat, respectively. The numbers 6–17 represent the total soil N, hydrolytic N, total P, available P, total K, available K, total Ca, exchangeable Ca, total Mg, exchangeable Mg, organic carbon, and pH, respectively. The numbers 18–31 represent the plant species, life form, DBH, tree height, <span class="html-italic">P<sub>n</sub></span>, <span class="html-italic">T<sub>r</sub></span>, <span class="html-italic">G<sub>s</sub></span>, <span class="html-italic">C<sub>i</sub></span>, <span class="html-italic">SLA</span>, <span class="html-italic">LDMC</span>, <span class="html-italic">LWC</span>, <span class="html-italic">LTD</span>, and N and P reabsorption rate, respectively.</p>
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<p>Variance decomposition results of stoichiometric characteristics of different plant components under the influence of ecological factors.</p>
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21 pages, 3674 KiB  
Article
Inconsistent Variations in Components of Functional Stability Under Heterogeneous Conditions: A Case Study from the Maolan Karst Forest Ecosystems in Guizhou Province, Southwest of China
by Yong Li, Longchenxi Meng, Luyao Chen, Mingzhen Sui, Guangqi Zhang, Qingfu Liu, Danmei Chen, Fangjun Ding and Lipeng Zang
Forests 2025, 16(2), 304; https://doi.org/10.3390/f16020304 - 9 Feb 2025
Viewed by 684
Abstract
Human-induced environmental changes threaten the functional stability of natural forest ecosystems. Understanding the dominant factors influencing both functional space and stability in extremely heterogeneous environments is crucial for elucidating the stability of heterogeneous forest ecosystems. Here, 30 forest dynamic plots were established along [...] Read more.
Human-induced environmental changes threaten the functional stability of natural forest ecosystems. Understanding the dominant factors influencing both functional space and stability in extremely heterogeneous environments is crucial for elucidating the stability of heterogeneous forest ecosystems. Here, 30 forest dynamic plots were established along the successional pathway in Maolan National Nature Reserve in Southwest China. By measuring 15,725 stems across 286 distinct species’ six key plant functional traits, we constructed the key plant functional traits for functional space and quantified functional redundancy (FR) and functional vulnerability (FV) to represent functional stability, and we further utilized the line model and multiple linear regression model to explore the key biotic/abiotic indicators influencing functional stability along the successional pathway of degraded karst forests. Additionally, as the successional pathway unfolded, the contribution of the six plant traits to the overall functional space increased, from 59.85% to 66.64%. These traits included specific leaf area (SLA), leaf dry matter content (LDMC), leaf thickness (LT) and leaf nitrogen content (LNC), which played a crucial role in driving functional space. With the increasing species richness (FR), functional entities (p < 0.001) and FR (p < 0.001) increased, while FV (p < 0.01) decreased. The results also demonstrated a higher FR in degraded karst forests (FR > 2). However, over 51% of FEs consisted of a single species, with the majority of species clustered into a few functional entities (FEs), indicating an elevated level of FV in karst forests. Soil nutrient availability significantly influences the ecosystem’s functional stability, explaining 87% of FR variability and 100% of FV variability. Finally, the rich SR of karst forests could provide sufficient insurance effects; soil pH and available potassium (AK) enhance resilience, and exchangeable calcium (Eca), total phosphorus (TP) and total potassium (TK) indicate the resistance of functional stability in degraded karst forests. This study highlights the complex mechanisms of functional stability in extreme habitat conditions, thereby deepening our understanding of ecosystem function maintenance. Full article
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<p>Geographic locations of the FDPs established.</p>
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<p>The PCA of functional traits within the functional space in the early successional stage (<b>A</b>), later successional stage (<b>B</b>) and climax community (<b>C</b>). Contour lines are used to outline the color gradient, which represents the kernel density of species distribution (from dense, indicated by red, to sparse, indicated by light yellow), corresponding to the 25%, 50% and 95% quantiles of species abundance. The differently colored dots represent the distribution of species in each successional stage.</p>
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<p>Variations in functional stability among successional stages in degraded karst forests. The bottom right of the distribution diagram indicates the number of functional entities (Nb F.E.) present in each successional community. Functional richness (FR, denoted as ‘Red.’) is represented by the horizontal dashed line, which corresponds to the mean number of species per functional entity, with the specific value annotated on the right margin of the panel. Functional vulnerability (FV) is indicated by the horizontal color line accompanied by arrows. Functional over-redundancy (FOR), which represents the percentage of species that exceed the expected number based on FR in over-represented functional entities, is depicted through color coding. Dark yellow represents the climax community stage (<b>A</b>); light brown represents the later successional stage (<b>B</b>); blue represents the early successional stage (<b>C</b>).</p>
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<p>Relationship between α-diversity (species richness (<b>A</b>–<b>D</b>), rarefied species richness (<b>E</b>–<b>H</b>), Pielou’s evenness (<b>I</b>–<b>L</b>)) and four functional indices for the successional stages. The black line delineates the fitted linear function relating α-diversity and the functional indices. Solid lines represent significant effects, while dashed lines denote nonsignificant effects. Dark yellow represents the climax community stage; light brown represents the later successional stage; blue represents the early successional stage. *, <span class="html-italic">p</span> &lt; 0.05; **, <span class="html-italic">p</span> &lt; 0.01; ***, <span class="html-italic">p</span> &lt; 0.001.</p>
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<p>Figure (<b>A</b>–<b>D</b>) illustrate the relative effects of various predictors on FEs, FR, FOR and FV, respectively. The model’s averaged parameter estimates, standardized as regression coefficients, are displayed alongside their corresponding 95% confidence intervals. The relative importance of each predictor is quantified by the proportion of explained variance it accounts for. The relative impact of the predictors and their interactions is calculated by dividing the parameter estimate of each predictor by the sum of all parameter estimates, with the result expressed as a percentage. Abiotic factors include topography and soil. Pfc is the profile curvature; Ele represents the elevation; Eca denotes the exchangeable calcium; POC represents the particulate organic carbon; LFOC represents the light-fraction organic carbon; pH indicates the pH value; TP denotes the total phosphorus; TK represents the total potassium; SOC represents the soil organic carbon; AK represents the available potassium; S-SC denotes the soil saccharase. *, <span class="html-italic">p</span> &lt; 0.05; **, <span class="html-italic">p</span> &lt; 0.01; ***, <span class="html-italic">p</span> &lt; 0.001.</p>
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12 pages, 1521 KiB  
Article
Carbon and Nitrogen Content and CO2 Efflux from Coarse Woody Debris of Norway Spruce, Black Alder, and Silver Birch
by Dovilė Čiuldienė, Egidijus Vigricas, Greta Galdikaitė, Vidas Stakėnas, Kęstutis Armolaitis and Iveta Varnagirytė-Kabašinskienė
Forests 2025, 16(2), 293; https://doi.org/10.3390/f16020293 - 8 Feb 2025
Viewed by 403
Abstract
Coarse woody debris (CWD) is an essential component in forest ecosystems, playing a significant role in enhancing biodiversity, soil formation, and nutrient cycling through decomposition processes. CWD also contributes to greenhouse gas fluxes, particularly through CO2 emissions. This study investigated the physical [...] Read more.
Coarse woody debris (CWD) is an essential component in forest ecosystems, playing a significant role in enhancing biodiversity, soil formation, and nutrient cycling through decomposition processes. CWD also contributes to greenhouse gas fluxes, particularly through CO2 emissions. This study investigated the physical and chemical properties of CWD and the CO2 effluxes from CWD of different decay classes. For this study, a range of CWD—from recently dead to highly decomposed wood—of native tree species such as silver birch (Betula pendula Roth), black alder (Alnus glutinosa (L.) Gaertn.), and Norway spruce (Picea abies (L.) H. Karst.) in hemiboreal forests were investigated. The findings showed that CWD properties significantly differed among tree species and CWD decay classes. Significant variations in wood density and total nitrogen (N) were observed in the early stages of CWD decay, with the highest values found for the deciduous tree species. The concentration of organic carbon (C) increased throughout the decomposition. The lowest CO2 efflux from CWD was found for spruce CWD from all decay classes and it was the highest for black alder and silver birch, especially for the 3rd and 4th decay classes. CO2 efflux was mainly influenced by the degree of decomposition, which was represented by the CWD decay class, followed by wood density and C content. Full article
(This article belongs to the Section Forest Ecology and Management)
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<p>Experimental site with collars installed in forest soil for CO<sub>2</sub> measurements from coarse woody debris (CWD) (Photo: E.Vigricas).</p>
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<p>Physical and chemical properties of coarse woody debris (CWD) of black alder, silver birch, and Norway spruce in different decay classes: wood density (<b>A</b>); wood moisture for each species (<b>B</b>); concentration of organic carbon (OC) (<b>C</b>); concentration of total nitrogen (TN) for each species (<b>D</b>); and C/N ratio (<b>E</b>). The results are expressed as the mean ± 95% CI. Different lowercase letters indicate significantly different (<span class="html-italic">p</span> &lt; 0.05) means among the species, based on Tukey’s test. The equation and coefficient of determination (<span class="html-italic">R</span><sup>2</sup>) indicate the relationship between decay classes and the physical and chemical parameters of the CWD samples.</p>
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<p>The mean CO<sub>2</sub> efflux released from coarse woody debris (CWD) of black alder, silver birch, and Norway spruce across different decay classes. The results are expressed as the mean ± 95% CI, and the different lowercase letters indicate significantly different (<span class="html-italic">p</span> &lt; 0.05) means based on Tukey’s test.</p>
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20 pages, 3900 KiB  
Article
Responses of Soil Enzyme Activity and Microbial Nutrient Limitations to Vegetation Types in a Degraded Karst Trough Valley
by Fengling Gan, Hailong Shi, Xiaohong Tan, Lisha Jiang, Wuyi Li, Yuanyue Xia, Junbing Pu, Quanhou Dai, Youjin Yan and Yuchuan Fan
Forests 2025, 16(2), 279; https://doi.org/10.3390/f16020279 - 6 Feb 2025
Viewed by 444
Abstract
Soil enzyme activities serve as the key indicators of microbial nutrient limitations. Vegetation types after farmland is returned modify both the biological and abiotic properties of the soil, thereby impacting the soil nutrient cycle and the stability of forest ecosystems. However, soil enzyme [...] Read more.
Soil enzyme activities serve as the key indicators of microbial nutrient limitations. Vegetation types after farmland is returned modify both the biological and abiotic properties of the soil, thereby impacting the soil nutrient cycle and the stability of forest ecosystems. However, soil enzyme activities and microbial nutrient limitations in degraded karst forests under different vegetation types after farmland return remain unclear. Therefore, this study investigated the soil physicochemical properties, enzyme activities, and microbial resource limitations in different vegetation types (grasslands (G), transitional grass–shrub (SG), shrubland (S), and secondary forest (F)) after returning farmland on dip and anti-dip slopes in a karst trough valley. The relationships among the factors influencing soil enzyme activities were analyzed to identify the drivers of microbial nutrient limitation. The results revealed that soil enzyme activities and physicochemical properties were significantly greater on anti-dip slopes than on dip slopes. Total nitrogen (27.4%) and bulk density (24.4%) influenced mainly soil enzyme activity and its stoichiometric ratio, whereas carbon and phosphorus limitations impacted soil microorganisms on the dip slopes of the F and G vegetation types. The soil physicochemical properties and enzyme characteristics accounted for 85.5% and 75.6%, respectively, of the observed influence. Notably, the total phosphorus content (36.8%) on the anti-dip erosion slope was significantly greater than that on the other slopes. These factors, especially bedrock strata dip and vegetation type, significantly affect soil enzyme activity. This study confirms that vegetation type enhances soil enzyme activities on anti-dip erosion slopes, providing a scientific basis for karst ecosystem restoration. Full article
(This article belongs to the Section Forest Soil)
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<p>Location of the study area.</p>
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<p>The influence of vegetation type on the physicochemical properties of soil in dip/anti-dip erosion slopes. Note: (<b>a</b>) SWC: soil water content; (<b>b</b>) BD: soil bulk density; (<b>c</b>) TSP: total soil porosity; (<b>d</b>) PH: pH; (<b>e</b>) OC: organic carbon; (<b>f</b>) TN: total nitrogen content; (<b>g</b>) TP: total phosphorus; G: four stages: grasslands; SG: transitional grass–shrub; S: shrubland; F: secondary forest. Significant differences between treatments, denoted by different asterisk number, “*” is statistically significant at the <span class="html-italic">p</span> &lt; 0.05 level; and the “**” is statistically significant at the <span class="html-italic">p</span> &lt; 0.01 level; “***” is statistically significant at the <span class="html-italic">p</span> &lt; 0.001 level. The graph also presents the standard deviation.</p>
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<p>Soil enzyme activities and its stoichiometry under different vegetation type on dip/anti-dip erosion slope. Note: Samples from different vegetation types at dip/anti-dip slopes, respectively. (<b>a</b>) AKP: acid phosphatase; (<b>b</b>) BDC: β-D-cellobiosidase; (<b>c</b>) BG: β-1,4-glucosidase; (<b>d</b>) BNA: β-1,4- N-acetylglucosaminidase; (<b>e</b>) LAP: L-leucine aminopeptidase; (<b>f</b>) E<sub>N:P</sub>: the ratio of (BNA + LAP) and AKP; (<b>g</b>) E<sub>C:N</sub>: the ratio of (BG + BDC): (BNA + LAP); (<b>h</b>) E<sub>C:P</sub>: the ratio of (BG + BDC):AKP; G: four stages: grasslands; SG: transitional grass–shrub stages; S: shrubland stage; F: secondary forest stage; Significant differences between treatments, denoted by different asterisk number, “*” is statistically significant at the <span class="html-italic">p</span> &lt; 0.05 level. The graph also presents the standard deviation.</p>
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<p>Correlation heatmap of soil physicochemical properties and soil enzyme activities under different vegetation types on dip and anti-dip slopes. Note: All abbreviations in this figure are consistent with those in <a href="#forests-16-00279-f002" class="html-fig">Figure 2</a> and <a href="#forests-16-00279-f003" class="html-fig">Figure 3</a>. Significant differences between treatments, denoted by different asterisk number, “*” is statis-tically significant at the <span class="html-italic">p</span> &lt; 0.05 level; and the “**” is statistically significant at the <span class="html-italic">p</span> &lt; 0.01 level.</p>
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<p>Redundancy analysis of the correlation between soil physicochemical properties and soil enzyme activities and the interpretation rate of each variable. Note: all abbreviations in this figure are consistent with those in <a href="#forests-16-00279-f002" class="html-fig">Figure 2</a> and <a href="#forests-16-00279-f003" class="html-fig">Figure 3</a>.</p>
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<p>A scatter plot of soil enzymatic stoichiometry showing the general pattern of microbial resource limitation. Note: all abbreviations in this figure are consistent with those in <a href="#forests-16-00279-f002" class="html-fig">Figure 2</a> and <a href="#forests-16-00279-f003" class="html-fig">Figure 3</a>.</p>
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<p>Variation of vector length and angle under different vegetation types on dip and anti-dip slopes. Note: all abbreviations in this figure are consistent with those in <a href="#forests-16-00279-f002" class="html-fig">Figure 2</a> and <a href="#forests-16-00279-f003" class="html-fig">Figure 3</a>. Significant differences between treatments, denoted by different lowercase letters (e.g., a, b), are statistically significant at the <span class="html-italic">p</span> &lt; 0.05 level. The graph also displays the standard deviation.</p>
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19 pages, 4294 KiB  
Article
Revealing the Exacerbated Drought Stress Impacts on Regional Vegetation Ecosystems in Karst Areas with Vegetation Indices: A Case Study of Guilin, China
by Zijian Gao, Wen He, Yuefeng Yao and Jinjun Huang
Sustainability 2025, 17(3), 1308; https://doi.org/10.3390/su17031308 - 6 Feb 2025
Viewed by 577
Abstract
Global warming has exacerbated the impact of regional drought on vegetation ecosystems, especially in typical karst areas with fragile ecosystems that are more severely affected by drought. However, the response mechanisms of vegetation ecosystems in karst areas to drought stress are still uncertain. [...] Read more.
Global warming has exacerbated the impact of regional drought on vegetation ecosystems, especially in typical karst areas with fragile ecosystems that are more severely affected by drought. However, the response mechanisms of vegetation ecosystems in karst areas to drought stress are still uncertain. With drought stress in the summer of 2022, we examined the spatiotemporal patterns of drought in a World Heritage karst site, Guilin, China, and revealed the exacerbated drought impacts on vegetation ecosystems in karst areas with various vegetation indices. Firstly, we analyzed the spatiotemporal characteristics of drought from 2000 to 2022, utilizing the temperature vegetation dryness index (TVDI), highlighting the intra-annual variability of drought in 2022. Additionally, we compared the responses of different vegetation types to drought stress in karst and non-karst areas and explored the exacerbated impacts of drought stress on vegetation ecosystems within the same year with three vegetation indices, namely, the Normalized Difference Vegetation Index (NDVI), Leaf Area index (LAI), and Gross Primary Production (GPP) in karst areas. The results showed that drought started in July and persisted from August to November at moderate to severe levels (with severe drought in September), eventually easing in December. Karst areas exhibited severe drought (TVDI = 0.76), which more significantly impacted regional vegetation ecosystems than those in non-karst areas. Different vegetation types also experienced greater drought stress in karst areas compared to non-karst areas. The vegetation indices increased at the early- to mid-stages of drought (July to September) compared to those in the baseline year (2020–2021), mainly due to the increase in non-karst areas. However, vegetation indices decreased at the late drought stage (October to November), primarily due to the decrease in karst areas, indicating that the karst topography exacerbated the impact of drought on regional vegetation ecosystems. Since LAI and GPP exhibited similar changing patterns to TVDI, with GPP showing particularly strong alignment, they can be used to reveal the response mechanisms of ecosystems to drought stress in karst areas. We emphasize the importance of monitoring the responses of vegetation ecosystems to climate-induced droughts stress and enhancing their resilience to future climatic challenges, particularly in karst areas. Full article
(This article belongs to the Special Issue Impact and Adaptation of Climate Change on Natural Ecosystems)
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<p>Guilin karst and non-karst area distribution patterns.</p>
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<p>Drought trend analysis in Guilin city based on the standardized precipitation index over 12 months (SPI-12), standardized precipitation evapotranspiration index over 12 months (SPEI-12), and TVDI.</p>
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<p>Spatial distribution of the TVDI in 2022, the black line represents the karst area.</p>
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<p>Spatial distribution and trend in drought in Guilin city: (<b>a</b>) Theil–Sen median drought trend based on the TVDI from 2000 to 2022; (<b>b</b>) significance test of drought changes using the Mann–Kendall test from 2000 to 2022; (<b>c</b>) coefficient of variation of the TVDI from 2000 to 2022, the black line represents the karst area.</p>
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<p>Monthly spatial patterns of the TVDI in 2022 in Guilin city.</p>
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<p>Monthly TVDI values in karst and non-karst areas of Guilin city in 2022.</p>
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<p>Comparison of TVDI among different vegetation types between karst and non-karst areas.</p>
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<p>The proportion of vegetation area and their distribution in drought severity categories in the karst area.</p>
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<p>Monthly variations in the average NDVI (<b>a</b>), LAI (<b>b</b>), and GPP (<b>c</b>) values during the second half of 2022 compared to those in the baseline year (2020–2021) in Guilin city. The background colors in the figure represent different phases of the drought: the yellow part represents the early to mid-drought phase, the orange part represents the late drought phase, and the green part represents the drought fade-away period.</p>
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<p>Differences in the NDVI (<b>a</b>), LAI (<b>b</b>), and GPP (<b>c</b>) values in the karst and non-karst areas between the 2022 drought period and the baseline year (2020–2021).</p>
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19 pages, 10553 KiB  
Article
Changes in Ecological–Production–Social Functions in Karst Areas: Insight from Guizhou Province, South China Karst
by Rong Zhao, Kangning Xiong, Anjun Lan, Qiwei Chen, Zhaojun Liu, Fangli Feng and Nana Yu
Land 2025, 14(2), 209; https://doi.org/10.3390/land14020209 - 21 Jan 2025
Viewed by 496
Abstract
The ecosystems and human social systems in karst areas are undergoing rapid development. In this context, effectively identifying changes in the various functions of karst areas is crucial for formulating accurate sustainable development policies. However, few studies have discussed the ecological, production, and [...] Read more.
The ecosystems and human social systems in karst areas are undergoing rapid development. In this context, effectively identifying changes in the various functions of karst areas is crucial for formulating accurate sustainable development policies. However, few studies have discussed the ecological, production, and social functions of karst areas within an integrated framework. Therefore, this paper utilizes comprehensive evaluation methods, standard deviation classification, and coordination models to analyze the spatiotemporal changes in these functions of karst areas from 2000 to 2020. The results indicate that over the 20-year period, the ecological function, production function, and social function in karst areas have shown an annual growth trend with noticeable spatiotemporal differentiation. The dominant functions of the area have undergone significant changes, with the ecological function being dominant in 2000, the production function becoming dominant in 2010, and the social function taking the lead in 2020. Over the past 20 years, the lagged development type has remained the predominant combined function type. The coordination levels among the three functions have significantly improved, with the coordination between the ecological function and the production function transitioning from non-coordination to coordination in 2010. Furthermore, the coordination between the ecological function and the social function, and between the production function and the social function, achieved coordination status in 2020. This study enhances the understanding of the multifunctional evolution in karst areas and provides theoretical and practical guidance for ecological restoration, industrial development, and social reconstruction in karst areas. Full article
(This article belongs to the Topic Karst Environment and Global Change)
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<p>Geographical location of karst areas in Guizhou, Southwest China.</p>
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<p>Spatial-temporal change in ecological, production, social, and comprehensive functions in the Guizhou karst area from 2000 to 2020. <span class="html-italic">Notes:</span> The natural breaks method was applied to categorize the functional values of counties from 2000 to 2020 into five levels. Ecological function: low [0, 0.159), mid-low [0.159, 0.246), mid [0.246, 0.371), mid-high [0.371, 0.534), high [0.534, 0.887). Production function: low [0, 0.116), mid-low [0.116, 0.189), mid [0.189, 0.278), mid-high [0.278, 0.388), high [0.388, 0.732). Social function: low [0, 0.075), mid-low [0.075, 0.142), mid [0.142, 0.242), mid-high [0.242, 0.407), high [0.407, 0.720). Comprehensive function: low [0, 0.350), mid-low [0.350, 0.503), mid [0.503, 0.721), mid-high [0.721, 1.020), high [1.020, 1.583).</p>
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<p>Kernel density distribution of comprehensive function index in the Guizhou karst area from 2000 to 2020.</p>
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<p>Standard deviation elliptic distribution of ecological, production, and social functions in the Guizhou karst area from 2000 to 2020.</p>
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<p>Distribution of the dominant functions in the Guizhou karst area from 2000 to 2020.</p>
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<p>Summary of combined functions in the Guizhou karst area from 2000 to 2020.</p>
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<p>Distribution of the combined functions in the Guizhou karst area from 2000 to 2020.</p>
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<p>Spatial-temporal evolution of the function’s coordination in the Guizhou karst area from 2000 to 2020.</p>
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<p>Coordinated evolution of sub-functions in the Guizhou karst area from 2000 to 2020. <span class="html-italic">Notes:</span> EF (ecological function); PF (production function); SF (social function).</p>
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<p>Coordinated mechanism of ecological, production, and social functions.</p>
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12 pages, 1232 KiB  
Article
Biochar Application and Mowing Independently and Interactively Influence Soil Enzyme Activity and Carbon Sequestration in Karst and Red Soils in Southern China
by Wenjia Luo, Daniel F. Petticord, Shiwen Zhu, Shaowu Zhu, Yuanlong Wu, Xun Yi, Xinyue Wang, Yili Guo and Xuxin Song
Agronomy 2025, 15(1), 252; https://doi.org/10.3390/agronomy15010252 - 20 Jan 2025
Viewed by 748
Abstract
Soil organic carbon (SOC), a critical component of the global carbon cycle, represents the largest terrestrial carbon reservoir, and is thus a major component of influencing climate regulation and ecosystem health. Grasslands store substantial carbon in their soils, but this carbon reservoir is [...] Read more.
Soil organic carbon (SOC), a critical component of the global carbon cycle, represents the largest terrestrial carbon reservoir, and is thus a major component of influencing climate regulation and ecosystem health. Grasslands store substantial carbon in their soils, but this carbon reservoir is easily degraded by both grazing and mowing, particularly in vulnerable karst landscapes. This study investigates the potential of biochar, a carbon-rich soil amendment, as a management tool to maintain SOC or mitigate the degradation of SOC during mowing in karst grasslands in Southern China, using both red acidic and calcareous soils as experimental variables. T SOC fractions, soil enzyme activities, and soil pH were measured to determine the effect of mowing and biochar application on carbon stability and microbial activity. Consistent with expectations, mowing increases belowground biomass and promotes carbon loss through increased microbial activity, particularly in calcareous soils where mowing also decreases soil pH, increasing acidity and reducing the stability of Ca–carbon complexes. Biochar, however, counteracted these effects, increasing both particulate organic carbon (POC) and mineral-associated organic carbon (MAOC), especially in red soils where the addition of biochar greatly increased soil pH (from 5.4 to 6.33) (an effect not observed in the already-alkaline karst soils). Enzyme activities related to carbon degradation, such as β-D-Glucosidase and peroxidase, increased in biochar-amended soils (β-D-Glucosidase increased from 12.77 to 24.53 nmol/g/h and peroxidase increased from 1.1 to 2.36 mg/g/2h), each of which contribute to the degradation of carbon containing organic matter so that it may be ultimately stored in more recalcitrant forms. Mowing led to reduced polyphenol oxidase activity, but the presence of biochar mitigated these losses, protecting SOC pools (increased from 0.03 to 0.79 mg/g/2h). This study highlights biochar as an effective tool for enhancing SOC stability in karst grasslands, particularly in acidic soils, and suggests that integrating biochar into mowing regimes may optimize carbon sequestration while reducing fire risk. These findings offer valuable theoretical guidance for developing sustainable land management in sensitive ecosystems. Full article
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<p>Effect of mowing and biochar on soil particulate organic carbon (POC) (<b>a</b>) and mineral-associated organic carbon (MAOC) (<b>b</b>) in different soil types (no biochar, CK; with biochar, B; red soil, R; and calcareous soil, C). Values represent mean ± SE (<span class="html-italic">n</span> = 4). Different uppercase letters indicate significant differences among treatments under no mowing, different lowercase letters indicate significant differences among treatments under mowing (<span class="html-italic">p</span> ≤ 0.05). Asterisk indicates significant differences between mowing and no mowing treatments (* <span class="html-italic">p</span> &lt; 0.05; ** <span class="html-italic">p</span> &lt; 0.01; and *** <span class="html-italic">p</span> &lt; 0.001).</p>
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<p>Effect of mowing and biochar on polyphenol oxidase (PPO) (<b>a</b>), peroxidase (PER) (<b>b</b>), β-D-Glucosidase (βG) (<b>c</b>), and leucine aminopeptidase (LAP) (<b>d</b>) in different soil types (no biochar, CK; with biochar, B; red soil, R; and calcareous soil, C). Values represent mean ± SE (<span class="html-italic">n</span> = 4). Different uppercase letters indicate significant differences among treatments under no mowing, different lowercase letters indicate significant differences among treatments under mowing (<span class="html-italic">p</span> ≤ 0.05). Asterisk indicates significant differences between mowing and no mowing treatments (** <span class="html-italic">p</span> &lt; 0.01; and *** <span class="html-italic">p</span> &lt; 0.001).</p>
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<p>Effect of mowing and biochar on belowground biomass (<b>a</b>), pH (<b>b</b>), microbial biomass carbon (MBC) (<b>c</b>), ammonium nitrogen (NH<sub>4</sub>-N) (<b>d</b>), nitrate nitrogen (NO<sub>3</sub>-N) (<b>e</b>), and total available nitrogen (AN) (<b>f</b>) in different soil types (no biochar, CK; with biochar, B; red soil, R; and calcareous soil, C). Values represent mean ± SE (<span class="html-italic">n</span> = 4). Different uppercase letters indicate significant differences among treatments under no mowing, different lowercase letters indicate significant differences among treatments under mowing (<span class="html-italic">p</span> ≤ 0.05). Asterisk indicates significant differences between mowing and no mowing treatments (* <span class="html-italic">p</span> &lt; 0.05; ** <span class="html-italic">p</span> &lt; 0.01; and *** <span class="html-italic">p</span> &lt; 0.001).</p>
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20 pages, 8949 KiB  
Article
Distribution, Risk Assessment, and Quantitative Source Analysis of Soil Heavy Metals in a Typical Agricultural City of East-Central China
by Wenyue Du, Peng Zeng, Shi Yu, Fan Liu and Ping’an Sun
Land 2025, 14(1), 66; https://doi.org/10.3390/land14010066 - 1 Jan 2025
Viewed by 937
Abstract
The land use in agricultural areas contributes to economic growth while concurrently accompanied by a series of environmental pollution issues. Xingguo County, Ganzhou City, Jiangxi Province, is a typical agricultural area with selenium-rich soil, and the rice and navel oranges grown there have [...] Read more.
The land use in agricultural areas contributes to economic growth while concurrently accompanied by a series of environmental pollution issues. Xingguo County, Ganzhou City, Jiangxi Province, is a typical agricultural area with selenium-rich soil, and the rice and navel oranges grown there have high nutritional value. This study analyzed the distribution of heavy metals in the soil of this area through the kriging interpolation method, evaluated the risks of heavy metals in the soil using different pollution index methods, and quantitatively analyzed their sources using principal component analysis (PCA) and positive matrix factorization (PMF), with the aim of protecting the ecological resources of this area and providing theoretical references for avoiding heavy metal pollution of crops in the soil. The research results indicate the following: (1) Based on the background values of Ganzhou, Jiangxi Province, all heavy metals have caused pollution to the soil except for As and Hg, among which Cd poses the highest potential ecological risk in the study area. According to the values of the Environmental Quality Standards for Soil (EQSS), the concentrations of heavy metals have not exceeded the standards and have relatively low potential ecological risks. (2) In terms of health risks, all soil heavy metals basically do not bring non-carcinogenic risks but acceptable carcinogenic risks to adults and children, except for Cd. The carcinogenic and non-carcinogenic risks of soil heavy metals for children are higher than those for adults, and the main exposure route is ingestion. Among different land use types, the carcinogenic and non-carcinogenic risks of soil heavy metals in orchards are the highest. (3) Combining the kriging interpolation method and the PCA and PMF models, it can be determined that there are two main sources of heavy metals in the study area: one is natural and the other is anthropogenic. Among the anthropogenic sources, agricultural sources contribute the most to soil heavy metal pollution. Through these research results, it can be found that soil heavy metal detection should be conducted in agricultural land, and risk-based management measures should be implemented. Full article
(This article belongs to the Special Issue New Insights in Soil Quality and Management in Karst Ecosystem II)
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<p>Map of the study region and sampling sites.</p>
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<p>Concentration and exceeding rate of heavy metals in soil from different land uses.</p>
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<p>SFPI values of heavy metals in soils of different land uses.</p>
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<p>Pearson correlation coefficients among heavy metals in soil. * <span class="html-italic">p</span> &lt; 0.05, ** <span class="html-italic">p</span> &lt; 0.01.</p>
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<p>Source profiles and source contributions of soil heavy metals. (<b>a</b>) source contributions of soil heavy metals by factor 1; (<b>b</b>) source contributions of soil heavy metals by factor 2; (<b>c</b>) source contributions of soil heavy metals by factor 3; (<b>d</b>) source contributions of soil heavy metals by factor 4; (<b>e</b>) source contributions of soil heavy metals by factor 5.</p>
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<p>Spatial distribution of heavy metals in the study area.</p>
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<p>Factor profiles of heavy metal sources identified by PMF.</p>
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18 pages, 7581 KiB  
Article
Prediction of Potential Habitat Distributions and Climate Change Impacts on the Rare Species Woonyoungia septentrionalis (Magnoliaceae) in China Based on MaxEnt
by Weihao Yao, Zenghui Wang, Yu Fan, Danyang Liu, Zeyang Ding, Yumei Zhou, Shuyue Hu, Wei Zhang and Jing Ou
Plants 2025, 14(1), 86; https://doi.org/10.3390/plants14010086 - 30 Dec 2024
Viewed by 723
Abstract
Changes in species’ habitats provide important insights into the effects of climate change. Woonyoungia septentrionalis, a critically endangered species endemic to karst ecosystems, has a highly restricted distribution and is a key biological resource. Despite its ecological importance, the factors influencing its [...] Read more.
Changes in species’ habitats provide important insights into the effects of climate change. Woonyoungia septentrionalis, a critically endangered species endemic to karst ecosystems, has a highly restricted distribution and is a key biological resource. Despite its ecological importance, the factors influencing its habitat suitability and distribution remain poorly understood. This study employed ecological niche modeling to predict the potential distribution of Woonyoungia septentrionalis across China and analyzed shifts in centroid location to explore migration pathways under current and future climate scenarios. The model exhibited high predictive accuracy (AUC = 0.988), indicating its robustness in assessing habitat suitability. Under current climatic conditions, Woonyoungia septentrionalis is predominantly found in the Guizhou–Guangxi border region, southeastern Yunnan, eastern Sichuan, southeastern Tibet, and parts of Chongqing, Hunan, and Hubei. Among these, the Guizhou-Guangxi border represents the primary suitable habitat. Temperature factors, particularly bio6 (minimum temperature of the coldest month) and bio7 (annual temperature range), were the most significant determinants of habitat suitability, contributing 43.29% and 12.65%, respectively. Soil cation exchange capacity (CEC) accounted for 15.82%, while precipitation had a relatively minor impact. Under future climate scenarios, suitable habitats for Woonyoungia septentrionalis are projected to shrink and shift toward higher altitudes and latitudes, increasing the risk of extinction due to the “mountain trap” effect, where migration is constrained by limited habitat at higher elevations. Stable habitats, particularly in Libo (Guizhou) and Huanjiang (Guangxi), are identified as critical refugia. We recommend prioritizing shrinking and stable habitats in Guizhou, Guangxi, and Yunnan for in situ conservation. Ex situ conservation efforts should focus on areas identified based on key environmental factors and predicted migration pathways to ensure the species’ long-term survival. This study provides both theoretical and practical guidance for the conservation of this species and its vulnerable habitat. Full article
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<p>Photographs (<b>a</b>–<b>c</b>) and occurrence records (<b>d</b>) of <span class="html-italic">W. septentrionalis</span> used in the MaxEnt model. All photographs were taken by the author.</p>
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<p>Performances of MaxEnt model in simulating and predicting the potential distribution of <span class="html-italic">W. septentrionalis</span> in different settings.</p>
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<p>The validation of the MaxEnt model predicting <span class="html-italic">W. septentrionalis</span> distribution: (<b>a</b>) omission rate and (<b>b</b>) ROC curve.</p>
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<p>Jackknife test for environmental variables.</p>
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<p>Response curves of <span class="html-italic">W. septentrionalis</span> to important climatic and edaphic factors.</p>
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<p>Distribution of suitable areas of <span class="html-italic">W. septentrionalis</span> under current climatic conditions.</p>
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<p>Areas (<b>A</b>) and area changes (<b>B</b>) of predicted suitable habitat in different climatic periods based on MaxEnt model.</p>
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<p>Map of predicted distribution of suitable areas. Predicted distribution under SSP126 scenario in the 2050s (<b>a</b>), 2070s (<b>d</b>), under the SSP245 scenario in the 2050s (<b>b</b>), 2070s (<b>e</b>), under the SSP585 scenario in the 2050s (<b>c</b>), and 2070s (<b>f</b>).</p>
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<p>Spatial change patterns of suitable habitats of <span class="html-italic">W. septentrionalis</span> under different climate scenarios.</p>
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<p>The centroid change in suitable habitats of <span class="html-italic">W. septentrionalis</span> under different climate scenarios.</p>
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