Nothing Special   »   [go: up one dir, main page]

You seem to have javascript disabled. Please note that many of the page functionalities won't work as expected without javascript enabled.
 
 
Sign in to use this feature.

Years

Between: -

Subjects

remove_circle_outline
remove_circle_outline
remove_circle_outline
remove_circle_outline
remove_circle_outline
remove_circle_outline
remove_circle_outline
remove_circle_outline
remove_circle_outline

Journals

remove_circle_outline
remove_circle_outline
remove_circle_outline
remove_circle_outline
remove_circle_outline
remove_circle_outline
remove_circle_outline
remove_circle_outline

Article Types

Countries / Regions

remove_circle_outline
remove_circle_outline
remove_circle_outline
remove_circle_outline
remove_circle_outline
remove_circle_outline

Search Results (1,517)

Search Parameters:
Keywords = sandy soil

Order results
Result details
Results per page
Select all
Export citation of selected articles as:
16 pages, 1191 KiB  
Article
Gigaspora roseae and Coriolopsis rigida Fungi Improve Performance of Quillaja saponaria Plants Grown in Sandy Substrate with Added Sewage Sludge
by Guillermo Pereira, Diyanira Castillo-Novales, Cristian Salazar, Cristian Atala and Cesar Arriagada-Escamilla
J. Fungi 2025, 11(1), 2; https://doi.org/10.3390/jof11010002 (registering DOI) - 24 Dec 2024
Abstract
The use of living organisms to treat human by-products, such as residual sludge, has gained interest in the last years. Fungi have been used for bioremediation and improving plant performance in contaminated soils. We investigated the impact of the mycorrhizal fungus (MF) Gigaspora [...] Read more.
The use of living organisms to treat human by-products, such as residual sludge, has gained interest in the last years. Fungi have been used for bioremediation and improving plant performance in contaminated soils. We investigated the impact of the mycorrhizal fungus (MF) Gigaspora roseae and the saprophytic fungus (SF) Coriolopsis rigida on the survival and growth of Quillaja saponaria seedlings cultivated in a sandy substrate supplemented with residual sludge. Q. saponaria is a sclerophyllous tree endemic to Chile, known for its high content of saponins. We inoculated plants with the MF, the SF, and a combination of both (MF + SF). Following inoculation, varying doses of liquid residual sludge equivalent to 0, 75, and 100% of the substrate’s field capacity were applied. After 11 months, we found a positive influence of the utilized microorganisms on the growth of Q. saponaria. Particularly, inoculation with the SF resulted in higher plant growth, mycorrhizal colonization percentage, and higher enzymatic activity, especially after the application of the sludge. This increase was more evident with higher doses of the applied sludge. These results highlight the potential of combined microorganism and residual sludge application as a sustainable strategy for enhancing plant growth and reducing waste. Full article
(This article belongs to the Special Issue Fungi Activity on Remediation of Polluted Environments, 2nd Edition)
Show Figures

Figure 1

Figure 1
<p>Growth performance of <span class="html-italic">Q. saponaria</span> plants inoculated with mycorrhizal and saprophytic fungi in sandy substrate. Height growth (<b>A</b>) and DAC (<b>B</b>) of <span class="html-italic">Q. saponaria</span> plants inoculated with the MF <span class="html-italic">G. roseae</span> and the SF <span class="html-italic">C. rigida</span>, and with both (MF + SF) in sandy substrate. Different letters denote significant differences (Tukey test <span class="html-italic">p</span> &lt; 0.05).</p>
Full article ">Figure 2
<p>Aerial and radicle biomass of <span class="html-italic">Q. Saponaria</span> plants inoculated with the MF <span class="html-italic">G. roseae</span> and SF <span class="html-italic">C. rigida</span>, or their combination (MF + SF), under increasing doses of residual sludge. Different letters denote significant differences (Tukey test <span class="html-italic">p</span> &lt; 0.05).</p>
Full article ">Figure 3
<p>Mycorrhization % in <span class="html-italic">Q. saponaria</span> plants inoculated with the MF <span class="html-italic">G. roseae</span> or with a combination of MF + SF (<span class="html-italic">G. roseae</span> and <span class="html-italic">C. rigida</span>) after the addition of increasing concentrations of waste sludge. Different letters denote significant differences (Tukey test <span class="html-italic">p</span> &lt; 0.05).</p>
Full article ">
18 pages, 5346 KiB  
Article
Metagenome Analysis Identified Novel Microbial Diversity of Sandy Soils Surrounded by Natural Lakes and Artificial Water Points in King Salman Bin Abdulaziz Royal Natural Reserve, Saudi Arabia
by Yahya S. Al-Awthan, Rashid Mir, Fuad A. Alatawi, Abdulaziz S. Alatawi, Fahad M. Almutairi, Tamer Khafaga, Wael M. Shohdi, Amal M. Fakhry and Basmah M. Alharbi
Life 2024, 14(12), 1692; https://doi.org/10.3390/life14121692 - 20 Dec 2024
Viewed by 362
Abstract
Background: Soil microbes play a vital role in the ecosystem as they are able to carry out a number of vital tasks. Additionally, metagenomic studies offer valuable insights into the composition and functional potential of soil microbial communities. Furthermore, analyzing the obtained data [...] Read more.
Background: Soil microbes play a vital role in the ecosystem as they are able to carry out a number of vital tasks. Additionally, metagenomic studies offer valuable insights into the composition and functional potential of soil microbial communities. Furthermore, analyzing the obtained data can improve agricultural restoration practices and aid in developing more effective environmental management strategies. Methodology: In November 2023, sandy soil samples were collected from ten sites of different geographical areas surrounding natural lakes and artificial water points in the Tubaiq conservation area of King Salman Bin Abdulaziz Royal Natural Reserve (KSRNR), Saudi Arabia. In addition, genomic DNA was extracted from the collected soil samples, and 16S rRNA sequencing was conducted using high-throughput Illumina technology. Several computational analysis tools were used for gene prediction and taxonomic classification of the microbial groups. Results: In this study, sandy soil samples from the surroundings of natural and artificial water resources of two distinct natures were used. Based on 16S rRNA sequencing, a total of 24,563 OTUs were detected. The metagenomic information was then categorized into 446 orders, 1036 families, 4102 genera, 213 classes, and 181 phyla. Moreover, the phylum Pseudomonadota was the most dominant microbial community across all samples, representing an average relative abundance of 34%. In addition, Actinomycetes was the most abundant class (26%). The analysis of clustered proteins assigned to COG categories provides a detailed understanding of the functional capabilities and adaptation of microbial communities in soil samples. Amino acid metabolism and transport were the most abundant categories in the soil environment. Conclusions: Metagenome analysis of sandy soils surrounding natural lakes and artificial water points in the Tubaiq conservation area of KSRNR (Saudi Arabia) has unveils rich microbial activity, highlighting the complex interactions and ecological roles of microbial communities in these environments. Full article
(This article belongs to the Special Issue Trends in Microbiology 2025)
Show Figures

Figure 1

Figure 1
<p>(<b>A</b>) A map showing research area inside within Al-Tubaiq region of the KSRNR. (<b>B</b>) Locations of the sampling sites within the Tubaiq area of KSRNR.</p>
Full article ">Figure 1 Cont.
<p>(<b>A</b>) A map showing research area inside within Al-Tubaiq region of the KSRNR. (<b>B</b>) Locations of the sampling sites within the Tubaiq area of KSRNR.</p>
Full article ">Figure 2
<p>Proportional abundance of key microbial orders and phyla in samples of soil. (<b>A</b>) Relative abundance of bacteria based on phylum. (<b>B</b>) Relative abundance of bacteria based on order.</p>
Full article ">Figure 3
<p>Proportional abundance of key microbial families and classes in samples of soil. (<b>A</b>) Relative abundance of bacteria based on class. (<b>B</b>) Relative abundance of bacteria based on family.</p>
Full article ">Figure 4
<p>Proportional abundance of key microbial species and genera in samples of soil. (<b>A</b>) Relative abundance of bacteria based on genus. (<b>B</b>) Relative abundance of bacteria based on species.</p>
Full article ">Figure 5
<p>(<b>A</b>) Correlation matrix illustrating the relationships between soil samples based on bacterial species prevalence. * <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) (<b>B</b>) Heatmap and hierarchical clustering of soil samples and dominant species distribution.</p>
Full article ">Figure 6
<p>(<b>A</b>) Enriched OTUs by COG functional groups. (<b>B</b>) Average OTU counts per COG category.</p>
Full article ">
19 pages, 4173 KiB  
Article
The Spatiotemporal Estimation of the Chupaderos Aquifer Groundwater Recharge for 2020 Based on the Soil Moisture Approach and Remote Sensing
by María López-Cuevas, Anuard Pacheco-Guerrero, Edith Olmos-Trujillo, Juan Ernesto Ramírez-Juárez, Anuar Badillo-Olvera, Claudia Ávila-Sandoval and Hiram Badillo-Almaraz
Hydrology 2024, 11(12), 218; https://doi.org/10.3390/hydrology11120218 - 20 Dec 2024
Viewed by 243
Abstract
Groundwater, which is widely used in arid regions due to scarcity of surface sources, has excellent quality and, under certain conditions, can be consumed directly. Human activities have caused climate change, leading to decreased precipitation and increased temperatures, which reduces water recharge and [...] Read more.
Groundwater, which is widely used in arid regions due to scarcity of surface sources, has excellent quality and, under certain conditions, can be consumed directly. Human activities have caused climate change, leading to decreased precipitation and increased temperatures, which reduces water recharge and increases underground extraction volume. To estimate the natural recharge of the Chupaderos aquifer, located in the State of Zacatecas, México, a spatiotemporal analysis methodology was used, using a soil moisture balance, which includes satellite information on precipitation and temperature, to obtain infiltration, evapotranspiration, and moisture. Using a Geographic Information System (GIS), a distributed spatial model was created in which the potential recharge areas that can be defined by raster images. The results show that there is a maximum annual recharge of 137 mm in the soil where Fluvisol and Kastanozem predominate, an indicator of a texture of sandy soil and franco-sandy area, which is mainly covered by forest and scrub. This result confirms that these characteristics are indispensable for the use of water in soil. Therefore, the preservation of the ecosystem is essential for aquifer recharge. Full article
(This article belongs to the Section Soil and Hydrology)
Show Figures

Figure 1

Figure 1
<p>(<b>a</b>) The study area showing the location of Mexico, (<b>b</b>) the Mexican state of Zacatecas, and (<b>c</b>) the map showing the extent of the Chupaderos aquifer.</p>
Full article ">Figure 2
<p>(<b>a</b>) <math display="inline"><semantics> <mrow> <msub> <mrow> <mi mathvariant="normal">C</mi> <mi mathvariant="normal">f</mi> </mrow> <mrow> <mi mathvariant="normal">o</mi> </mrow> </msub> </mrow> </semantics></math> is defined as the foliage retention coefficient. It is the percentage of monthly rain that is retained by foliage, which ranges from 0% for bodies of water and urban areas to 20% for the forest and its different vegetative species, which include grassland, scrubland, beans in rain-fed agriculture, and chili peppers in irrigation agriculture (<a href="#hydrology-11-00218-t001" class="html-table">Table 1</a>). (<b>b</b>) Infiltration by vegetation cover (<math display="inline"><semantics> <mrow> <msub> <mrow> <mi mathvariant="normal">K</mi> </mrow> <mrow> <mi mathvariant="normal">v</mi> </mrow> </msub> </mrow> </semantics></math>), is the fraction of rain that infiltrates due to the effect of vegetation cover, with a range of values from 0.1 to 0.2. (<b>c</b>) Infiltration by texture (<math display="inline"><semantics> <mrow> <msub> <mrow> <mi mathvariant="normal">K</mi> </mrow> <mrow> <mi mathvariant="normal">f</mi> <mi mathvariant="normal">c</mi> </mrow> </msub> </mrow> </semantics></math>), is defined as a fraction of rain that infiltrates due to the effect of soil texture, which allows for obtaining monthly infiltrated rain using that concept. It is within the range of a minimum of 0.40 and a maximum value of 0.93.</p>
Full article ">Figure 3
<p>(<b>a</b>) Base infiltration (Fc), defined as the fluctuation of the basic infiltration rate according to the soil texture, in millimeters per day; (<b>b</b>) the second is by slope, which is defined as <math display="inline"><semantics> <mrow> <msub> <mrow> <mi mathvariant="normal">K</mi> </mrow> <mrow> <mi mathvariant="normal">p</mi> </mrow> </msub> </mrow> </semantics></math>. It is the fraction that infiltrates due to the slope effect. The lower the slope of the land and the greater the vegetation cover, the lower is speed of runoff, generating greater infiltration. The study area is mostly flat, and (<b>c</b>) infiltration coefficient (<math display="inline"><semantics> <mrow> <msub> <mrow> <mi mathvariant="normal">C</mi> </mrow> <mrow> <mi mathvariant="normal">i</mi> </mrow> </msub> </mrow> </semantics></math>), is the factor by which the monthly precipitation must be multiplied to obtain the monthly water infiltration into the soil, the value of which must not be greater than 1.</p>
Full article ">Figure 4
<p>(<b>a</b>) DA: It allows us to see the ease of penetration of the roots into the soil, as well as the transmission of water. The change in soil porosity is responsible for the rapid drainage of excess water. It is a good indicator of soil quality. Its values range from 1.25 g/cm<sup>3</sup> for areas where clay predominates to 1.68 g/cm<sup>3</sup> for sandy soils. (<b>b</b>) <math display="inline"><semantics> <mrow> <msub> <mrow> <mi mathvariant="normal">P</mi> </mrow> <mrow> <mi mathvariant="normal">r</mi> </mrow> </msub> </mrow> </semantics></math>: It shows the root depth of the study area. The value 0 represents the areas where there are bodies of water and urban areas, while the deepest root is that of the scrub with 5.1 m depth. (<b>c</b>) CC: It is the maximum moisture that a soil can have without being saturated; it is when the plant has the maximum transpiration capacity, defined as the available water layer. The values range from 0 for bodies of water and urban areas to 2231.25 mm for soil where clay predominates. (<b>d</b>) PMP: When soil moisture reaches the PMP, the plant does not transpire and dies; just as CC is represented by the water layer, this results in a value of 0 mm for water bodies and urban areas up to 1083.75 mm, in relation to the soil texture.</p>
Full article ">Figure 5
<p>(<b>a</b>) Water recharge in January varies between −56.90 mm to 1.86 mm, with an average of −6.29 mm. The green color represents the lowest value, spreading out in some central areas, while blue predominates in the northern part, representing the highest values. In January, the recharge is somewhat scarce due to the presence of low rainfall. (<b>b</b>) February has low rainfall, so the balance shows an average recharge of 1.09 mm. It can be seen that there is a minimum recharge of −5.38 mm and that the green color, the same that represents the lower levels, predominates in the whole area, while the blue one is found only in some central portions. This difference in distribution is due to the fact that precipitation is not uniform and is considered as a maximum recharge of 49.22 mm. (<b>c</b>) In March, the recharge already begins to stabilize, and the balance obtained has a minimum of −50.61 mm and the maximum of 10.32 mm, with an average of 4.38 m. In March, the negative values are no longer predominant in the raster image because the sum of actual evapotranspiration and final soil moisture does not exceed the sum of initial soil precipitation and moisture. (<b>d</b>) The maximum recharge obtained can be observed in some areas south of the aquifer (76.53 mm) and the minimum of −19.88 mm is present in the central part to the north (these negative values are translated as a deficit of the recharge), with an average of 1.12 mm throughout the area.</p>
Full article ">Figure 6
<p>(<b>a</b>) In May, although the maximum recharge is not very high, the aquifer predominates in most of the area, specifically in the north with 2.74 mm and the minimum of −58.80 in the south, and the average of −11.63 mm becomes present in the central zone of the aquifer. (<b>b</b>) In June when the rains begin to be abundant, the temperature increases considerably, causing the actual evapotranspiration and moisture of the final soil to exceed the values of precipitation and moisture of the initial soil. The average recharge is −8.25 mm, the same as observed throughout the study area; the minimum of −47.88 is in the center, and the maximum of 79.62 mm occurs in minimal portions to the southeast of the aquifer. (<b>c</b>) July is the month when rainfall exceeds average precipitation levels. It is confirmed that despite high evapotranspiration rates, there are no negative values or deficit of recharge, an average of 12.64 mm, a minimum of 0.01 mm, and a maximum of 65.12 mm. (<b>d</b>) For the month of August, as in July, there are no deficit rates. The image shows the spatial distribution of recharge in different aquifer areas. The values obtained through the methodology show that the recharge is between 3.19 mm as the minimum and 77.31 mm as the maximum and an average of 31.55 mm.</p>
Full article ">Figure 7
<p>(<b>a</b>) in September, the recharge rate has already fallen to −75.41 mm, with a minimum of −16.02 mm, although negative values are already present. In the distribution, it can be seen that the maximum predominates in much of the aquifer. (<b>b</b>) in October, precipitation rates decrease considerably; however, temperature decreases are observed, which is attributed to low evapotranspiration and a high predominance of soil moisture. The balance shows that the average is 15.82 mm, the maximum is 70.98 mm, and the minimum is 5.33. We can conclude that throughout the month, the infiltration of rain is constant. (<b>c</b>) In November, the balance shows that the average is 1.87 mm, the maximum is 7.16 mm, and the minimum is -58.80 mm. The initial moisture and the precipitation decrease allowing to the increase of evapotranspiration. The minimum values are present in the aquifer center area, whereas the average and maximum values are present in the rest of the aquifer.(<b>d</b>) In December, the minimum recharge is −9.35 and the average is 0.99 mm, with both values predominating throughout the rea; whereas, the 57.81 mm maximum is only present in small portions of the center and to the south of the aquifer.</p>
Full article ">Figure 8
<p>Finally, the annual natural recharge was obtained by adding all previous months, with the value for the average recharge being 27.27 mm, the minimum of −34.20 mm, and the maximum of 137.76 mm. The mean and maximum values are observed in the center, north, and southwest of the Chupaderos aquifer. The deficit or negative values are present in the southeast.</p>
Full article ">
13 pages, 1557 KiB  
Article
A Study of the Effects of Wetland Degradation on Soil-Microbial-Extracellular Enzyme Carbon, Nitrogen, and Phosphorus and Their Ecological Stoichiometry
by Ye Li, Jiuwang Jin, Shuangyi Li, Shuhao Xia and Jianbing Wei
Agronomy 2024, 14(12), 3008; https://doi.org/10.3390/agronomy14123008 - 18 Dec 2024
Viewed by 253
Abstract
Due to the unique geographic location of A’er Xiang, there is a natural landscape where sandy land and lake-marsh wetlands coexist. However, the wetland degradation caused by the disturbance of anthropogenic activities has led to the change in land use. In this study, [...] Read more.
Due to the unique geographic location of A’er Xiang, there is a natural landscape where sandy land and lake-marsh wetlands coexist. However, the wetland degradation caused by the disturbance of anthropogenic activities has led to the change in land use. In this study, the spatial-temporal substitution method was used to select five sample plots: the original wetland converted to forest land for reuse area of five years and ten years; the original wetland converted to cropland for reuse area of five years and ten years; and the native wetland. It aims to investigate the variations in carbon, nitrogen, and phosphorus and their stoichiometric characteristics of soil-microorganisms-extracellular enzymes before and after reuse, and to analyze potential interactions among these elements. The results indicated that following wetlands degradation, changes in land use for five years did not significantly affect the content of soil organic carbon (TOC), total nitrogen (TN), or total phosphorus (TP). However, after ten years, both TOC and TN, except for TP, decreased significantly. Microbial biomass carbon (MBC) and microbial biomass nitrogen (MBN) contents in cropland were consistently higher than those in WL, showing a trend of first increasing and then decreasing with longer conversion periods. In contrast, forest land values were lower than in WL and increased as the conversion period lengthened. The microbial biomass phosphorus (MBP) content was ranked across the five sample sites as follows: 10 CL > 5 CL > 5 FL > 10 FL > WL. β-1,4-glucosidase (BG) activity was significantly increased after conversion to forest land and significantly decreased after conversion to cropland. β-1,4-N-glucosidase (NAG) and L-leucine aminopeptidase (LAP) activities were ranked as follows among the five sites: 5 FL > WL > 5 CL > 10 FL > 10 CL. Phosphatase (PHOS) activity showed no significant changes post-conversion, though it was consistently lower compared to WL. Full article
(This article belongs to the Section Soil and Plant Nutrition)
Show Figures

Figure 1

Figure 1
<p>Variation characteristics of soil C, N, and P contents among different land use types. Note: lowercase letters denote significant differences (<span class="html-italic">p</span> &lt; 0.05). The fertilizer treatment abbreviations are defined in Introduction.</p>
Full article ">Figure 2
<p>Variation characteristics of soil MBC, MBN, and MBP contents across different land use types. Note: lowercase letters denote significant differences (<span class="html-italic">p</span> &lt; 0.05). The fertilizer treatment abbreviations are defined in Introduction.</p>
Full article ">Figure 3
<p>Variation characteristics of soil extracellular enzyme activity cross different land use types. Note: lowercase letters denote significant differences (<span class="html-italic">p</span> &lt; 0.05). The fertilizer treatment abbreviations are defined in Introduction.</p>
Full article ">Figure 4
<p>Correlation between Soil Microbial Extracellular Enzyme Carbon, Nitrogen, and Phosphorus Content and Its Stoichiometric Ratio. Note: * indicates a significant difference at the 0.05 level; ** indicates a significant difference at the 0.01 level; *** indicates a significant difference at the 0.001 level.</p>
Full article ">
20 pages, 4591 KiB  
Article
“From Waste to Wonder”: Comparative Evaluation of Chinese Cabbage Waste and Banana Peel Derived Hydrogels on Soil Water Retention Performance
by Yufan Xie, Yuan Zhong, Jun Wu, Shiwei Fang, Liqun Cai, Minjun Li, Jun Cao, Hejie Zhao and Bo Dong
Gels 2024, 10(12), 833; https://doi.org/10.3390/gels10120833 - 18 Dec 2024
Viewed by 287
Abstract
Under the increasing severity of drought issues and the urgent need for the resourceful utilization of agricultural waste, this study aimed to compare the soil water retention properties of hydrogels prepared from Chinese cabbage waste (CW) and banana peel (BP) using grafting techniques [...] Read more.
Under the increasing severity of drought issues and the urgent need for the resourceful utilization of agricultural waste, this study aimed to compare the soil water retention properties of hydrogels prepared from Chinese cabbage waste (CW) and banana peel (BP) using grafting techniques with acrylic acid (AA) and acrylamide (AAm). Free radical polymerization was initiated with ammonium persulfate (APS), and N, N′-methylene bisacrylamide (MBA) served as the crosslinking agent to fabricate the grafted polymer hydrogels. The hydrogels were subjected to detailed evaluations of their water absorption, reusability, and water retention capabilities through indoor experiments. The optimal hydrogel was identified and its applicability in wheat seedling growth was assessed. The findings revealed that the CW-gel, with an equilibrium swelling ratio of 551.8 g/g in ultrapure water, demonstrated remarkable performance and sustained a high water retention of 57.6% even after drying, which was markedly superior to that of the BP-gel. The CW-gel with the best comprehensive properties significantly improved water retention in sandy soil by 78.2% and prolonged the retention time by five days, indicating its potential for long-term irrigation management. In contrast, the BP-gel showed better performance in clay soil, with an increased water-holding capacity of 43.3%. The application of a 1.5% CW-gel concentration under drought stress significantly improved wheat seedling growth, highlighting the role of hydrogels in agriculture and providing a new path for sustainable water resource management in dryland farming. Full article
(This article belongs to the Special Issue Gel-Based Adsorbent Materials for Environmental Remediation)
Show Figures

Figure 1

Figure 1
<p>Synthetic Route of Cross-linked (AA-AAm) Copolymers as Water Super-absorbent Hydrogels.</p>
Full article ">Figure 2
<p>FTIR spectral characterization of (a) CW, (b) BP, (c) CK, (d) BP-(AA-AAm) gel, and (e) CW-(AA-AAm) gel. The term “CK” denotes a hydrogel that has been prepared without incorporating any agricultural waste materials, serving as a control in our experiments to isolate the effects of the added waste components.</p>
Full article ">Figure 3
<p>Comparative Analysis of Relative Peak Areas for C-O, COOH, and OH Groups in Waste Materials (CW, BP) and Hydrogels (CK, CW-gel, BP-gel). In the bar graph, letters (a–d) indicate the degree of significant differences among the groups represented by each bar, with “a” denoting the group with the highest level of significance, followed by “b”, “c”, and “d” representing groups with decreasing levels of significance.</p>
Full article ">Figure 4
<p>Surface characteristics of (<b>a</b>) CW, (<b>b</b>) BP, (<b>c</b>,<b>d</b>) CK, (<b>e</b>) CW-(AA-AAm) gel, and (<b>f</b>) BP-(AA-AAm) gel.</p>
Full article ">Figure 5
<p>(<b>a</b>) Swelling capacity of CK, CW-(AA-AAm) gel, and BP-(AA-AAm) gel at different times; (<b>b</b>) Swelling capacity of CW-(AA-AAm) gel under different treatments; (<b>c</b>) Swelling capacity of BP-(AA-AAm) gel under different treatments. In the bar graph, letters (a–f) indicate the degree of significant differences among the groups represented by each bar, with “a” denoting the group with the highest level of significance, followed by “b”, “c”, “d”, “e” and “f” representing groups with decreasing levels of significance.</p>
Full article ">Figure 6
<p>Water absorption curves for CW-(AA-AAm), BP-(AA-AAm), and CK gels at different pH conditions.</p>
Full article ">Figure 7
<p>Water retention capacity of various hydrogels under different treatments at room temperature.</p>
Full article ">Figure 8
<p>Reuse properties of various hydrogels under different treatments at room temperature. In the bar graph, letters (a–f) indicate the degree of significant differences among the groups represented by each bar, with “a” denoting the group with the highest level of significance, followed by “b”, “c”, “d”, “e” and “f” representing groups with decreasing levels of significance.</p>
Full article ">Figure 9
<p>(<b>a</b>) Water-holding capacity of CK, CW-(AA-AAm) gel and BP-(AA-AAm) gel added at 0.6% in different soils; (<b>b</b>–<b>d</b>) Water retention of CK, CW-(AA-AAm) gel and BP-(AA-AAm) gel in different soils. In the bar graph, letters (a–c) indicate the degree of significant differences among the groups represented by each bar, with “a” denoting the group with the highest level of significance, followed by “b” and “c” representing groups with decreasing levels of significance.</p>
Full article ">Figure 10
<p>(<b>a</b>) Growth of wheat seedlings on day 4 under water restriction; (<b>b</b>)Plant height of wheat after cessation of growth at different hydrogel concentrations (0.0% to 3.0%); (<b>c</b>,<b>d</b>) Mean weight and height for varying hydrogel concentrations. In the bar graph, letters (a–e) indicate the degree of significant differences among the groups represented by each bar, with “a” denoting the group with the highest level of significance, followed by “b”, “c”, “d” and “e” representing groups with decreasing levels of significance.</p>
Full article ">Figure 11
<p>The process of CW-(AA-AAm) gel and BP-(AA-AAm) gel synthesis.</p>
Full article ">
21 pages, 4073 KiB  
Article
Date Palm Waste-Derived Biochar for Improving Hydrological Properties of Sandy Soil Under Saturated and Unsaturated Conditions
by Abdulaziz G. Alghamdi, Abdulrasoul Alomran, Hesham M. Ibrahim, Arafat Alkhasha and Zafer Alasmary
Sustainability 2024, 16(24), 11081; https://doi.org/10.3390/su162411081 - 17 Dec 2024
Viewed by 520
Abstract
Water conservation and effective irrigation management are vital for sustainable agriculture in arid regions. While organic soil amendments have been widely used to enhance water retention in sandy soils, research on the use of date palm waste-derived biochar remains limited. Thus, this study [...] Read more.
Water conservation and effective irrigation management are vital for sustainable agriculture in arid regions. While organic soil amendments have been widely used to enhance water retention in sandy soils, research on the use of date palm waste-derived biochar remains limited. Thus, this study aimed to explore the innovative application of biochar produced from date palm waste, focusing on its effects on the hydrological properties of sandy soil. Biochars of varying particle sizes (0.5, 1, and 2 mm) and pyrolysis temperatures (300 °C, 450 °C, and 600 °C) were produced and their impacts were assessed under both saturated and unsaturated conditions on soil hydrological properties. The biochar was incorporated into soil columns at application rates of 0%, 1%, 3%, and 5% (w/w) within a 10 cm layer on top of 35 cm deep soil columns. The soil columns were placed vertically into water basins for saturation. Evaporation, infiltration, and saturated hydraulic conductivity were measured. The findings revealed that the application of 1%, 3%, and 5% biochar significantly increased soil water retention by 36.80%, 34.18%, and 29.66%, while cumulative evaporation decreased by 7.30%, 2.00%, and 1.35%, respectively, as compared to the control. Water retained at the end of the experiment was increased by 100.63%, 112.29%, and 101.68%, while unsaturated hydraulic conductivity decreased by 21.27%, 26.15%, and 26.17% after amending the soil with 1%, 3%, and 5% biochar, respectively, as compared to the control. The water retention ranged between 30.34 and 42.51%, 22.59 and 43.20%, and 22.48 and 38.81% for biochar produced at 300 °C, 450 °C, and 600 °C, respectively. Water infiltration rate and pore size was decreased with the increased pyrolysis temperature. Overall, the application rates of 3% and 5% with particle sizes of 1 and 0.5 mm and low pyrolysis temperature were most efficient for improving soil properties such as water retention, reducing unsaturated hydraulic conductivity, reducing the rate and volume of infiltration, and enhancing the micro-porosity reduction of sandy soils. In a nutshell, this study highlights the potential of date palm waste-derived biochar as an effective soil amendment, significantly enhancing water retention by up to 112.29% and reducing evaporation. By optimizing irrigation management in sandy soils, these findings contribute to more sustainable agricultural practices. Full article
(This article belongs to the Section Soil Conservation and Sustainability)
Show Figures

Figure 1

Figure 1
<p>A schematic for demonstrating the soil layer with biochar on top of the soil in the treated columns.</p>
Full article ">Figure 2
<p>Effect of pyrolytic temperature on cumulative evaporation after the application of date palm-derived biochar produced at 300 °C (T300) with particle sizes of 1–2 mm, 0.5–1.0 mm, and less than 0.5 mm (P2, P1, and P0.5, respectively), and applied at 1%, 3%, and 5% (R1, R3, and R5, respectively), with (<b>a</b>) showing cumulative evaporation from day 1 to 45, (<b>b</b>) showing cumulative evaporation from day 1 to 6, and (<b>c</b>) showing cumulative evaporation from day 37 to 41. (CK: Control, T1: T<sub>300</sub>R<sub>1</sub>P<sub>2</sub>, T2: T<sub>300</sub>R<sub>3</sub>P<sub>2</sub>, T3: T<sub>300</sub>R<sub>5</sub>P<sub>2</sub>, T4: T<sub>300</sub>R<sub>1</sub>P<sub>1</sub>, T5: T<sub>300</sub>R<sub>3</sub>P<sub>1</sub>, T6: T<sub>300</sub>R<sub>5</sub>P<sub>1</sub>, T7: T<sub>300</sub>R<sub>1</sub>P<sub>0.5</sub>, T8: T<sub>300</sub>R<sub>3</sub>P<sub>0.5</sub>, and T9: T<sub>300</sub>R<sub>5</sub>P<sub>0.5</sub>).</p>
Full article ">Figure 3
<p>Effect of pyrolytic temperature on cumulative evaporation after the application of date palm-derived biochar produced at 300 °C (T300) with particle sizes of 1–2 mm, 0.5–1.0 mm, and less than 0.5 mm (P2, P1, and P0.5, respectively), and applied at 1%, 3%, and 5% (R1, R3, and R5, respectively), with (<b>a</b>) showing cumulative evaporation from day 1 to 45, (<b>b</b>) showing cumulative evaporation from day 1 to 6, and (<b>c</b>) showing cumulative evaporation from day 37 to 41. (CK: Control, T10: T<sub>450</sub>R<sub>1</sub>P<sub>2</sub>, T11: T<sub>450</sub>R<sub>3</sub>P<sub>2</sub>, T12: T<sub>450</sub>R<sub>5</sub>P<sub>2</sub>, T13: T<sub>450</sub>R<sub>1</sub>P<sub>1</sub>, T14: T<sub>450</sub>R<sub>3</sub>P<sub>1</sub>, T15: T<sub>450</sub>R<sub>5</sub>P<sub>1</sub>, T16: T<sub>450</sub>R<sub>1</sub>P<sub>0.5</sub>, T17: T<sub>450</sub>R<sub>3</sub>P<sub>0.5</sub>, and T18: T<sub>450</sub>R<sub>5</sub>P<sub>0.5</sub>).</p>
Full article ">Figure 4
<p>Effect of pyrolytic temperature on cumulative evaporation after the application of date palm-derived biochar produced at 300 °C (T300) with particle sizes of 1–2 mm, 0.5–1.0 mm, and less than 0.5 mm (P2, P1, and P0.5, respectively), and applied at 1%, 3%, and 5% (R1, R3, and R5, respectively), with (<b>a</b>) showing cumulative evaporation from day 1 to 45, (<b>b</b>) showing cumulative evaporation from day 1 to 6, and (<b>c</b>) showing cumulative evaporation from day 37 to 41. (CK: Control, T19: T<sub>600</sub>R<sub>1</sub>P<sub>2</sub>, T20: T<sub>600</sub>R<sub>3</sub>P<sub>2</sub>, T21: T<sub>600</sub>R<sub>5</sub>P<sub>2</sub>, T22: T<sub>600</sub>R<sub>1</sub>P<sub>1</sub>, T23: T<sub>600</sub>R<sub>3</sub>P<sub>1</sub>, T24: T<sub>600</sub>R<sub>5</sub>P<sub>1</sub>, T25: T<sub>600</sub>R<sub>1</sub>P<sub>0.5</sub>, T26: T<sub>600</sub>R<sub>3</sub>P<sub>0.5</sub>, and T27: T<sub>600</sub>R<sub>5</sub>P<sub>0.5</sub>).</p>
Full article ">Figure 5
<p>Effect of pyrolytic temperature on cumulative infiltration before wetting after the application of date palm-derived biochar produced at 300 °C (T<sub>300</sub>), 450 °C (T<sub>450</sub>), and 600 °C (T<sub>600</sub>) with particle sizes of 1–2 mm, 0.5–1.0 mm, and less than 0.5 mm (P<sub>2</sub>, P<sub>1</sub>, and P<sub>0.5</sub>, respectively), and applied at 1%, 3%, and 5% (R<sub>1</sub>, R<sub>3</sub>, and R<sub>5,</sub> respectively). Panel (<b>a</b>) shows the plot of cumulative infiltration vs. time, while (<b>b</b>) shows the plot of cumulative infiltration vs. sq. time for treatments T1 to T9. Panel (<b>c</b>) shows the plot of cumulative infiltration vs. time, while (<b>d</b>) shows the plot of cumulative infiltration vs. sq. time for treatments T10 to T18. Panel (<b>e</b>) shows the plot of cumulative infiltration vs. time, while (<b>f</b>) shows the plot of cumulative infiltration vs. sq. time for treatments T19 to T27. (CK: Control, T1: T<sub>300</sub>R<sub>1</sub>P<sub>2</sub>, T2: T<sub>300</sub>R<sub>3</sub>P<sub>2</sub>, T3: T<sub>300</sub>R<sub>5</sub>P<sub>2</sub>, T4: T<sub>300</sub>R<sub>1</sub>P<sub>1</sub>, T5: T<sub>300</sub>R<sub>3</sub>P<sub>1</sub>, T6: T<sub>300</sub>R<sub>5</sub>P<sub>1</sub>, T7: T<sub>300</sub>R<sub>1</sub>P<sub>0.5</sub>, T8: T<sub>300</sub>R<sub>3</sub>P<sub>0.5</sub>, T9: T<sub>300</sub>R<sub>5</sub>P<sub>0.5</sub>, T10: T<sub>450</sub>R<sub>1</sub>P<sub>2</sub>, T11: T<sub>450</sub>R<sub>3</sub>P<sub>2</sub>, T12: T<sub>450</sub>R<sub>5</sub>P<sub>2</sub>, T13: T<sub>450</sub>R<sub>1</sub>P<sub>1</sub>, T14: T<sub>450</sub>R<sub>3</sub>P<sub>1</sub>, T15: T<sub>450</sub>R<sub>5</sub>P<sub>1</sub>, T16: T<sub>450</sub>R<sub>1</sub>P<sub>0.5</sub>, T17: T<sub>450</sub>R<sub>3</sub>P<sub>0.5</sub>, T18: T<sub>450</sub>R<sub>5</sub>P<sub>0.5</sub>, T19: T<sub>600</sub>R<sub>1</sub>P<sub>2</sub>, T20: T<sub>600</sub>R<sub>3</sub>P<sub>2</sub>, T21: T<sub>600</sub>R<sub>5</sub>P<sub>2</sub>, T22: T<sub>600</sub>R<sub>1</sub>P<sub>1</sub>, T23: T<sub>600</sub>R<sub>3</sub>P<sub>1</sub>, T24: T<sub>600</sub>R<sub>5</sub>P<sub>1</sub>, T25: T<sub>600</sub>R<sub>1</sub>P<sub>0.5</sub>, T26: T<sub>600</sub>R<sub>3</sub>P<sub>0.5</sub>, and T27: T<sub>600</sub>R<sub>5</sub>P<sub>0.5</sub>).</p>
Full article ">Figure 6
<p>Effect of pyrolytic temperature on infiltration rate before wetting after the application of date palm-derived biochar produced at 300 °C (T<sub>300</sub>), 450 °C (T<sub>450</sub>), and 600 °C (T<sub>600</sub>) with particle sizes of 1–2 mm, 0.5–1.0 mm, and less than 0.5 mm (P<sub>2</sub>, P<sub>1</sub>, and P<sub>0.5</sub>, respectively), and applied at 1%, 3%, and 5% (R<sub>1</sub>, R<sub>3</sub>, and R<sub>5,</sub> respectively). Panels (<b>a</b>,<b>b</b>) show the effects of treatments T1 to T9 on the infiltration rate, panels (<b>c</b>,<b>d</b>) show the effects of treatments T10 to T18 on the infiltration rate, and panels (<b>e</b>,<b>f</b>) show the effects of treatments T19 to T27 on the infiltration rate (CK: Control, T1: T<sub>300</sub>R<sub>1</sub>P<sub>2</sub>, T2: T<sub>300</sub>R<sub>3</sub>P<sub>2</sub>, T3: T<sub>300</sub>R<sub>5</sub>P<sub>2</sub>, T4: T<sub>300</sub>R<sub>1</sub>P<sub>1</sub>, T5: T<sub>300</sub>R<sub>3</sub>P<sub>1</sub>, T6: T<sub>300</sub>R<sub>5</sub>P<sub>1</sub>, T7: T<sub>300</sub>R<sub>1</sub>P<sub>0.5</sub>, T8: T<sub>300</sub>R<sub>3</sub>P<sub>0.5</sub>, T9: T<sub>300</sub>R<sub>5</sub>P<sub>0.5</sub>, T10: T<sub>450</sub>R<sub>1</sub>P<sub>2</sub>, T11: T<sub>450</sub>R<sub>3</sub>P<sub>2</sub>, T12: T<sub>450</sub>R<sub>5</sub>P<sub>2</sub>, T13: T<sub>450</sub>R<sub>1</sub>P<sub>1</sub>, T14: T<sub>450</sub>R<sub>3</sub>P<sub>1</sub>, T15: T<sub>450</sub>R<sub>5</sub>P<sub>1</sub>, T16: T<sub>450</sub>R<sub>1</sub>P<sub>0.5</sub>, T17: T<sub>450</sub>R<sub>3</sub>P<sub>0.5</sub>, T18: T<sub>450</sub>R<sub>5</sub>P<sub>0.5</sub>, T19: T<sub>600</sub>R<sub>1</sub>P<sub>2</sub>, T20: T<sub>600</sub>R<sub>3</sub>P<sub>2</sub>, T21: T<sub>600</sub>R<sub>5</sub>P<sub>2</sub>, T22: T<sub>600</sub>R<sub>1</sub>P<sub>1</sub>, T23: T<sub>600</sub>R<sub>3</sub>P<sub>1</sub>, T24: T<sub>600</sub>R<sub>5</sub>P<sub>1</sub>, T25: T<sub>600</sub>R<sub>1</sub>P<sub>0.5</sub>, T26: T<sub>600</sub>R<sub>3</sub>P<sub>0.5</sub>, and T27: T<sub>600</sub>R<sub>5</sub>P<sub>0.5</sub>).</p>
Full article ">Figure 7
<p>Effect of pyrolytic temperature on cumulative infiltration after wetting after the application of date palm-derived biochar produced at 300 °C (T<sub>300</sub>), 450 °C (T<sub>450</sub>), and 600 °C (T<sub>600</sub>) with particle sizes of 1–2 mm, 0.5–1.0 mm, and less than 0.5 mm (P<sub>2</sub>, P<sub>1</sub>, and P<sub>0.5</sub>, respectively), and applied at 1%, 3%, and 5% (R<sub>1</sub>, R<sub>3</sub>, and R<sub>5,</sub> respectively). Panels (<b>a</b>,<b>b</b>) show the effects of treatments T1 to T9 on cumulative infiltration, panels (<b>c</b>,<b>d</b>) show the effects of treatments T10 to T18 on cumulative infiltration, and panels (<b>e</b>,<b>f</b>) show the effects of treatments T19 to T27 on cumulative infiltration (CK: Control, T1: T<sub>300</sub>R<sub>1</sub>P<sub>2</sub>, T2: T<sub>300</sub>R<sub>3</sub>P<sub>2</sub>, T3: T<sub>300</sub>R<sub>5</sub>P<sub>2</sub>, T4: T<sub>300</sub>R<sub>1</sub>P<sub>1</sub>, T5: T<sub>300</sub>R<sub>3</sub>P<sub>1</sub>, T6: T<sub>300</sub>R<sub>5</sub>P<sub>1</sub>, T7: T<sub>300</sub>R<sub>1</sub>P<sub>0.5</sub>, T8: T<sub>300</sub>R<sub>3</sub>P<sub>0.5</sub>, T9: T<sub>300</sub>R<sub>5</sub>P<sub>0.5</sub>, T10: T<sub>450</sub>R<sub>1</sub>P<sub>2</sub>, T11: T<sub>450</sub>R<sub>3</sub>P<sub>2</sub>, T12: T<sub>450</sub>R<sub>5</sub>P<sub>2</sub>, T13: T<sub>450</sub>R<sub>1</sub>P<sub>1</sub>, T14: T<sub>450</sub>R<sub>3</sub>P<sub>1</sub>, T15: T<sub>450</sub>R<sub>5</sub>P<sub>1</sub>, T16: T<sub>450</sub>R<sub>1</sub>P<sub>0.5</sub>, T17: T<sub>450</sub>R<sub>3</sub>P<sub>0.5</sub>, T18: T<sub>450</sub>R<sub>5</sub>P<sub>0.5</sub>, T19: T<sub>600</sub>R<sub>1</sub>P<sub>2</sub>, T20: T<sub>600</sub>R<sub>3</sub>P<sub>2</sub>, T21: T<sub>600</sub>R<sub>5</sub>P<sub>2</sub>, T22: T<sub>600</sub>R<sub>1</sub>P<sub>1</sub>, T23: T<sub>600</sub>R<sub>3</sub>P<sub>1</sub>, T24: T<sub>600</sub>R<sub>5</sub>P<sub>1</sub>, T25: T<sub>600</sub>R<sub>1</sub>P<sub>0.5</sub>, T26: T<sub>600</sub>R<sub>3</sub>P<sub>0.5</sub>, and T27: T<sub>600</sub>R<sub>5</sub>P<sub>0.5</sub>).</p>
Full article ">Figure 8
<p>Effect of pyrolytic temperature on infiltration rate after wetting after the application of date palm-derived biochar produced at 300 °C (T<sub>300</sub>), 450 °C (T<sub>450</sub>), and 600 °C (T<sub>600</sub>) with particle sizes of 1–2 mm, 0.5–1.0 mm, and less than 0.5 mm (P<sub>2</sub>, P<sub>1</sub>, and P<sub>0.5</sub>, respectively), and applied at 1%, 3%, and 5% (R<sub>1</sub>, R<sub>3</sub>, and R<sub>5,</sub> respectively). Panels (<b>a</b>,<b>b</b>) show the effects of treatments T1 to T9 on the infiltration rate, panels (<b>c</b>,<b>d</b>) show the effects of treatments T10 to T18 on the infiltration rate, and panels (<b>e</b>,<b>f</b>) show the effects of treatments T19 to T27 on the infiltration rate (CK: Control, T1: T<sub>300</sub>R<sub>1</sub>P<sub>2</sub>, T2: T<sub>300</sub>R<sub>3</sub>P<sub>2</sub>, T3: T<sub>300</sub>R<sub>5</sub>P<sub>2</sub>, T4: T<sub>300</sub>R<sub>1</sub>P<sub>1</sub>, T5: T<sub>300</sub>R<sub>3</sub>P<sub>1</sub>, T6: T<sub>300</sub>R<sub>5</sub>P<sub>1</sub>, T7: T<sub>300</sub>R<sub>1</sub>P<sub>0.5</sub>, T8: T<sub>300</sub>R<sub>3</sub>P<sub>0.5</sub>, T9: T<sub>300</sub>R<sub>5</sub>P<sub>0.5</sub>, T10: T<sub>450</sub>R<sub>1</sub>P<sub>2</sub>, T11: T<sub>450</sub>R<sub>3</sub>P<sub>2</sub>, T12: T<sub>450</sub>R<sub>5</sub>P<sub>2</sub>, T13: T<sub>450</sub>R<sub>1</sub>P<sub>1</sub>, T14: T<sub>450</sub>R<sub>3</sub>P<sub>1</sub>, T15: T<sub>450</sub>R<sub>5</sub>P<sub>1</sub>, T16: T<sub>450</sub>R<sub>1</sub>P<sub>0.5</sub>, T17: T<sub>450</sub>R<sub>3</sub>P<sub>0.5</sub>, T18: T<sub>450</sub>R<sub>5</sub>P<sub>0.5</sub>, T19: T<sub>600</sub>R<sub>1</sub>P<sub>2</sub>, T20: T<sub>600</sub>R<sub>3</sub>P<sub>2</sub>, T21: T<sub>600</sub>R<sub>5</sub>P<sub>2</sub>, T22: T<sub>600</sub>R<sub>1</sub>P<sub>1</sub>, T23: T<sub>600</sub>R<sub>3</sub>P<sub>1</sub>, T24: T<sub>600</sub>R<sub>5</sub>P<sub>1</sub>, T25: T<sub>600</sub>R<sub>1</sub>P<sub>0.5</sub>, T26: T<sub>600</sub>R<sub>3</sub>P<sub>0.5</sub>, and T27: T<sub>600</sub>R<sub>5</sub>P<sub>0.5</sub>).</p>
Full article ">Figure 9
<p>Impact of pyrolytic temperature on hydraulic conductivity upon wetness following the application of biochar made from date palms at 300 °C (T<sub>300</sub>), 450 °C (T<sub>450</sub>), and 600 °C (T<sub>600</sub>), with particle sizes of 1–2 mm, 0.5–1.0 mm, and less than 0.5 mm (P<sub>2</sub>, P<sub>1</sub>, and P<sub>0.5</sub>, respectively), and applied at 1%, 3%, and 5% (R<sub>1</sub>, R<sub>3</sub>, and R<sub>5</sub>, respectively). (CK: Control, T1: T<sub>300</sub>R<sub>1</sub>P<sub>2</sub>, T2: T<sub>300</sub>R<sub>3</sub>P<sub>2</sub>, T3: T<sub>300</sub>R<sub>5</sub>P<sub>2</sub>, T4: T<sub>300</sub>R<sub>1</sub>P<sub>1</sub>, T5: T<sub>300</sub>R<sub>3</sub>P<sub>1</sub>, T6: T<sub>300</sub>R<sub>5</sub>P<sub>1</sub>, T7: T<sub>300</sub>R<sub>1</sub>P<sub>0.5</sub>, T8: T<sub>300</sub>R<sub>3</sub>P<sub>0.5</sub>, T9: T<sub>300</sub>R<sub>5</sub>P<sub>0.5</sub>, T10: T<sub>450</sub>R<sub>1</sub>P<sub>2</sub>, T11: T<sub>450</sub>R<sub>3</sub>P<sub>2</sub>, T12: T<sub>450</sub>R<sub>5</sub>P<sub>2</sub>, T13: T<sub>450</sub>R<sub>1</sub>P<sub>1</sub>, T14: T<sub>450</sub>R<sub>3</sub>P<sub>1</sub>, T15: T<sub>450</sub>R<sub>5</sub>P<sub>1</sub>, T16: T<sub>450</sub>R<sub>1</sub>P<sub>0.5</sub>, T17: T<sub>450</sub>R<sub>3</sub>P<sub>0.5</sub>, T18: T<sub>450</sub>R<sub>5</sub>P<sub>0.5</sub>, T19: T<sub>600</sub>R<sub>1</sub>P<sub>2</sub>, T20: T<sub>600</sub>R<sub>3</sub>P<sub>2</sub>, T21: T<sub>600</sub>R<sub>5</sub>P<sub>2</sub>, T22: T<sub>600</sub>R<sub>1</sub>P<sub>1</sub>, T23: T<sub>600</sub>R<sub>3</sub>P<sub>1</sub>, T24: T<sub>600</sub>R<sub>5</sub>P<sub>1</sub>, T25: T<sub>600</sub>R<sub>1</sub>P<sub>0.5</sub>, T26: T<sub>600</sub>R<sub>3</sub>P<sub>0.5</sub>, and T27: T<sub>600</sub>R<sub>5</sub>P<sub>0.5</sub>).</p>
Full article ">Scheme 1
<p>Representation of the transformation of date palm waste into biochar via pyrolysis.</p>
Full article ">
16 pages, 3229 KiB  
Article
Analysis of CH4 and N2O Fluxes in the Dry Season: Influence of Soils and Vegetation Types in the Pantanal
by Gabriela Cugler, Viviane Figueiredo, Vincent Gauci, Tainá Stauffer, Roberta Bittencourt Peixoto, Sunitha Rao Pangala and Alex Enrich-Prast
Forests 2024, 15(12), 2224; https://doi.org/10.3390/f15122224 - 17 Dec 2024
Viewed by 338
Abstract
This study examines CH4 and N2O fluxes during the dry season in two distinct areas of the Pantanal: Barranco Alto Farm (BAF), dominated by grasslands, and Passo da Lontra (PL), a forested region. As climate change increases the occurrence of [...] Read more.
This study examines CH4 and N2O fluxes during the dry season in two distinct areas of the Pantanal: Barranco Alto Farm (BAF), dominated by grasslands, and Passo da Lontra (PL), a forested region. As climate change increases the occurrence of droughts, understanding greenhouse gas (GHG) fluxes in tropical wetlands during dry periods is crucial. Using static chambers, CH4 and N2O emissions were measured from soils and tree stems in both regions, with additional measurements from grass in BAF. Contrary to expectations, PL—characterized by clayey soils—had sandy mud samples that retained less water, promoting oxic conditions and methane uptake, making it a CH4 sink. Meanwhile, BAF’s sandy, well-drained soils exhibited minimal CH4 fluxes, with negligible methane uptake or emissions. N2O fluxes were generally higher in BAF, particularly from tree stems, indicating significant interactions between soil type, moisture, and vegetation. These findings highlight the pivotal roles of soil texture and aeration in GHG emissions, suggesting that well-drained, sandy soils in tropical wetlands may not always enhance methane oxidation. This underscores the importance of continuous GHG monitoring in the Pantanal to refine climate change mitigation strategies. Full article
(This article belongs to the Section Forest Meteorology and Climate Change)
Show Figures

Figure 1

Figure 1
<p>Location of Pantanal sampling sites. (<b>A</b>) The top-left map highlights the Pantanal biome (grey) within Brazil’s borders. (<b>B</b>) A zoomed-in view of the southern Pantanal shows the sampling sites: Passo da Lontra (PL, triangle) in the Miranda microregion and Barranco Alto Farm (BAF, circle) in the Aquidauana microregion. (<b>C</b>) A detailed map of the PL site near Medalha Lake and the Rio Miranda. (<b>D</b>) A detailed map of the BAF site near the Aquidauana River, with surrounding water bodies in light blue. The shapefiles for the Pantanal boundaries and hydrography were obtained from Terrabrasilis (INPE, 2023), while the map of Brazil and municipality boundaries were sourced from IBGE (2023).</p>
Full article ">Figure 2
<p>Photographs showing the chambers used to measure CH<sub>4</sub> and N<sub>2</sub>O fluxes at Fazenda Barranco Alto and Passo do Lontra. Opaque PVC static chambers were used for measuring fluxes from grass and soil, while semi-rigid static chambers were used for tree stem measurements. Source: Photographs are taken by collaborators Pernilha Eriksson and Louise Larsson and are the property of the research group.</p>
Full article ">Figure 3
<p>Box plot illustrating CH<sub>4</sub> fluxes (µg C-CH<sub>4</sub> m<sup>−2</sup> d<sup>−1</sup>) measured across compartments and sites. The BAF site includes CH<sub>4</sub> emissions from tree stems, soil, and grass, while the PL site includes emissions from tree stems and soil. Each box represents the interquartile range (IQR), with whiskers extending to the minimum and maximum values, including the outliers (black circles). The Kolmogorov–Smirnov test indicates that the distribution of all data is nonparametric (<span class="html-italic">p</span> &lt; 0.05). Different letters represent statistically significant differences according to Kruskal–Wallis test with Dunn’s post hoc test (<span class="html-italic">p</span> &lt; 0.05).</p>
Full article ">Figure 4
<p>Box plot illustrating N<sub>2</sub>O fluxes (µg N-N<sub>2</sub>O m<sup>−2</sup> d<sup>−1</sup>) measured from tree steams, exposed soil, and grasses across PL and BAF study sites. The BAF site includes N<sub>2</sub>O emissions from tree stems, soil, and grass, while the PL site includes emissions from tree stems and soil. Each box represents the interquartile range (IQR), with whiskers extending to the minimum and maximum values, including the outliers (black circles). Letter (a) above the boxes represents no statistically significant differences according to the Kruskal–Wallis test with Dunn’s post hoc test (<span class="html-italic">p</span> &lt; 0.05).</p>
Full article ">Figure 5
<p>Boxplots illustrating CH<sub>4</sub> and N<sub>2</sub>O fluxes at Passo da Lontra (PL) and Barranco Alto Farm (BAF) across three areas (Area 1: closest to the lake, Area 3: furthest). Panels (<b>A</b>,<b>B</b>) depict CH<sub>4</sub> fluxes, while panels (<b>C</b>,<b>D</b>) show N<sub>2</sub>O fluxes. Each box represents the interquartile range (IQR), with whiskers extending to minimum and maximum non-outlier values. The letter (a) above the boxes represents no statistically significant differences according to the Kruskal–Wallis test with Dunn’s post hoc test (<span class="html-italic">p</span> &lt; 0.05).</p>
Full article ">Figure 6
<p>Relationship between tree stem diameter (cm) and GHG fluxes. (<b>A</b>) Represent the CH<sub>4</sub> (μg CH<sub>4</sub> m<sup>−2</sup> d<sup>−1</sup>). (<b>B</b>) Represent the N<sub>2</sub>O (μg N<sub>2</sub>O m<sup>−2</sup> d<sup>−1</sup>). The blue lines show the non-parametric trend (LOWESS) of fluxes with increasing stem diameter.</p>
Full article ">
15 pages, 2104 KiB  
Article
Estimating Tetrachloroethene Sorption Coefficients Based on Soil Properties in Organic-Poor Soils
by Veronika Rippelová, Lenka McGachy, Josef Janků and Jiří Kroužek
Appl. Sci. 2024, 14(24), 11761; https://doi.org/10.3390/app142411761 - 17 Dec 2024
Viewed by 303
Abstract
In the context of contaminated site remediation, the fate of chlorinated solvents in the subsurface and subsequent groundwater contamination is influenced by soil properties governing sorption. The solid–water distribution coefficient (Kd) is a key parameter for modeling contaminant distribution and [...] Read more.
In the context of contaminated site remediation, the fate of chlorinated solvents in the subsurface and subsequent groundwater contamination is influenced by soil properties governing sorption. The solid–water distribution coefficient (Kd) is a key parameter for modeling contaminant distribution and transport, essential for risk assessment and remediation planning. This study evaluated tetrachloroethene sorption isotherms in 34 low-organic-carbon soils from the Czech Republic, assessing the influence of soil properties on Kd. Soil samples exhibited variability in organic carbon content (˂0.05–0.81%), with clay ranging from 0% to 64.9%, silt 5.1% to 71.2%, and sand 5.2% to 88.9%, specific surface area (0.41–64.39 m2 g−1), particle density (2.05–4.09 g cm−3), and porosity (43.5–67.3%). Batch experiments were conducted using standard procedures, with Kd values ranging from 0.379 to 2.272 L kg−1. Statistical analysis grouped the soils into three textural classes: sandy, clayey fine, and silty loam. The findings reveal that organic carbon content and specific surface area are the primary predictors of Kd, while clay and sand also play a significant role in shaping sorption behavior. Multivariate regression models explained 63.6% to 98.5% of Kd variability with high accuracy, as indicated by low root means square error (0.070–0.329) and mean absolute percentage error (3.8–28.8%) values. These models offer reliable predictions of sorption behavior, providing valuable tools for risk assessment and remediation strategies. Full article
(This article belongs to the Section Environmental Sciences)
Show Figures

Figure 1

Figure 1
<p><b>Summary of Pearson’s correlation coefficients and corresponding <span class="html-italic">p</span>-values.</b> The heatmap displays the Pearson’s correlation coefficients for all studied parameters, with positive correlations shown in red and negative correlations in blue. The coefficients range from −1 to 1, where −1 indicates a perfect negative linear relationship, 1 indicates a perfect positive linear relationship, and 0 signifies no linear relationship between the variables.</p>
Full article ">Figure 2
<p>Biplot of PC1 and PC2 axes (63.77% variance explained): points represent 34 soil samples, vectors represent seven variables (reps. <span class="html-italic">K</span><sub>d</sub> and six soil properties).</p>
Full article ">Figure 3
<p>Soil texture triangles: (<b>A</b>) the relative composition of tested soil samples, (<b>B</b>) three soil texture classes identified through AHC analysis.</p>
Full article ">Figure 4
<p>Correlation of loadings and score plot with confidence ellipses: (<b>A</b>) the loading plot represents the correlation between the soil properties in the classes and the discriminant functions, (<b>B</b>) the score plot displays soil samples, and their position indicates their score on the discriminant functions. The confidence ellipses (95%) visualize the separation between groups and the variability within each group.</p>
Full article ">Figure 5
<p>Comparison of the measured and predicted <span class="html-italic">K</span><sub>d</sub> values of used samples using the multivariate linear regression models for Classes 1, 2 and 3.</p>
Full article ">
20 pages, 13662 KiB  
Article
Unmanned Aerial Vehicle (UAV) Hyperspectral Imagery Mining to Identify New Spectral Indices for Predicting the Field-Scale Yield of Spring Maize
by Yue Zhang, Yansong Wang, Hang Hao, Ziqi Li, Yumei Long, Xingyu Zhang and Chenzhen Xia
Sustainability 2024, 16(24), 10916; https://doi.org/10.3390/su162410916 - 12 Dec 2024
Viewed by 675
Abstract
A nondestructive approach for accurate crop yield prediction at the field scale is vital for precision agriculture. Considerable progress has been made in the use of the spectral index (SI) derived from unmanned aerial vehicle (UAV) hyperspectral images to predict crop yields before [...] Read more.
A nondestructive approach for accurate crop yield prediction at the field scale is vital for precision agriculture. Considerable progress has been made in the use of the spectral index (SI) derived from unmanned aerial vehicle (UAV) hyperspectral images to predict crop yields before harvest. However, few studies have explored the most sensitive wavelengths and SIs for crop yield prediction, especially for different nitrogen fertilization levels and soil types. This study aimed to investigate the appropriate wavelengths and their combinations to explore the ability of new SIs derived from UAV hyperspectral images to predict yields during the growing season of spring maize. In this study, the hyperspectral canopy reflectance measurement method, a field-based high-throughput method, was evaluated in three field experiments (Wang-Jia-Qiao (WJQ), San-Ke-Shu (SKS), and Fu-Jia-Jie (FJJ)) since 2009 with different soil types (alluvial soil, black soil, and aeolian sandy soil) and various nitrogen (N) fertilization levels (0, 168, 240, 270, and 312 kg/ha) in Lishu County, Northeast China. The measurements of canopy spectral reflectance and maize yield were conducted at critical growth stages of spring maize, including the jointing, silking, and maturity stages, in 2019 and 2020. The best wavelengths and new SIs, including the difference spectral index, ratio spectral index, and normalized difference spectral index forms, were obtained from the contour maps constructed by the coefficient of determination (R2) from the linear regression models between the yield and all possible SIs screened from the 450 to 950 nm wavelengths. The new SIs and eight selected published SIs were subsequently used to predict maize yield via linear regression models. The results showed that (1) the most sensitive wavelengths were 640–714 nm at WJQ, 450–650 nm and 750–950 nm at SKS, and 450–700 nm and 750–950 nm at FJJ; (2) the new SIs established here were different across the three experimental fields, and their performance in maize yield prediction was generally better than that of the published SIs; and (3) the new SIs presented different responses to various N fertilization levels. This study demonstrates the potential of exploring new spectral characteristics from remote sensing technology for predicting the field-scale crop yield in spring maize cropping systems before harvest. Full article
Show Figures

Figure 1

Figure 1
<p>Location of the study area (<b>a</b>), UAV hyperspectral images (<b>b</b>–<b>d</b>) and the nitrogen application rates (<b>e</b>) of three experimental fields (WJQ, SKS, and FJJ).</p>
Full article ">Figure 2
<p>Mean canopy reflectance spectra curves of spring maize under different N treatments across three growth stages in the three experimental fields. (<b>a</b>): WJQ, (<b>b</b>): SKS, (<b>c</b>): FJJ.</p>
Full article ">Figure 3
<p>Contour maps for the linear model between the difference spectral index (DSI), ratio spectral index (RSI), normalized difference spectral index (NDSI), and maize yield for the WJQ experimental field. (<b>a</b>–<b>c</b>): DSI, RSI, and NDSI forms at the jointing stage; (<b>d</b>–<b>f</b>): DSI, RSI, and NDSI forms at the silking stage; (<b>g</b>–<b>i</b>): DSI, RSI, and NDSI forms at the maturity stage.</p>
Full article ">Figure 4
<p>Contour maps for the linear model between the difference spectral index (DSI), ratio spectral index (RSI), normalized difference spectral index (NDSI), and maize yield for the SKS experimental field. (<b>a</b>–<b>c</b>): DSI, RSI, and NDSI forms at the jointing stage; (<b>d</b>–<b>f</b>): DSI, RSI, and NDSI forms at the silking stage; (<b>g</b>–<b>i</b>): DSI, RSI, and NDSI forms at the maturity stage.</p>
Full article ">Figure 5
<p>Contour maps for the linear model between the difference spectral index (DSI), ratio spectral index (RSI), normalized difference spectral index (NDSI), and maize yield for the FJJ experimental field. (<b>a</b>–<b>c</b>): DSI, RSI, and NDSI forms at the jointing stage; (<b>d</b>–<b>f</b>): DSI, RSI, and NDSI forms at the silking stage; (<b>g</b>–<b>i</b>): DSI, RSI, and NDSI forms at the maturity stage.</p>
Full article ">Figure 6
<p>Scatter plots of the measured yield (kg/ha) versus the yield (kg/ha) predicted by the new SIs: (<b>a</b>) NDSI (690, 710) at WJQ, (<b>b</b>) RSI (906, 546) at SKS, and (<b>c</b>) DSI (698, 922) at FJJ.</p>
Full article ">Figure 7
<p>The response of the maize yield to different N application rates on the three experimental fields.</p>
Full article ">Figure 8
<p>The response of the new SIs to different N treatments on the three experimental fields. (<b>a</b>−<b>c</b>): DSI, RSI, and NDSI forms for WJQ; (<b>d</b>−<b>f</b>): DSI, RSI, and NDSI forms for SKS; and (<b>g</b>−<b>i</b>): DSI, RSI, and NDSI forms for FJJ, respectively.</p>
Full article ">Figure 8 Cont.
<p>The response of the new SIs to different N treatments on the three experimental fields. (<b>a</b>−<b>c</b>): DSI, RSI, and NDSI forms for WJQ; (<b>d</b>−<b>f</b>): DSI, RSI, and NDSI forms for SKS; and (<b>g</b>−<b>i</b>): DSI, RSI, and NDSI forms for FJJ, respectively.</p>
Full article ">Figure 8 Cont.
<p>The response of the new SIs to different N treatments on the three experimental fields. (<b>a</b>−<b>c</b>): DSI, RSI, and NDSI forms for WJQ; (<b>d</b>−<b>f</b>): DSI, RSI, and NDSI forms for SKS; and (<b>g</b>−<b>i</b>): DSI, RSI, and NDSI forms for FJJ, respectively.</p>
Full article ">
19 pages, 3731 KiB  
Article
Soil and Site Productivity Effects on Above- and Belowground Radiata Pine Carbon Pools at Harvesting Age
by Daniel Bozo, Rafael Rubilar, Otávio Camargo Campoe, Rosa M. Alzamora, Juan Pedro Elissetche, Juan Carlos Valverde, Roberto Pizarro, Matías Pincheira, Juan Carlos Valencia and Claudia Sanhueza
Plants 2024, 13(24), 3482; https://doi.org/10.3390/plants13243482 (registering DOI) - 12 Dec 2024
Viewed by 366
Abstract
Pinus radiata D. Don is the most widely planted forest species in Chile, making it crucial to understand carbon pools in adult plantations. This study aimed to evaluate the effect of soil type and site productivity on the total carbon stock in adult [...] Read more.
Pinus radiata D. Don is the most widely planted forest species in Chile, making it crucial to understand carbon pools in adult plantations. This study aimed to evaluate the effect of soil type and site productivity on the total carbon stock in adult radiata pine plantations, considering sites with contrasting water and nutrient availability. We selected 10 sites with sandy and recent volcanic ash soils, representing a productivity gradient. At each site, three 1000 m2 plots were established to quantify the carbon stock of total biomass using allometric equations and in situ carbon assessments of the forest floor and mineral soil (up to 1 m deep). The results indicated significantly higher carbon stocks in the mineral soil of recent ash sites (281.4 Mg ha⁻1) compared to sandy soils (139.9 Mg ha⁻1). The total site carbon was also higher in recent ash (473.2 Mg ha⁻1) than in sandy sites (330.9 Mg ha⁻1). A significant relationship was found between stand productivity and soil organic carbon (r2 = 0.88), as well as total carbon stock (r2 = 0.91) when considering soil type. These findings highlight the importance of including assessments up to 1 m depth and developing soil type and productivity models to improve site carbon stock estimates. Full article
Show Figures

Figure 1

Figure 1
<p>Aboveground biomass carbon stock (AGBC) and belowground biomass carbon stock (BGBC) at each site by soil type and cumulative over bark stand volume at harvesting age. The dashed lines represent the average total biomass carbon stock for sandy and recent volcanic ash soil sites. Error bars indicate standard deviations for each site (n = 3).</p>
Full article ">Figure 2
<p>(<b>A</b>) Soil carbon stock up to 1 m depth; and (<b>B</b>) proportion of carbon for each soil depth, at each site by soil type and cumulative over bark stand volume at harvesting age. The dashed lines represent the average values of soil organic carbon stock for sandy and recent volcanic ash soil sites. In (<b>A</b>), differences between soil type means are indicated by lowercase letters and error bars represent standard deviations for each site (n = 3).</p>
Full article ">Figure 3
<p>(<b>A</b>) Relationship between site productivity (cumulative over bark stand volume at harvesting age, VOL) and organic carbon stock in the mineral soil (up to 1 m deep) (SOC) using soil type as the dummy variable; and (<b>B</b>) relationship between observed SOC and predicted SOC estimated using the dummy variable regression adjusted model.</p>
Full article ">Figure 4
<p>(<b>A</b>) Forest floor carbon stock in organic horizons and coarse woody debris; and (<b>B</b>) proportion of carbon stock in forest floor and coarse woody debris at each site by soil type and cumulative over bark stand volume at harvesting age. The dashed lines represent the average value of forest floor carbon stock for sandy and recent volcanic ash soil sites. In (<b>A</b>), differences between soil type means are indicated by lowercase letters and error bars represent standard deviations for each site (n = 3).</p>
Full article ">Figure 5
<p>(<b>A</b>) Total carbon stock for soil organic carbon (SOC), forest floor carbon (FFC), belowground biomass (BGBC), and aboveground biomass (ABGC); and (<b>B</b>) proportion of total site carbon stock at each site by soil type and cumulative over bark stand volume at harvesting age. The dashed lines represent the average value of total carbon stock for sandy and recent volcanic ash soil sites. In (<b>A</b>), differences between soil type means are indicated by lowercase letters and error bars represent standard deviations for each site (n = 3).</p>
Full article ">Figure 6
<p>(<b>A</b>) Regression models of the relationship between cumulative over bark stand volume at harvesting age (VOL) and total site carbon stock (TCS), considering soil type as a dummy variable; and (<b>B</b>) relationship between observed and predicted TCS using the dummy variable model.</p>
Full article ">Figure 7
<p>(<b>a</b>) Study area in Central South Chile, (<b>b</b>) Study area and site locations’ mean summer (January to March) temperature (°C), (<b>c</b>) Study area and site locations’ mean annual rainfall (mm yr<sup>−1</sup>) (site code name is presented in <a href="#plants-13-03482-t005" class="html-table">Table 5</a>).</p>
Full article ">
17 pages, 1870 KiB  
Article
Bioaccumulation of Cr by the Buddleja Species and Schinus molle L. Grown with and Without Compost in a Sandy Soil Contaminated by Leather Industrial Effluents
by Jamilet Huarsaya-Huillca, Sheyla Callo-Sánchez, Camila Aguilar-Ccuno, Oswaldo Rodríguez-Salazar, Danny Tupayachy-Quispe, Giuliana Romero-Mariscal, Zulema Hachire-Patiño and Jonathan Almirón
Plants 2024, 13(24), 3469; https://doi.org/10.3390/plants13243469 - 11 Dec 2024
Viewed by 352
Abstract
This research aimed to assess the bioaccumulation capacity of the Buddleja species and Schinus molle L. using organic amendments to the phytoremediation of total chromium in the mid-zone of the Añashuayco Ravine, Uchumayo, Arequipa, impacted by tanneries from the Rio Seco Industrial Park. [...] Read more.
This research aimed to assess the bioaccumulation capacity of the Buddleja species and Schinus molle L. using organic amendments to the phytoremediation of total chromium in the mid-zone of the Añashuayco Ravine, Uchumayo, Arequipa, impacted by tanneries from the Rio Seco Industrial Park. Additionally, it analyzed total chromium concentrations, soil physicochemical properties, and morphological changes in plants with and without organic matter. Samples of the Buddleja species and Schinus molle L. were distributed into groups with and without compost, along with control groups. They were monitored over 6 months, every 60 days, showing significant morphological variations. The results highlight an important finding: the remarkable bioaccumulation capacity of the species studied all exceeded 30%. The samples without compost showed a lower percentage of total chromium bioaccumulation in plants compared to the samples with the organic amendment. The Buddleja species demonstrated a 39.01% chromium bioaccumulation with compost compared to 37.99% without it. Likewise, Schinus molle L. achieved 33.99% chromium accumulation with compost and 31.84% without it. These findings emphasize the superior ability of these species to bioaccumulate heavy metals, highlighting that the Buddleja species has mayor bioaccumulation capacity and more remotion of total chromium in the soil. Full article
(This article belongs to the Section Plant–Soil Interactions)
Show Figures

Figure 1

Figure 1
<p>Location of the monitoring point in the evaluated area. Source: Own elaboration using Google Earth.</p>
Full article ">Figure 2
<p>Plants tested.</p>
Full article ">Figure 3
<p>pH and conductivity of the sampled soil during experimentation (0 days and 180 days).</p>
Full article ">Figure 4
<p>Growth of species during experimentation. The black lines indicate the value of size of each subgroup, whose averages are found in <a href="#plants-13-03469-t004" class="html-table">Table 4</a>.</p>
Full article ">Figure 5
<p>Comparison of % bioaccumulation of the species at the end of the evaluation.</p>
Full article ">
11 pages, 8372 KiB  
Article
A Rapid Evaluation Method of Permafrost Bearing Capacity in the Tibetan Plateau Region Based on the Correlation Between CPT-CBR
by Haowu Wang, Bo Tian, Lei Quan, Panpan Zhang, Lihui Li, Yitong Hou and Sen Hu
Appl. Sci. 2024, 14(23), 11439; https://doi.org/10.3390/app142311439 - 9 Dec 2024
Viewed by 461
Abstract
Permafrost, as a soil type under unique environmental conditions, has bearing characteristics that are highly susceptible to thermo-hydraulic environments. Rapid evaluation of the bearing characteristics of in situ permafrost at various depths in perennially frozen regions is a critical scientific issue urgently needing [...] Read more.
Permafrost, as a soil type under unique environmental conditions, has bearing characteristics that are highly susceptible to thermo-hydraulic environments. Rapid evaluation of the bearing characteristics of in situ permafrost at various depths in perennially frozen regions is a critical scientific issue urgently needing resolution in the road design and construction sectors in China. To address this, this study investigates the correlation between CPT parameters and laboratory mechanical indices under the combined effects of multiple factors in frozen sandy soils. By conducting both CPT and CBR tests on frozen sandy soils, the study analyzes the trends in changes in cone tip resistance (qc) and CBR values under the influence of temperature (T), moisture content (ω), and compaction degree (K) and establishes a functional relationship between them. Based on the standard requirements for indoor CBR, an evaluation criterion using qc for assessing the bearing capacity of frozen sandy soil is proposed. The results indicate that both CBR values and qc increase initially and then stabilize as K increases. With decreasing temperature, both indices stabilize after an initial increase, with turning points at −3.1 °C for CBR values and −2.5 °C for qc. As ω increases, both indices first increase and then stabilize, with a turning point at 40%ω. There is a robust linear relationship between the CBR values and qc, with the ratio of predicted CBR values to actual values showing a histogram and log-normal distribution accounting for 81% and 51.3%, respectively, within a 20% accuracy level, indicating good predictive performance. Referring to the highway subgrade specifications for indoor CBR, a standard for evaluating the bearing capacity of frozen sandy soils using CPT technology is proposed. This study provides new insights for geological surveys in perennially frozen regions and a theoretical basis for the application of CPT technology in evaluating the bearing capacity of permafrost. Full article
Show Figures

Figure 1

Figure 1
<p>Experimental procedures for CBR and CPT.</p>
Full article ">Figure 2
<p>Variation in soil sample CBR values with temperature and moisture content: (<b>a</b>) variation in CBR values with temperature for a sample with 40% moisture content; (<b>b</b>) variation in CBR values with moisture content for a sample at −2.1 °C.</p>
Full article ">Figure 3
<p>Variation in soil sample <span class="html-italic">q</span><sub>c</sub> with temperature and moisture content: (<b>a</b>) variation in <span class="html-italic">q</span><sub>c</sub> with temperature for a sample with 40% moisture content; (<b>b</b>) variation in <span class="html-italic">q</span><sub>c</sub> with moisture content for a sample at −2.1 °C.</p>
Full article ">Figure 4
<p>Comparison of soil sample CBR Values and <span class="html-italic">q</span><sub>c</sub>: (<b>a</b>) comparison of CBR values and <span class="html-italic">q</span><sub>c</sub> for a sample with 40% moisture content; (<b>b</b>) comparison of CBR values and <span class="html-italic">q</span><sub>c</sub> at −2.1 °C.</p>
Full article ">Figure 5
<p>Fit between <span class="html-italic">q</span><sub>c</sub> and CBR values. The * in the figure represents the multiplication symbol.</p>
Full article ">Figure 6
<p>Histogram and log-normal distribution of <span class="html-italic">CBR</span>p versus <span class="html-italic">CBR</span>.</p>
Full article ">
14 pages, 11343 KiB  
Article
Study of the Shear Strength Model of Unsaturated Soil in the Benggang Area of Southern China
by Maojin Yang, Nanbo Cen, Zumei Wang, Bifei Huang, Jinshi Lin, Fangshi Jiang, Yanhe Huang and Yue Zhang
Water 2024, 16(23), 3528; https://doi.org/10.3390/w16233528 - 7 Dec 2024
Viewed by 687
Abstract
Benggangs are a unique type of soil erosion commonly found in southern China, with the gully wall being the most dynamic component of the Benggang system and is crucial for assessing its overall progression. The unsaturated shear strength of soil in Benggang areas [...] Read more.
Benggangs are a unique type of soil erosion commonly found in southern China, with the gully wall being the most dynamic component of the Benggang system and is crucial for assessing its overall progression. The unsaturated shear strength of soil in Benggang areas is a key factor influencing the stability of the gully wall. However, quantitative analyses of the unsaturated shear strength in the gully walls of Benggangs remain limited. In this study, the soil–water characteristic curves (SWCC) and shear strengths of undisturbed soil samples from four different soil layers in the gully wall of Benggang were measured using a pressure membrane meter and a quadruple direct shear apparatus. The results revealed that the water holding capacity of the soil decreased gradually with increasing matrix suction, and the order of the water holding capacity was the sandy soil layer > transition layer > laterite layer > clastic layer. With an increasing soil water content (SWC), the shear strength, cohesion (c), and internal friction angle (φ) of the four soil layers decreased significantly, and the φ showed a power function decreasing curve (p < 0.05), whereas c in the laterite layer and transition layer exhibited a power function decreasing curve (p < 0.01). The c of the sandy soil layer and clastic layer decreased linearly and logarithmically (p < 0.01) with increasing SWC, respectively. The unsaturated shear strength model for the four soil layers was developed based on the Vanapalli model. The root mean square error (RMSE) of the simulated and measured values was less than 29.349, while the Nash–Sutcliffe efficiency (NSE) and R2 values were greater than 0.638 and 0.788, respectively. The model can be used to analyze and predict the unsaturated shear strength in different layers of Benggang gully walls, providing a theoretical foundation for studying the erosion mechanisms of Benggangs. Full article
(This article belongs to the Section Soil and Water)
Show Figures

Figure 1

Figure 1
<p>The related map of the study area includes (<b>a</b>) a map of the locations of sampling points; (<b>b</b>) a drone image of the Benggang; and (<b>c</b>) a simplified diagram showing the division of soil layers at the sampling point.</p>
Full article ">Figure 2
<p>SWCC test equipment.</p>
Full article ">Figure 3
<p>Samples from quadruple direct shear and standard circular ring cutter 1.</p>
Full article ">Figure 4
<p>SWCC of different soil layers of the Benggang gully wall.</p>
Full article ">Figure 5
<p>Relationships between the soil shear strength and normal stress in the various soil layers of the Benggang gully wall under different SWC conditions. Note: (<b>a</b>–<b>d</b>) denote the laterite layer, transition layer, sandy soil layer, and clastic layer, respectively.* indicates a significant correlation (<span class="html-italic">p</span> &lt; 0.05); ** indicates a highly significant correlation (<span class="html-italic">p</span> &lt; 0.01).</p>
Full article ">Figure 6
<p>Fitted curves of the SWC versus <span class="html-italic">c</span> (<b>A</b>) and angle of <span class="html-italic">φ</span> (<b>B</b>) for different soil layers of the Benggang gully wall. Note: a–d denote the laterite layer, transition layer, sandy soil layer, and clastic layer, respectively. * indicates a significant correlation (<span class="html-italic">p</span> &lt; 0.05); ** indicates a highly significant correlation (<span class="html-italic">p</span> &lt; 0.01).</p>
Full article ">Figure 7
<p>Comparison of the measured values from this experiment with the values predicted by Vanapalli’s (1996) [<a href="#B23-water-16-03528" class="html-bibr">23</a>] model. Note: (<b>a</b>–<b>d</b>) denote the laterite layer, transition layer, sandy soil layer, and clastic layer, respectively.</p>
Full article ">
15 pages, 3488 KiB  
Article
Components of High-Yielding Cotton Grown in Rain-Fed Conditions in the Brazilian Cerrado
by Fábio R. Echer, Leonardo V. Galdi, Gustavo R. A. Silva, Jorge W. S. Santos, Caroline H. Rocha, Camila P. Cagna, Cássio A. Tormena, Igor F. Silva and Ricardo Atarassi
Agronomy 2024, 14(12), 2920; https://doi.org/10.3390/agronomy14122920 - 6 Dec 2024
Viewed by 501
Abstract
Brazil leads globally in achieving high lint yields for rain-fed cotton in large-scale fields, with about 92% of its cotton area unirrigated. This study hypothesized that cotton could achieve high yields when favorable climate conditions and management practices favor high fruit load. The [...] Read more.
Brazil leads globally in achieving high lint yields for rain-fed cotton in large-scale fields, with about 92% of its cotton area unirrigated. This study hypothesized that cotton could achieve high yields when favorable climate conditions and management practices favor high fruit load. The objective was to analyze the impact of these factors on cotton yields by examining two commercial fields in Brazil in the same climatic zone (Aw, Koppen)—one in Sapezal (SPZ) and the other in Riachão das Neves (RN). The SPZ field (cv. TMG 47B2RF) spanned 20 hectares, while the RN field (cv. FM 974GLT) covered 90 hectares. The soils of both fields were classified as oxisols, with SPZ possessing a clayey texture and RN a sandy loam texture. The findings indicate that the high lint cotton yields—3111 kg·ha⁻1 in SPZ and 3239 kg·ha⁻1 in RN—were achieved through a combination of ideal weather conditions, high-quality soil, and effective management practices, which favored boll retention, and an optimal plant architecture with short stature (<1.1 m), 19–22 nodes, and ~165 bolls m−2. Boll weights averaged 1.85–1.91 g of lint, and fruit retention rates were 61.6% in SPZ and 66.2% in RN. The study reveals a significant yield gap compared to Brazil’s average lint cotton yield (~1900 kg·ha⁻1) and other high-yield commercial fields (~3500–3900 kg·ha⁻1 of lint). The results underscore that bridging this gap—ranging from 1200 to 2000 kg·ha⁻1—could enhance the sustainability of cotton farming in Brazil by maximizing existing cultivated areas. Ultimately, the insights from this study highlight the role of combining climate suitability, management practices, and soil quality improvement to achieve higher cotton productivity and reduce environmental pressures from agricultural expansion. Full article
(This article belongs to the Section Farming Sustainability)
Show Figures

Figure 1

Figure 1
<p>Brazilian historic cotton area, production, and lint yield. Source: [<a href="#B2-agronomy-14-02920" class="html-bibr">2</a>]. Abbreviations: mi = million; ha = hectares.</p>
Full article ">Figure 2
<p>Daily rainfall, solar radiation and maximum and minimum air temperatures in Sapezal, MT, and Riachão das Neves, BA, Brazil, during 2021/2022 season and historical data.</p>
Full article ">Figure 3
<p>Effective daily temperature (degree days) and vapor pressure deficit (VPD) recorded during the 2021/2022 season and the historical data in Sapezal, MT, and Riachão das Neves, BA, Brazil.</p>
Full article ">Figure 4
<p>Overview of the commercial fields evaluated in Sapezal (<b>top</b>) and Riachão das Neves (<b>bottom</b>).</p>
Full article ">Figure 5
<p>Yield accumulation per node and per plant in Sapezal, MT (<b>a</b>) and Riachão das Neves, BA (<b>b</b>), Brazil. Yield accumulation is the result of the sum of fruit positions (P1, P2, and P3+) from each node multiplied by plant density.</p>
Full article ">Figure 6
<p>Percentage of boll retention and contribution to yield from bolls of first, second, and third position in a high-yielding rainfed field from Sapezal and Riachão das Neves, Brazil.</p>
Full article ">
25 pages, 18819 KiB  
Article
Integrating Geosynthetics and Vegetation for Sustainable Erosion Control Applications
by Tatiana Olinic, Ernest-Daniel Olinic and Ana-Cornelia Butcaru
Sustainability 2024, 16(23), 10621; https://doi.org/10.3390/su162310621 - 4 Dec 2024
Viewed by 642
Abstract
The stability of slopes is a critical challenge in various civil engineering projects, such as embankments, cut-slopes, landfills, dams, transportation infrastructure, and riverbank restoration. Stabilizing slopes using bioengineering methods is a sustainable approach that limits the negative impact of engineering works; such methods [...] Read more.
The stability of slopes is a critical challenge in various civil engineering projects, such as embankments, cut-slopes, landfills, dams, transportation infrastructure, and riverbank restoration. Stabilizing slopes using bioengineering methods is a sustainable approach that limits the negative impact of engineering works; such methods should be implemented and adopted worldwide. Geosynthetic materials and plant roots are sustainable for preventing erosion and surface landslides. The plants used for this paper are known to have beneficial effects on erosion control, namely Festuca arundinaceous, Dactylis glomerata, Phleum pratensis, Trifolium pratense, and Trifolium repens. Using vegetation as a bio-reinforcement method is often more cost effective and environmentally friendly than traditional engineering solutions, making a more sustainable engineering solution for shallow slope stabilization applications. The paper presents the erosion process that occurred on sandy slopes protected by organic soil layers and geosynthetic materials under rainfall simulation in scaled model tests. Full article
(This article belongs to the Section Environmental Sustainability and Applications)
Show Figures

Figure 1

Figure 1
<p>The geosynthetic materials used for this study: (<b>a</b>) GEC 1, (<b>b</b>) GEC 2, and (<b>c</b>) GEC 3.</p>
Full article ">Figure 2
<p>Grain size distribution (blue line) and the histogram (red line) of the sand sample.</p>
Full article ">Figure 3
<p>The distribution of the topsoil layer in the cylindrical containers to determine the optimum OS thickness: (<b>a</b>) 0 cm OS, (<b>b</b>) 5 cm OS, (<b>c</b>) 10 cm OS, (<b>d</b>) 15 cm OS, and (<b>e</b>) 20 cm OS.</p>
Full article ">Figure 4
<p>The direct shear methodology: (<b>a</b>) the sample of 20 cm OS with living vegetation, (<b>b</b>) sheared sample at the interface between OS and sand with roots, (<b>c</b>) the Shearmatic automatic direct/residual shear machine, (<b>d</b>) sheared samples in the oven, (<b>e</b>) sample of OS with roots sheared, and (<b>f</b>) sample taken from the upper part of the cylinder.</p>
Full article ">Figure 5
<p>Scaled model device [<a href="#B26-sustainability-16-10621" class="html-bibr">26</a>]: (<b>a</b>,<b>a’</b>) sketch of the rainfall simulator at the upper part, (<b>b</b>) sketch of the erosion control chamber with a slope of 2:3 (V:H), (<b>c</b>,<b>c’</b>) image of the rainfall simulator at the upper part, (<b>d</b>) image of the erosion control chamber with an artificial slope of 2:3 (V:H) realized by compacted sand (<b>e</b>) sketch of the erosion control chamber with the dimensions of the artificial slope protected by a 5 cm OS layer placed in steps, and (<b>f</b>) image of the erosion control chamber with an artificial slope protected by OS and mature vegetation.</p>
Full article ">Figure 6
<p>The meteorological data: (<b>a</b>) the variations in the highest, average, and lowest temperatures recorded in May, June, July, and August 2023, (<b>b</b>) the variations in the precipitation recorded from 1 May 2023 to 1 September 2023, and (<b>c</b>) the variations in highest, average, and lowest daily temperatures.</p>
Full article ">Figure 7
<p>The growing plants’ stages at different periods: (<b>a</b>) 30 September 2022 (day 0), (<b>b</b>) 25 October 2022 (25 days), (<b>c</b>) 19 November 2022 (50 days), (<b>d</b>) 14 December 2022 (75 days), and (<b>e</b>) 27 February 2023 (150 days).</p>
Full article ">Figure 8
<p>The comparison of the influence of the OS layer thickness on root length (mm) measured (<b>a</b>) manually, and (<b>b</b>) with WinRHIZO.</p>
Full article ">Figure 9
<p>The comparison of the influence of the OS layer thickness on root volume (cm<sup>3</sup>) measured (<b>a</b>) manually, and (<b>b</b>) with WinRHIZO.</p>
Full article ">Figure 10
<p>Variations in shear stress vs. normal stress (<b>left</b>) and shear strength vs. horizontal displacement (<b>right</b>) on soil/soil-root samples [<a href="#B37-sustainability-16-10621" class="html-bibr">37</a>].</p>
Full article ">Figure 10 Cont.
<p>Variations in shear stress vs. normal stress (<b>left</b>) and shear strength vs. horizontal displacement (<b>right</b>) on soil/soil-root samples [<a href="#B37-sustainability-16-10621" class="html-bibr">37</a>].</p>
Full article ">Figure 11
<p>The variations in shear stress vs. normal stress on all analyzed samples: (<b>a</b>) sandy samples, (<b>b</b>) OS samples, and (<b>c</b>) samples collected from the interface between OS and sand [<a href="#B37-sustainability-16-10621" class="html-bibr">37</a>].</p>
Full article ">Figure 12
<p>Variations in the profile of the unprotected sandy slope during a rainfall simulation for different periods [<a href="#B26-sustainability-16-10621" class="html-bibr">26</a>]: (<b>a</b>) t = 0 min, (<b>b</b>) t = 10 min, (<b>c</b>) t = 20 min, and (<b>d</b>) t = 30 min.</p>
Full article ">Figure 13
<p>The variations in the profile of a sandy excavation unprotected and protected with GEC1 during rainfall simulation for different periods [<a href="#B26-sustainability-16-10621" class="html-bibr">26</a>]: (<b>a</b>) t = 0 min, (<b>b</b>) t = 10 min, (<b>c</b>) t = 20 min, and (<b>d</b>) t = 30 min.</p>
Full article ">Figure 14
<p>The variations in the profile of a sandy excavation unprotected and protected with GEC2 during rainfall simulation for different periods [<a href="#B26-sustainability-16-10621" class="html-bibr">26</a>]: (<b>a</b>) t = 0 min, (<b>b</b>) t = 10 min, (<b>c</b>) t = 20 min, and (<b>d</b>) t = 30 min.</p>
Full article ">Figure 15
<p>The variations in the profile of a sandy excavation unprotected and protected with GEC3 during rainfall simulation for different periods [<a href="#B26-sustainability-16-10621" class="html-bibr">26</a>]: (<b>a</b>) t = 0 min, (<b>b</b>) t = 10 min, (<b>c</b>) t = 20 min, and (<b>d</b>) t = 30 min.</p>
Full article ">Figure 16
<p>The variations in the profile of a sandy excavation protected by 0.5 cm of OS with immature vegetation during rainfall simulation for different periods [<a href="#B26-sustainability-16-10621" class="html-bibr">26</a>]: (<b>a</b>) t = 0 min, (<b>b</b>) t = 10 min, (<b>c</b>) t = 20 min, and (<b>d</b>) t = 30 min.</p>
Full article ">Figure 17
<p>The variations in the profile of a sandy excavation protected by 5 cm of OS (with seeds) during rainfall simulation for different periods: (<b>a</b>) t = 0 min, (<b>b</b>) t = 10 min, and (<b>c</b>) after approx. four months, during the winter.</p>
Full article ">Figure 18
<p>The sandy slope protected by 5 cm OS layer after seeding (1 May 2023): (<b>a</b>) slope protected by 5 cm OS, (<b>b</b>) slope protected by 5 cm OS and GEC 1, (<b>c</b>) slope protected by 5 cm OS and GEC 2, and (<b>d</b>) slope protected by 5 cm OS and GEC 3.</p>
Full article ">Figure 19
<p>The sandy slope protected by a 5 cm OS layer and mature vegetation after 45 days of seeding (15 June 2023): (<b>a</b>) slope protected by 5 cm OS, (<b>b</b>) slope protected by 5 cm OS and GEC 1, (<b>c</b>) slope protected by 5 cm OS and GEC 2, and (<b>d</b>) slope protected by 5 cm OS and GEC 3.</p>
Full article ">Figure 20
<p>The variations in the profile of a sandy excavation protected by 5 cm of OS with trimmed mature vegetation during rainfall simulation for different periods: (<b>a</b>) t = 0 min, (<b>b</b>) t = 10 min, (<b>c</b>) t = 30 min and (<b>d</b>) t = 50 min.</p>
Full article ">Figure 21
<p>The variations in the profile of a sandy excavation protected by 5 cm of OS with dried mature vegetation during rainfall simulation for different periods: (<b>a</b>) t = 0 min, (<b>b</b>) t = 10 min, (<b>c</b>) t = 30 min and (<b>d</b>) t = 50 min.</p>
Full article ">Figure 22
<p>The variations in the profile of a sandy excavation protected by 5 cm of OS with dried mature vegetation during rainfall simulation for different periods: (<b>a</b>) t = 0 min, (<b>b</b>) t = 80 min, (<b>c</b>) t = 100 min and (<b>d</b>) t = 120 min.</p>
Full article ">Figure 23
<p>The variations in the profile of a sandy excavation protected by 5 cm of OS with dried mature vegetation and GEC 1 during rainfall simulation for different periods: (<b>a</b>) t = 0 min, (<b>b</b>) t = 10 min, (<b>c</b>) t = 30 min and (<b>d</b>) t = 50 min.</p>
Full article ">Figure 24
<p>The variations in the profile of a sandy excavation protected by 5 cm of OS with dried mature vegetation and GEC 2 during rainfall simulation for different periods: (<b>a</b>) t = 0 min, (<b>b</b>) t = 10 min, (<b>c</b>) t = 30 min and (<b>d</b>) t = 50 min.</p>
Full article ">Figure 25
<p>The variations in the profile of a sandy excavation protected by 5 cm of OS with dried mature vegetation and GEC 3 during rainfall simulation for different periods: (<b>a</b>) t = 0 min, (<b>b</b>) t = 10 min, (<b>c</b>) t = 30 min and (<b>d</b>) t = 50 min.</p>
Full article ">
Back to TopTop