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Search Results (533)

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Keywords = nitrous oxide emissions

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17 pages, 3498 KiB  
Review
Application of Google Earth Engine to Monitor Greenhouse Gases: A Review
by Damar David Wilson, Gebrekidan Worku Tefera and Ram L. Ray
Data 2025, 10(1), 8; https://doi.org/10.3390/data10010008 (registering DOI) - 11 Jan 2025
Viewed by 210
Abstract
Google Earth Engine (GEE) is a cloud-based platform revolutionizing geospatial analysis by providing access to vast satellite datasets and computational capabilities for monitoring environmental and societal issues. It incorporates machine learning (ML) techniques and algorithms as part of its tools for analyzing and [...] Read more.
Google Earth Engine (GEE) is a cloud-based platform revolutionizing geospatial analysis by providing access to vast satellite datasets and computational capabilities for monitoring environmental and societal issues. It incorporates machine learning (ML) techniques and algorithms as part of its tools for analyzing and processing large geospatial data. This review explores the diverse applications of GEE in monitoring and mitigating greenhouse gas emissions and uptakes. GEE is a cloud-based platform built on Google’s infrastructure for analyzing and visualizing large-scale geospatial datasets. It offers large datasets for monitoring greenhouse gas (GHG) emissions and understanding their environmental impact. By leveraging GEE’s capabilities, researchers have developed tools and algorithms to analyze remotely sensed data and accurately quantify GHG emissions and uptakes. This review examines progress and trends in GEE applications, focusing on monitoring carbon dioxide (CO2), methane (CH4), and nitrous oxide/nitrogen dioxide (N2O/NO2) emissions. It discusses the integration of GEE with different machine learning methods and the challenges and opportunities in optimizing algorithms and ensuring data interoperability. Furthermore, it highlights GEE’s role in pinpointing emission hotspots, as demonstrated in studies monitoring uptakes. By providing insights into GEE’s capabilities for precise monitoring and mapping of GHGs, this review aims to advance environmental research and decision-making processes in mitigating climate change. Full article
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<p>Conceptual framework of the study.</p>
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<p>Represents the number of published articles that apply GEE between 2017 and 2024. SC = Soil carbon.</p>
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<p>Visual representation of the number of GEE-related articles used in the review by countries between 2017 and2024.</p>
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<p>Spatial visualization of carbon monoxide (CO) concentrations over Houston, Texas using Sentinel-5P data in GEE. On the left, the GEE script processes the CO data by defining the Texas boundary, filtering the dataset for 2022, and calculating the mean CO concentration.</p>
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<p>Methane concentrations across Texas in 2022, mapped using GEE and Sentinel-5P satellite data. On the left, you can see the GEE code used to process and analyze the data, which includes defining Texas as the study area, setting the time period, and visualizing the results. On the right, the map highlights methane levels across the state using a color gradient (blue to red), where red indicates higher concentrations.</p>
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<p>The spatial distribution of nitrogen dioxide (NO<sub>2</sub>) concentrations over Texas, visualized using GEE and Sentinel-5P data. On the left, the GEE script processes NO<sub>2</sub> data by defining the Texas boundary, filtering the dataset for a specific date range (2022), and applying visualization parameters with a color gradient (blue to red) representing varying NO<sub>2</sub> levels. On the right, the map displays NO<sub>2</sub> concentrations across Texas, with notable hotspots in certain regions indicating higher emissions or pollution levels.</p>
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23 pages, 4273 KiB  
Review
Ammonia Combustion: Internal Combustion Engines and Gas Turbines
by Edith Flora Eyisse, Ebrahim Nadimi and Dawei Wu
Energies 2025, 18(1), 29; https://doi.org/10.3390/en18010029 - 25 Dec 2024
Viewed by 363
Abstract
The quest for renewable energy sources has resulted in alternative fuels like ammonia, which offer promising carbon-free fuel for combustion engines. Ammonia has been demonstrated to be a potential fuel for decarbonizing power generator, marine, and heavy-duty transport sectors. Ammonia’s infrastructure for transportation [...] Read more.
The quest for renewable energy sources has resulted in alternative fuels like ammonia, which offer promising carbon-free fuel for combustion engines. Ammonia has been demonstrated to be a potential fuel for decarbonizing power generator, marine, and heavy-duty transport sectors. Ammonia’s infrastructure for transportation has been established due to its widespread primary use in the agriculture sector. Ammonia has the potential to serve as a zero-carbon alternative fuel for internal combustion engines and gas turbines, given successful carbon-free synthesis and necessary modifications to legacy heat engines. While its storage characteristics surpass those of hydrogen, the intrinsic properties of ammonia pose challenges in ignition, flame propagation, and the emissions of nitrogen oxides (NOx) and nitrous oxide (N2O) during combustion in heat engines. Recent noteworthy efforts in academia and industry have been dedicated to developing innovative combustion strategies and enabling technologies for heat engines, aiming to enhance efficiency, fuel economy, and emissions. This paper provides an overview of the latest advancements in the combustion of neat or high-percentage ammonia, offering perspectives on the most promising technical solutions for gas turbines, spark ignition, and compression ignition engines. Full article
(This article belongs to the Section I1: Fuel)
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<p>Contributions to engine power and cylinder pressure, respectively [<a href="#B30-energies-18-00029" class="html-bibr">30</a>].</p>
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<p>In-cylinder pressure traces for a compression ratio of eight (<b>a</b>) and a compression ratio of ten (<b>b</b>) [<a href="#B37-energies-18-00029" class="html-bibr">37</a>].</p>
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<p>NOx, NH<sub>3</sub>, and N<sub>2</sub>O emissions from an SI engine [<a href="#B29-energies-18-00029" class="html-bibr">29</a>].</p>
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<p>Air-assisted prechamber TJI system [<a href="#B47-energies-18-00029" class="html-bibr">47</a>].</p>
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<p>GHG emissions of an ammonia/diesel-fuelled engine for various ammonia/diesel ratios [<a href="#B60-energies-18-00029" class="html-bibr">60</a>].</p>
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<p>Comparison of three fuels’ (ammonia, gasoline, and ethanol) spray shapes 1 ms after injection where the yellow sections correspond to the flash boiling [<a href="#B70-energies-18-00029" class="html-bibr">70</a>].</p>
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<p>Velocity field of the ammonia spray at different injection and chamber pressures [<a href="#B72-energies-18-00029" class="html-bibr">72</a>].</p>
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<p>The impact of a slight change in the orifice geometry and inner flashing, L/D = 11: (<b>a</b>) glass nozzle 9–2 with the reduced section and opening (Da,out = 0.19 mm, Da,min = 0.18 mm); (<b>b</b>) glass nozzle 9–3 with straight orifice after reduction (Db,out = Db,min = 0.18 mm); red represent the projected area for c and d: (<b>c</b>) enlarged image of (<b>a</b>); and (<b>d</b>) enlarged image of (<b>b</b>) [<a href="#B74-energies-18-00029" class="html-bibr">74</a>].</p>
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<p>The two-stage, rich/lean burner [<a href="#B79-energies-18-00029" class="html-bibr">79</a>].</p>
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<p>Measured NOx emissions vs. overall DCR [<a href="#B86-energies-18-00029" class="html-bibr">86</a>].</p>
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15 pages, 3137 KiB  
Article
Effects of Long-Term Nitrogen Fertilization on Nitrous Oxide Emission and Yield in Acidic Tea (Camellia sinensis L.) Plantation Soils
by Fuying Jiang, Yunni Chang, Jiabao Han, Xiangde Yang and Zhidan Wu
Agronomy 2025, 15(1), 7; https://doi.org/10.3390/agronomy15010007 - 24 Dec 2024
Viewed by 288
Abstract
The responses of nitrous oxide (N2O) emissions to nitrogen (N) application in acidic, perennial agricultural systems, and the factors driving these emissions, remain poorly understood. To address this gap, a 12-year field experiment was conducted to investigate the effects of different [...] Read more.
The responses of nitrous oxide (N2O) emissions to nitrogen (N) application in acidic, perennial agricultural systems, and the factors driving these emissions, remain poorly understood. To address this gap, a 12-year field experiment was conducted to investigate the effects of different N application rates (0, 112.5, 225, and 450 kg N ha−1 yr−1) on N2O emissions, tea yield, and the associated driving factors in a tea plantation. The study found that soil pH significantly decreased with long-term N application, dropping by 0.32 to 0.85 units. Annual tea yield increased significantly, by 148–243%. N application also elevated N2O emission fluxes by 33–277%, with notable seasonal fluctuations observed. N2O flux was positively correlated with N rates, water-filled pore space (WFPS), soil temperature (Tsoil), and inorganic N (NH4+-N and NO3-N), while showing a negative correlation with soil pH. Random forest (RF) modeling identified WFPS, N rates, and Tsoil as the most important variables influencing N2O flux. The cumulative N2O emissions for N112.5, N225, and N450 were 1584, 2791, and 45,046 g N ha−2, respectively, representing increases of 1.33, 2.34, and 3.77 times compared to N0. The N2O-N emission factors (EF) were 0.35%, 0.71%, and 0.74%, respectively, and increased with higher N rates. These findings highlight the importance of selecting appropriate fertilization timing and improving water and fertilizer management as key strategies for mitigating soil acidification, enhancing nitrogen use efficiency (NUE), and reducing N2O emissions in acidic tea-plantation systems. This study offers a theoretical foundation for developing rational N fertilizer management practices and strategies aimed at reducing N2O emissions in tea-plantation soils. Full article
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<p>Geographic coordinates of the study area and the experimental design. (<b>a</b>) map of China, (<b>b</b>) map of Fujian Province, (<b>c</b>) map of Fu’An City and (<b>d</b>) experimental plot.</p>
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<p>Daily variations in average air temperature (°C) and precipitation (mm) for a tea plantation under different levels of N application during the whole experimental period (1 January 2023–31 December 2023). The meteorological data were obtained using a WS-MC01 compact automatic weather station installed on-site.</p>
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<p>Seasonal variations in T<sub>soil</sub> (<b>a</b>) and WFPS (<b>b</b>) for a tea plantation under different N rates during the experimental period. The <b>left</b> panels indicate the dynamic variations of T<sub>soil</sub> and WFPS with seasons, while the <b>right</b> panels indicate T<sub>soil</sub> and WFPS changes under different N rates. Error bars represent the standard errors (n = 3). The vertical arrows indicate the timing of fertilization. Lowercase letters above the bars indicate significant differences in T<sub>soil</sub> and WFPS among N rates, based on Tukey’s post hoc.</p>
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<p>Variations in soil pH (<b>a</b>), NH<sub>4</sub><sup>+</sup>-N (<b>b</b>), and NO<sub>3</sub><sup>−</sup>-N (<b>c</b>) in the soil with fertilization during the experimental period. The <b>left</b> panels indicate the dynamic variations of soil pH, NH<sub>4</sub><sup>+</sup>-N, and NO<sub>3</sub><sup>−</sup>-N content with seasons, while the <b>right</b> panels indicate soil pH, NH<sub>4</sub><sup>+</sup>-N, and NO<sub>3</sub><sup>−</sup>-N contents under different N rates. Error bars represent the standard errors (n = 3). The vertical arrows indicate the timing of fertilization. Lowercase letters above the bars indicate significant differences in soil pH, NH<sub>4</sub><sup>+</sup>-N, and NO<sub>3</sub><sup>−</sup>-N among N rates, based on Tukey’s post hoc test (<span class="html-italic">p</span> &lt; 0.05).</p>
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<p>Variations in N<sub>2</sub>O flux and cumulative N<sub>2</sub>O emission during the experimental period. The insert panel displays the cumulative N<sub>2</sub>O emissions under different levels of N application. Error bars represent the standard errors (n = 3). The vertical arrows indicate the timing of fertilization. Lowercase letters above the bars indicate significant differences across different N rates, based on Tukey’s post hoc test (<span class="html-italic">p</span> &lt; 0.05).</p>
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<p>The response of tea yield to four different N rates. (<b>a</b>) Bar plots show ANOVA results of the effect of N rates on tea yield. Tea data shown are mean ± standard error (SE; n = 3); lowercase letters above the bars indicate significant differences (<span class="html-italic">p</span> &lt; 0.05). (<b>b</b>) Trend lines show the linear regressions of tea yield against N rates, and the gray shading represents 95% confidence intervals.</p>
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<p>The relationship between N<sub>2</sub>O flux, N rates, T<sub>soil</sub>, WFPS, soil pH, NH<sub>4</sub><sup>+</sup>-N, and NO<sub>3</sub><sup>−</sup>-N. (<b>a</b>) Heatmap shows relationship between N<sub>2</sub>O flux, N rates, T<sub>soil</sub>, WFPS, soil pH, NH<sub>4</sub><sup>+</sup>-N, and NO<sub>3</sub><sup>−</sup>-N. * <span class="html-italic">p</span> &lt; 0.05, ** <span class="html-italic">p</span> &lt; 0.01. (<b>b</b>) Random forest modeling reveals the key factors influencing N<sub>2</sub>O flux. The %IncMSE stands for “the increase in the mean square error”, and R<sup>2</sup> refers to the model’s goodness of fit. The star above the bars indicates that the factor significantly influenced N<sub>2</sub>O flux, ** <span class="html-italic">p</span> &lt; 0.01.</p>
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14 pages, 2447 KiB  
Article
Straw Returning with Decomposition Agent Enhanced Rice Yield and Decreased Yield-Scaled N2O Emissions in Tropical Paddy Fields
by Longwei Meng, Qiqian Lu, Tian Lin, Lu Dong, Xiaochen Wu, Yixiu Zhuo, Anfu Yang, Qilin Zhu and Lei Meng
Agronomy 2024, 14(12), 3060; https://doi.org/10.3390/agronomy14123060 - 22 Dec 2024
Viewed by 370
Abstract
Straw returning (R) combined with the application of a decomposition agent (RD) can increase crop yield and soil carbon (C) storage. However, the effect of RD on soil nitrous oxide (N2O) emissions in tropical areas remains poorly understood. In this study, [...] Read more.
Straw returning (R) combined with the application of a decomposition agent (RD) can increase crop yield and soil carbon (C) storage. However, the effect of RD on soil nitrous oxide (N2O) emissions in tropical areas remains poorly understood. In this study, an in situ experiment was performed under different water management strategies (long-term flooding or alternate wetting and drying) with the R and RD treatments to evaluate soil N2O emissions and rice yield. The SOC and TN contents were significantly lower under the RD treatment than under the R treatment. The R treatment significantly increased rice yield; however, the yield was further significantly increased under the RD treatment. The soil N2O emissions and yield-scaled N2O emissions were higher under the R treatment than under the no-straw-returning treatment. However, the RD treatment greatly reduced soil N2O emissions and yield-scaled N2O emissions under various water management strategies compared with those under the R treatment. Moreover, yield-scaled N2O emissions were lower in the RD treatment than in the control. The soil N2O emissions and yield-scaled N2O emissions were distinctly higher under alternate wetting and drying than under long-term flooding. Our results indicated that long-term flooding and straw returning with decomposition agents can effectively increase rice yield and reduce soil N2O emissions in tropical areas. Full article
(This article belongs to the Section Innovative Cropping Systems)
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<p>Soil nitrous oxide (N<sub>2</sub>O) emissions in paddy field under different treatments.</p>
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<p>Cumulative soil N<sub>2</sub>O emissions in paddy field under different treatments. (<b>a</b>) represents soil N<sub>2</sub>O cumulative emission; (<b>b</b>) represents soil N<sub>2</sub>O emission per unit of yield production. The same lowercase letters suggest no significant difference between different treatments at 0.05 level.</p>
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<p>The NH<sub>4</sub><sup>+</sup> and NO<sub>3</sub><sup>−</sup> contents in paddy field under different treatments.</p>
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<p>Copy numbers of <span class="html-italic">nirK</span> (<b>a</b>), <span class="html-italic">nirS</span> (<b>b</b>), AOA (<b>c</b>) AOB (<b>d</b>) Fungi-<span class="html-italic">nirK</span> (<b>e</b>) <span class="html-italic">nosZ</span>, (<b>f</b>) gene (mean ± standard errors) under different treatments in the paddy field. The same lowercase letters suggest no significant difference between different treatments at 0.05 level.</p>
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<p>Partial correlations between the soil N<sub>2</sub>O emissions (<b>a</b>), rice yield (<b>b</b>), and four types of contributing factors. * <span class="html-italic">p</span> &lt; 0.05; ** <span class="html-italic">p</span> &lt; 0.01.</p>
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<p>Pearson’s correlation among soil properties, plant nutrients, yield, and soil N<sub>2</sub>O emissions. * <span class="html-italic">p</span> &lt; 0.05; ** <span class="html-italic">p</span> &lt; 0.01.</p>
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13 pages, 10017 KiB  
Article
Estimation of Nitrous Oxide Emissions from Agricultural Sources and Characterization of Spatial and Temporal Changes in Anhui Province (China)
by Zhou Ye, Yujuan Sun, Xianglin Zhang and Youzhi Yao
Atmosphere 2024, 15(12), 1538; https://doi.org/10.3390/atmos15121538 - 22 Dec 2024
Viewed by 357
Abstract
To evaluate the estimation and spatiotemporal variation characteristics of nitrous oxide emissions from agricultural sources in Anhui Province, the nitrous oxide emissions generated during crop cultivation and manure management were assessed based on the recommended methods in the “Guidelines for Provincial Greenhouse Gas [...] Read more.
To evaluate the estimation and spatiotemporal variation characteristics of nitrous oxide emissions from agricultural sources in Anhui Province, the nitrous oxide emissions generated during crop cultivation and manure management were assessed based on the recommended methods in the “Guidelines for Provincial Greenhouse Gas Inventories” and official statistical data. The results showed that the overall emission of nitrous oxide from agricultural land showed a downward trend, reaching a valley value in 2019 with an emission of 2.83 × 104 tons. The annual average emissions of nitrous oxide from agricultural land and manure management account for 80.98% and 19.02% of the total annual average emissions of nitrous oxide from agricultural activities in Anhui Province, respectively. Both agricultural land emissions and livestock manure management show a trend of nitrous oxide emissions decreasing from the northern region of Anhui > central region of Anhui > southern region of Anhui. In this paper, we explored and discussed the intrinsic driving factors behind the spatiotemporal changes in nitrous oxide emissions, and analyzed the potential for future emission reductions. It is suggested that the emissions of nitrous oxide from agricultural sources can be reduced through measures such as reasonable nitrogen application, adjustment of aquaculture structures, and the improvement of manure treatment methods, providing a theoretical reference for the estimation of greenhouse gas emissions from agricultural sources. Full article
(This article belongs to the Section Air Quality)
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<p>Changes in the number of farmed animals: (<b>a</b>) for non-dairy cows (×10<sup>3</sup>), (<b>b</b>) for poultry (×10<sup>5</sup>), (<b>c</b>) for sheep (×10<sup>3</sup>), and (<b>d</b>) for pigs (×10<sup>5</sup>).</p>
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<p>Mechanism diagram of nitrous oxide-emissions from agricultural sources [<a href="#B21-atmosphere-15-01538" class="html-bibr">21</a>].</p>
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<p>Historical changes in nitrous oxide emissions from agricultural activities in Anhui Province.</p>
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<p>Annual emissions of nitrous oxide from agricultural land in Anhui Province.</p>
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<p>Annual emissions of nitrous oxide from animal fecal management.</p>
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<p>Statistical chart of nitrous oxide emissions from agricultural land at some prefecture-level cities in Anhui Province (<b>a</b>) and nitrous oxide emissions from livestock and poultry manure management (<b>b</b>).</p>
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<p>Contribution of animal manure management (<b>a</b>) and agricultural land (<b>b</b>) to nitrous oxide emissions in some prefecture-level cities of Anhui Province in 2014 and 2022.</p>
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16 pages, 2511 KiB  
Article
Impacts of N2O Oversaturated Sewage Effluents on the Spatial Distribution of Riverine N2O: Insights from Sanya Estuaries, Hainan Province
by Dajun Qin, Jing Geng, Bingnan Ren and Bo Yang
Water 2024, 16(24), 3685; https://doi.org/10.3390/w16243685 - 20 Dec 2024
Viewed by 375
Abstract
Rivers and estuaries are recognized as significant sources of atmospheric greenhouse gas nitrous oxide (N2O), primarily through diffusive pathways. Anthropogenic nitrogen contributions to surface water bodies can alter the baseline emissions from natural sources; however, due to high spatial variability and [...] Read more.
Rivers and estuaries are recognized as significant sources of atmospheric greenhouse gas nitrous oxide (N2O), primarily through diffusive pathways. Anthropogenic nitrogen contributions to surface water bodies can alter the baseline emissions from natural sources; however, due to high spatial variability and limited datasets, the specific sources and sinks contributing to N2O remain poorly understood. This study investigates the sources and sinks of nitrous oxide (N2O) in river systems located in Sanya, Hainan Province, China. In April 2023, we collected 48 samples of river water and seawater, measuring hydrochemical parameters in situ while analyzing N2O concentrations in the laboratory. The results indicate that N2O concentrations vary significantly across different river systems within Sanya. Specifically, N2O concentrations ranged from 0.33 to 307.18 nmol/L for samples from the Sanya River, 2.28 to 3113.46 nmol/L for samples from Damaoshui River, 5.72 to 122.75 nmol/L for Tengqiao River waters, and between 11.08 and 18.07 nmol/L for Ningyuan River waters; coastal seawater exhibited concentrations ranging from 2.42 to 21.96 nmol/L. Notably, we observed that riverine N2O levels near sewage discharge points were oversaturated—indicating a peak concentration—which subsequently declined towards levels more consistent with those found in natural river systems as one approaches the mouths of estuaries. Both Sanya River and Damaoshui River appear to be significant sources of N2O; conversely, coastal seawater is not considered a substantial source. Our data suggest that wastewater discharges may play a critical role in influencing N2O levels within river waters by directly introducing oversaturated effluents into these ecosystems. Full article
(This article belongs to the Special Issue The Environmental Fate and Transport of Organic Pollutants)
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<p>The locations of the field sampling sites in four river estuaries in Sanya, Hainan, China, are presented. Blue lines and areas represent rivers and water bodies (ponds or reservoirs depending on their size). Detailed studies were conducted at two selected rivers (WR + ER and DR) in Sanya. Site 4 is situated near a wastewater treatment plant (WWTP) discharge point along the East Sanya River (ER), while site 13 corresponds to a sewage effluent location adjacent to cracked sewer systems beside Damaoshui River (DR). Blue lines represent the river systems, and blue-filled areas denote water bodies such as reservoirs and ponds. Red open diamonds indicate sites designated for collecting river water samples, green solid circles represent coastal seawater samples (CS), and green solid diamonds mark locations for inland seawater samples near Haitang Bay (HS). TR1 and TR2 refer to two branches of Tengqiao River. This time, four samples were collected from Ningyuan River (NR).</p>
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<p>Histograms of the concentrations of N<sub>2</sub>O for river waters (<b>a</b>) and seawaters (<b>b</b>). Frequency = count/total number. The equilibrium value in rivers with the atmosphere is about 6.9 nmol/L.</p>
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<p>Box plots of the concentrations of N<sub>2</sub>O (<b>a</b>), NO<sub>3</sub><sup>−</sup> (<b>b</b>), N<sub>2</sub>O saturation ((<b>c</b>), expressed as a percentage on a logarithmic scale), and dissolved oxygen (DO) (<b>d</b>). The concentrations of N<sub>2</sub>O and the saturation percentages are presented on a logarithmic scale. Solid diamonds and circles denote sample points. The symbols along the <span class="html-italic">x</span>-axis represent rivers located in the Sanya area of Hainan Province, consistent with the previous explanations provided in this context. The <span class="html-italic">x</span>-axis labels correspond to those used in <a href="#water-16-03685-f001" class="html-fig">Figure 1</a>.</p>
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<p>Concentrations of N<sub>2</sub>O (<b>a</b>), dissolved oxygen (DO) (<b>b</b>), nitrate (NO<sub>3</sub><sup>−</sup>) (<b>c</b>), and pH (<b>d</b>) in river water at each sampling site, plotted against the distance from each estuary mouth. N<sub>2</sub>O concentrations are presented on a logarithmic scale. The peak concentration of N<sub>2</sub>O corresponds to the location of sewage effluents, while the peak for NO<sub>3</sub><sup>−</sup> is observed 1 to 2 km downstream from this point. The legends remain consistent with those in <a href="#water-16-03685-f001" class="html-fig">Figure 1</a>.</p>
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<p>Riverine N<sub>2</sub>O concentration versus potential causal factors. (<b>a</b>) N<sub>2</sub>O vs. NO<sub>3</sub><sup>−</sup>; (<b>b</b>) DO vs. NO<sub>3</sub><sup>−</sup>; (<b>c</b>) N<sub>2</sub>O vs. DO; and (<b>d</b>) DO vs. pH. The red dotted arrow line represents mixing of sewerage and river water. The inverse correlation between DO and NO<sub>3</sub><sup>−</sup> (<b>b</b>) and N<sub>2</sub>O and DO (<b>c</b>) indicates the mixing between sewage and river water, and the positive correlation between N<sub>2</sub>O and NO<sub>3</sub><sup>−</sup> (<b>a</b>) is the mixing from the high-N<sub>2</sub>O point to the low-value direction. The blue arrow dotted line indicates nitrification. The dashed blue circle delineates the range of points with elevated N<sub>2</sub>O values in (<b>d</b>). In the process of nitrification, the oxygen content decreases, the N<sub>2</sub>O decreases, and the NO<sub>3</sub><sup>−</sup> increases. The process of denitrification is inhabited in oxic conditions. The <span class="html-italic">y</span>-axis of N<sub>2</sub>O is on the log scale. Legends are the same as <a href="#water-16-03685-f001" class="html-fig">Figure 1</a>.</p>
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<p>Model of riverine N<sub>2</sub>O generation and regulation influenced by N<sub>2</sub>O-oversaturated sewage effluents: (<b>a</b>) denitrification of N<sub>2</sub>O within sewer systems leading to N<sub>2</sub>O accumulation; (<b>b</b>) partial nitrification and denitrification processes occurring in riverine environments; and (<b>c</b>) riverine nitrification (N<sub>2</sub>O + O<sub>2</sub>→ NO<sub>3</sub><sup>−</sup>) stimulated by the introduction of N<sub>2</sub>O-oversaturated sewage effluents. Within the metabolism of ammonia-oxidizing bacteria (AOB), N<sub>2</sub>O can be produced through two distinct mechanisms: oxidation of NH<sub>2</sub>OH and reduction in NO<sub>2</sub><sup>−</sup> (nitrifier denitrification) [<a href="#B41-water-16-03685" class="html-bibr">41</a>,<a href="#B42-water-16-03685" class="html-bibr">42</a>]. Arrow lines indicate the directionality of reactions.</p>
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16 pages, 4967 KiB  
Article
Effects of Solid Dairy Manure Application on Greenhouse Gas Emissions and Corn Yield in the Upper Midwest, USA
by Eric Young and Jessica Sherman
Sustainability 2024, 16(24), 11171; https://doi.org/10.3390/su162411171 - 20 Dec 2024
Viewed by 431
Abstract
Dairy manure is an important nitrogen (N) source for crops, but its role in greenhouse gas (GHG) emissions and farm sustainability is not fully understood. We evaluated the effects of application of two dairy manure sources (bedded pack heifer, BP, and separated dairy [...] Read more.
Dairy manure is an important nitrogen (N) source for crops, but its role in greenhouse gas (GHG) emissions and farm sustainability is not fully understood. We evaluated the effects of application of two dairy manure sources (bedded pack heifer, BP, and separated dairy solids, SDS) on corn silage yield and GHG emissions (carbon dioxide, CO2; methane, CH4; nitrous oxide, N2O) compared to a urea-fertilizer-only control (80 kg N ha−1 yr−1). The BP and SDS were applied at 18.4 and 19.4 Mg dry matter ha−1 in fall 2020 in the final year of ryegrass production. No-till corn was planted from 2021 to 2023, and GHG emissions were measured each season (from May to November). The results showed significantly greater CO2-C emissions for BP in 2021 and no differences in 2022 or 2023. A small N2O-N emission increase for BP occurred in the spring after application; however, seasonal fluxes were low or negative. Mean CH4-C emissions ranged from 2 to 7 kg ha−1 yr−1 with no treatment differences. Lack of soil aeration appeared to be an important factor affecting seasonal N2O-N and CH4-C emissions. The results suggest that GHG models should account for field-level nutrient management factors in addition to soil aeration status. Full article
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<p>Select soil properties from samples taken in fall 2020 before manure application. Average soil pH (<b>a</b>), Bray-1 extractable phosphorus (<b>b</b>), Bray 1 extractable potassium (<b>c</b>), soil organic matter content (<b>d</b>), total nitrogen (<b>e</b>), and total carbon (<b>f</b>) at three depth intervals (0–5 cm, 5–15 cm, and 15–30 cm). Error bars are one standard error of the mean of four replicated plots. Note: These were baseline soil analyses prior to manure application to assess consistency. Dairy heifer bedded pack manure designated plots = BP; separated dairy manure solids designated plots = SDS; control (fertilizer only) = CON.</p>
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<p>Dry matter solids and nutrients applied from dairy heifer bedded pack manure (BP) and separated dairy manure solids (SDS). Solids = manure solids (Mg ha<sup>−1</sup>); N = total nitrogen (kg ha<sup>−1</sup>); P = total phosphorus (kg ha<sup>−1</sup>); K = potassium (kg ha<sup>−1</sup>); S = sulfur (kg ha<sup>−1</sup>); Amm-N = ammonium-nitrogen (kg ha<sup>−1</sup>).</p>
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<p>Corn silage dry matter yield in 2021, 2022, and 2023 along with mean soil inorganic nitrogen concentration (ammonium-N + nitrate-N) taken from control plots when corn was approximately at the V5 growth stage. Means with different lowercase letters differ at <span class="html-italic">p</span> ≤ 0.05. Dairy heifer bedded pack manure = BP; separated dairy manure solids = SDS; control (fertilizer only) = CON.</p>
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<p>Mean carbon dioxide–carbon (CO<sub>2</sub>-C) emissions for each study year. Means notated with different lowercase letters for an event differ <span class="html-italic">(p</span> ≤ 0.05). Means without letters do not differ (<span class="html-italic">p</span> &gt; 0.05). Error bars are one standard error of the mean of four replicated plots. Dairy heifer bedded pack manure = BP; separated dairy manure solids = SDS; control (fertilizer only) = CON. FTIR breakdown denotes the time during which the FTIR instrument was under repair, and field measurements were not taken.</p>
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<p>Cumulative carbon dioxide–carbon (CO<sub>2</sub>-C) (<b>a</b>), nitrous oxide–nitrogen (N<sub>2</sub>O-N) (<b>b</b>), and methane–carbon (CH<sub>4</sub>-C) (<b>c</b>) emissions in each study year. Means notated with different lowercase letters differ (<span class="html-italic">p</span> ≤ 0.05). Error bars are one standard error of the mean of four replicated plots. Dairy heifer bedded pack manure = BP; separated dairy manure solids = SDS; control (fertilizer only) = CON.</p>
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<p>Mean nitrous oxide–nitrogen (N<sub>2</sub>O-N) and methane–carbon (CH<sub>4</sub>-C) emissions for 2020 and 2021. Means notated with different lowercase letters for an event differ (<span class="html-italic">p</span> ≤ 0.05). Means without letters do not differ (<span class="html-italic">p</span> &gt; 0.05). Error bars are one standard error of the mean of four replicated plots. Dairy heifer bedded pack manure = BP; separated dairy manure solids = SDS; control (fertilizer only) = CON. FTIR breakdown denotes the time during which the FTIR instrument was under repair, and field measurements were not taken.</p>
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<p>Mean nitrous oxide–nitrogen (N<sub>2</sub>O-N) and methane–carbon (CH<sub>4</sub>-C) emissions for 2022 and 2023. Means notated with different lowercase letters for an event differ (<span class="html-italic">p</span> ≤ 0.05). Means without letters do not differ (<span class="html-italic">p</span> &gt; 0.05). Error bars are one standard error of the mean of four replicated plots. Dairy heifer bedded pack manure = BP; separated dairy manure solids = SDS; control (fertilizer only) = CON.</p>
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<p>Changes in plot soil moisture content and temperature for 2020 and 2021. Means notated with different lowercase letters for an event differ (<span class="html-italic">p</span> ≤ 0.05). Means without letters do not differ (<span class="html-italic">p</span> &gt; 0.05). Error bars are one standard error of the mean of four replicated plots. Dairy heifer bedded pack manure = BP; separated dairy manure solids = SDS; control (fertilizer only) = CON. FTIR breakdown denotes the time during which the FTIR instrument was under repair, and field measurements were not taken.</p>
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<p>Changes in plot soil moisture content and temperature for 2020 and 2021. Means notated with different lowercase letters for an event differ (<span class="html-italic">p</span> ≤ 0.05). Means without letters do not differ (<span class="html-italic">p</span> &gt; 0.05). Error bars are one standard error of the mean of four replicated plots. Dairy heifer bedded pack manure = BP; separated dairy manure solids = SDS; control (fertilizer only) = CON.</p>
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<p>Daily total precipitation and temperature at the study site for 2020–2023.</p>
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13 pages, 1598 KiB  
Article
Nitrite Cycling in Freshwater Ecosystems: A Case Study of an Artificial Reservoir in Eastern China Using Nitrite Dual Isotopes Combined with a Geochemical Model
by Xinwei Li, Xingzhou Zhang, Yuanyuan Yang, Yingying Li, Lujie Jia and Yangjun Chen
Sustainability 2024, 16(24), 11099; https://doi.org/10.3390/su162411099 - 18 Dec 2024
Viewed by 550
Abstract
Reservoirs are hotspots for emissions of the greenhouse gas nitrous oxide; however, the nitrite cycling processes associated with nitrous oxide production therein remain poorly understood, limiting a better assessment of the potential for reservoirs to emit nitrous oxide. Accordingly, this study presents the [...] Read more.
Reservoirs are hotspots for emissions of the greenhouse gas nitrous oxide; however, the nitrite cycling processes associated with nitrous oxide production therein remain poorly understood, limiting a better assessment of the potential for reservoirs to emit nitrous oxide. Accordingly, this study presents the application of the natural abundance isotope technique combined with a geochemical model to elucidate the nitrite cycling in the freshwater aquaculture and non-aquaculture zones of a large artificial reservoir in eastern China. We employed nitrite dual isotopes to identify nitrite transformation processes. Additionally, a steady-state model was used to estimate the rates of these processes as well as the residence time of nitrite. Our findings indicate that nitrite production in this reservoir may be primarily driven by ammonia oxidation. However, the pathways of nitrite removal differ notably between the aquaculture and non-aquaculture zones, suggesting a significant impact of the aquaculture activities. The steady-state model calculations revealed that nitrification may be more pronounced in the aquaculture zones compared to the non-aquaculture zones, which may be related to the altered balance of competition for substrates between phytoplankton and microbes induced by aquaculture activities. Moreover, we observed a latitude-dependent increase in the significance of nitrite oxidation in natural environments, highlighting potential implications for regional and global nitrogen cycling. Our study highlights the complexity of the nitrite cycle and emphasizes the roles of both natural and anthropogenic factors in shaping nitrogen dynamics within freshwater reservoirs. This understanding contributes to a more accurate assessment of the greenhouse gas emission potential of reservoirs, offering valuable implications for the adoption of sustainable aquaculture practices to mitigate climate impacts and support global sustainable development goals. Full article
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<p>A map of sampling stations. Stations S6–S10 were situated in the cage aquaculture zone, while S1–S5 were in the non-agriculture zone.</p>
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<p>An illustration of biogeochemical processes affecting nitrite dual isotopes in the Shilianghe reservoir. Note that the error bars for the sample measurements are masked by the data symbols.</p>
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<p>Significance of nitrite oxidation in aquatic ecosystems at various latitudes. Data calculated using same model in marine environment at different latitudes were used for comparison [<a href="#B8-sustainability-16-11099" class="html-bibr">8</a>,<a href="#B9-sustainability-16-11099" class="html-bibr">9</a>,<a href="#B12-sustainability-16-11099" class="html-bibr">12</a>].</p>
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<p>The comparison of the residence time of nitrite due to biological turnover in marine [<a href="#B8-sustainability-16-11099" class="html-bibr">8</a>,<a href="#B9-sustainability-16-11099" class="html-bibr">9</a>,<a href="#B12-sustainability-16-11099" class="html-bibr">12</a>,<a href="#B15-sustainability-16-11099" class="html-bibr">15</a>,<a href="#B16-sustainability-16-11099" class="html-bibr">16</a>] and freshwater ecosystems. The bar chart includes letters (a, b, ab) to indicate statistical significance. Bars labeled with the same letter are not significantly different, while bars with different letters indicate significant differences (<span class="html-italic">p</span> &lt; 0.05).</p>
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17 pages, 7464 KiB  
Article
Soil Greenhouse Gas Emissions and Nitrogen Dynamics: Effects of Maize Straw Incorporation Under Contrasting Nitrogen Fertilization Levels
by Zhengyu Wang, Jiaxin Shang, Xuelian Wang, Rongqi Ye, Dan Zhao, Xiangyu Li, Yadong Yang, Hongyu Zhang, Xiangwei Gong, Ying Jiang and Hua Qi
Agronomy 2024, 14(12), 2996; https://doi.org/10.3390/agronomy14122996 - 16 Dec 2024
Viewed by 491
Abstract
Straw is widely incorporated into conservation agriculture around the world. However, its effects on greenhouse gas emissions (GHGs) and nitrogen dynamics under soils formed by the long-term application of different amounts of nitrogen (N) fertilizer are still unclear. An incubation experiment was conducted [...] Read more.
Straw is widely incorporated into conservation agriculture around the world. However, its effects on greenhouse gas emissions (GHGs) and nitrogen dynamics under soils formed by the long-term application of different amounts of nitrogen (N) fertilizer are still unclear. An incubation experiment was conducted on soils collected from a field study after 6 years of contrasting N fertilization of 0 (low N), 187 (medium N), and 337 kg N ha−1 (high N), with and without maize straw. Straw amendment significantly stimulated both nitrous oxide (N2O) and carbon dioxide (CO2) fluxes (p < 0.05), and increased cumulative emissions by 0.8 and 19.0 times on average compared to those without straw incorporation. Medium-N soil observably weakened N2O emissions (23.8 μg kg−1) compared to high-N soil (162.7 μg kg−1), and increased CO2 emissions (1.9 g kg−1) compared to low-N soils (2.3 g kg−1) with straw amendment. Soil NH4+-N and NO3-N invariably increased with rising soil N level, whereas straw promoted the turnover of mineral N by enhancing soil N fixation capacity. From the first day until the end of incubation, NH4+-N decreased by 79.0% and 24.7%, while NO3-N showed a decrease of 58.8% or an increase of 75.2%, depending on whether straw was amended or not, respectively. Moreover, partial least squares path modeling and random forest mean predictor importance were used to find that straw affected GHGs by altering the N turnover capacity. Straw amendment increased GHGs and diminished the risk of losing mineral N by enhancing its turnover. Combining straw with medium-N soil could mitigate the greenhouse effect and improve the N and carbon (C) balance in farming systems compared to low- and high-N soils. This is recommended as a farmland management strategy in Northeast China. Full article
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<p>N<sub>2</sub>O-N flux (<b>a</b>), CO<sub>2</sub>-C flux (<b>b</b>), and CH<sub>4</sub>-C uptake flux (<b>c</b>) of treatments during the incubation period. LN, MN, HN, and N<sub>m</sub>—low, medium, high, and the mean of soil; LN+S, MN+S, HN+S, and SN<sub>m</sub>—low, medium, high, and the mean of soil with straw amendment. S, straw amendment; N, soil N level; S × N, the interaction of straw amendment and soil N level. *, ** and *** on numbers indicate significant difference at levels of <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. ns, no significant difference (ANOVA). * over symbols indicate significant difference between N<sub>m</sub> and SN<sub>m</sub> in the same incubation point at a <span class="html-italic">p</span> &lt; 0.05 level. Different letters indicate significant differences between treatments at the same incubation point at a <span class="html-italic">p</span> &lt; 0.05 level.</p>
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<p>Accumulative dynamic and emission of N<sub>2</sub>O-N (<b>a</b>,<b>d</b>), CO<sub>2</sub>-C (<b>b</b>,<b>e</b>), and CH<sub>4</sub>-C (<b>c</b>,<b>f</b>) of treatments during the whole incubation. LN, MN, HN and N<sub>m</sub>—low, medium, high, and the mean of soil; LN+S, MN+S, HN+S, and SN<sub>m</sub>—low, medium, high, and the mean of soil with straw amendment. S, straw amendment; N, soil N level; S × N, the interaction of straw amendment and soil N level. *, ** and *** on numbers indicate significant difference at levels of <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. ns, no significant difference (ANOVA). Different lowercase and capital letters indicate significant differences between treatments without/with straw amendment at a <span class="html-italic">p</span> &lt; 0.05 level, respectively.</p>
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<p>Global warming potential (GWP) of treatments during the whole incubation. LN, MN, HN, and N<sub>m</sub>—low, medium, high, and the mean of soil; LN+S, MN+S, HN+S, and SN<sub>m</sub>—low, medium, high, and the mean of soil with straw amendment. S, straw amendment; N, soil N level; S×N, the interaction of straw amendment and soil N level. *, ** and *** on numbers indicate significant differences at levels of <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 (ANOVA). Different lowercase and capital letters indicate significant difference between treatments without/with straw amendment at a <span class="html-italic">p</span> &lt; 0.05 level, respectively.</p>
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<p>Ammonium ((<b>a</b>), NH<sub>4</sub><sup>+</sup>-N), nitrate ((<b>b</b>), NO<sub>3</sub><sup>−</sup>-N), and microbial biomass nitrogen ((<b>c</b>), SMBN) concentration dynamics of treatments during the whole incubation period. LN, MN, HN, and N<sub>m</sub>—low, medium, high, and the mean of soil; LN+S, MN+S, HN+S, and SN<sub>m</sub>—low, medium, high, and the mean of soil with straw amendment. S, straw amendment; N, soil N level; S × N, the interaction of straw amendment and soil N level. *, ** and *** on numbers indicate significant differences at levels of <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. ns, no significant difference (ANOVA). * over symbols indicate significant difference between Nm and SN<sub>m</sub> in the same incubation point at a <span class="html-italic">p</span> &lt; 0.05 level. Different letters indicate significant differences between treatments at the same incubation point at a <span class="html-italic">p</span> &lt; 0.05 level.</p>
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<p>Net ammonification rate ((<b>a</b>) NAR), net nitrification rate ((<b>b</b>) NNR), net nitrogen mineralization rate ((<b>c</b>) NNMR), nitrogen turnover rate ((<b>d</b>) NTR), nitrification potential ((<b>e</b>) NP), and the ratio of ammonium to nitrate (<b>f</b>) of treatments during the incubation period. LN, MN, HN, and N<sub>m</sub>—low, medium, high, and the mean of soil; LN+S, MN+S, HN+S, and SN<sub>m</sub>—low, moderate, high, and the mean of soil with straw amendment. S, straw amendment; N, soil N level; S × N, the interaction of straw amendment and soil N level. *, ** and *** on numbers indicate significant differences at levels of <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. ns, no significant difference (ANOVA). * over symbols indicate significant difference between N<sub>m</sub> and SN<sub>m</sub> in the same incubation point at <span class="html-italic">p</span> &lt; 0.05 level. Different letters indicate significant differences between treatments at the same incubation point at a <span class="html-italic">p</span> &lt; 0.05 level.</p>
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<p>Partial least squares path modeling (PLS-PM) disentangling major pathways of the effects of soil properties on greenhouse gas emissions (GHGs: N<sub>2</sub>O, CO<sub>2</sub> and CH<sub>4</sub>) and the total effects of these variables on GHGs without straw amendment (<b>a</b>,<b>b</b>) and with straw amendment (<b>c</b>,<b>d</b>). SOC, soil organic C; TN, total nitrogen; C:N ratios, the ratio of SOC to TN; NH<sub>4</sub><sup>+</sup>-N, ammonium concentration; NO<sub>3</sub><sup>−</sup>-N, nitrate concentration; SMBN, microbial biomass nitrogen concentration; NAR, net ammonification rate; NNR, net nitrification rate; NNMR, net nitrogen mineralization rate; NTR, nitrogen turnover rate; NP, nitrification potential and NH<sub>4</sub><sup>+</sup>-N: NO<sub>3</sub><sup>−</sup>-N, the ratio of ammonium to nitrate. The model’s reliability was assessed using the goodness of fit (GoF). Solid and dotted arrows denote positive and negative causality, respectively. Numbers above the arrow lines are indicative of the correlation and significance standardized path coefficients. <span class="html-italic">R</span><sup>2</sup> indicates the variance of the dependent variable explained by the model.</p>
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<p>Redundancy analysis (RDA) and random forest mean predictor importance (% increase in MSE) showing the relationship and the relative importance of soil properties on greenhouse gas emissions under the circumstance of straw removal ((<b>a</b>,<b>b</b>): N<sub>2</sub>O, (<b>c</b>): CO<sub>2</sub>, (<b>d</b>): CH<sub>4</sub>) and straw amendment ((<b>e</b>,<b>f</b>): N<sub>2</sub>O, (<b>g</b>): CO<sub>2</sub>, (<b>h</b>): CH<sub>4</sub>). Blue lines represent environmental variables; red lines represent response variables (N<sub>2</sub>O, CO<sub>2</sub> and CH<sub>4</sub>). Percentage increases in the MSE (mean squared error) of variables were used to estimate the importance of these predictors, and higher MSE% values imply more important predictors. Significance levels of each predictor are as follows: * <span class="html-italic">p</span> &lt; 0.05 and ** <span class="html-italic">p</span> &lt; 0.01. SOC, soil organic C; TN, total nitrogen; C:N ratios, the ratio of SOC to TN; NH<sub>4</sub><sup>+</sup>-N, ammonium concentration; NO<sub>3</sub><sup>−</sup>-N, nitrate concentration; SMBN, microbial biomass nitrogen concentration; NAR, net ammonification rate; NNR, net nitrification rate; NNMR, net nitrogen mineralization rate; NTR, nitrogen turnover rate; NP, nitrification potential; and NH<sub>4</sub><sup>+</sup>-N: NO<sub>3</sub><sup>−</sup>-N, the ratio of ammonium to nitrate. MSE, mean squared error.</p>
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22 pages, 781 KiB  
Review
Anesthetic Gases: Environmental Impacts and Mitigation Strategies for Fluranes and Nitrous Oxide
by William A. Anderson and Anita Rao
Environments 2024, 11(12), 275; https://doi.org/10.3390/environments11120275 - 2 Dec 2024
Viewed by 1058
Abstract
Anesthetic gases represent a small but significant portion of the environmental impact of health care in many countries. These compounds include several fluorocarbons commonly referred to as “fluranes”. The fluranes are greenhouse gases (GHG) with global warming potentials in the hundreds to thousands [...] Read more.
Anesthetic gases represent a small but significant portion of the environmental impact of health care in many countries. These compounds include several fluorocarbons commonly referred to as “fluranes”. The fluranes are greenhouse gases (GHG) with global warming potentials in the hundreds to thousands and are also PFAS compounds (per- and polyfluorinated alkyl substances) according to at least one definition. Nitrous oxide (N2O) is sometimes used as an adjunct in anesthesia, or for sedation, but has a significant stratospheric ozone depletion potential as well as GHG effects. Reducing emissions of these compounds into the environment is, therefore, a growing priority in the health care sector. Elimination or substitution of the highest impact fluranes with alternatives has been pursued with some success but limitations remain. Several emission control strategies have been developed for fluranes including adsorption onto solids, which has shown commercial promise. Catalytic decomposition methods have been pursued for N2O emission control, although mixtures of fluranes and N2O are potentially problematic for this technology. All such emission control technologies require the effective scavenging and containment of the anesthetics during use, but the limited available information suggests that fugitive emissions into the operating room may be a significant route for unmitigated losses of approximately 50% of the used fluranes into the environment. A better understanding and quantification of such fugitive emissions is needed to help minimize these releases. Further cost–benefit and techno-economic analyses are also needed to identify strategies and best practices for the future. Full article
(This article belongs to the Special Issue Air Quality, Health and Climate)
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<p>Structures of the common halocarbon anesthetics (<b>left</b> to <b>right</b>) Isoflurane, Sevoflurane, and Desflurane.</p>
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<p>Illustration of the anesthesia machine usage: (<b>a</b>) patient breathing circuit with controlled flow, flurane, and oxygen concentrations; (<b>b</b>) anesthesia machine controlling the breathing circuit; (<b>c</b>) fresh gas flow to replace metabolized oxygen; (<b>d</b>) discharge of excess gases to the scavenging system; (<b>e</b>) uncontrolled escape of fluranes to the surrounding environment.</p>
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17 pages, 1884 KiB  
Article
Indoor Air Quality in a Museum Storage Room: Conservation Issues Induced in Plastic Objects
by Maria Catrambone, Marianna Cappellina, Francesca Olivini, Elena Possenti, Ilaria Saccani and Antonio Sansonetti
Atmosphere 2024, 15(12), 1409; https://doi.org/10.3390/atmos15121409 - 23 Nov 2024
Viewed by 505
Abstract
This study focuses on assessing the indoor air quality in a storage room (SR) belonging to Museo Nazionale Scienza e Tecnologia Leonardo da Vinci in Milan (MUST), covering pollutants originating from outdoor sources and emissions from historical plastic objects made from cellulose acetate [...] Read more.
This study focuses on assessing the indoor air quality in a storage room (SR) belonging to Museo Nazionale Scienza e Tecnologia Leonardo da Vinci in Milan (MUST), covering pollutants originating from outdoor sources and emissions from historical plastic objects made from cellulose acetate (CA), cellulose nitrate (CN), and urea–formaldehyde (UF) stored in metal cabinets. The concentrations of SO2 (sulphur dioxide), NO2 (nitrogen dioxide), NOx (nitrogen oxides), HONO (nitrous acid), HNO3 (nitric acid), O3 (ozone), NH3 (ammonia), CH3COOH (acetic acid), and HCOOH (formic acid) were determined. The concentrations of SO2, O3, and NOx measured inside the metal cabinets were consistently lower compared to the other sampling sites. This result was expected due to their reactivity and the lack of internal sources. The SR and metal cabinets showed similar concentrations of NO and NO2, except for CA, where a high NO concentration was detected. The interaction between the CA surfaces and NO2 altered the distribution of NO and NO2, leading to a significant increase in NO. The presence of HNO3 potentially led to the formation of ammonium nitrate, as confirmed by ER-FTIR measurements. High levels of HONO and HNO3 in CN and NH3 in the UF indicate object deterioration, while elevated concentrations of CH3COOH in CA and HCOOH in the SR suggest specific degradation pathways for cellulose acetate and other organic materials, respectively. These results could direct conservators towards the most appropriate practical actions. Full article
(This article belongs to the Section Air Quality)
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<p>Metal cabinet containing object in cellulose acetate (<b>a</b>) and storage room (<b>b</b>); the arrow indicates the position of diffusive samplers.</p>
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<p>Average concentrations of (<b>a</b>) SO<sub>2</sub>, (<b>b</b>) NO<sub>2,</sub> (<b>c</b>) NO<sub>x</sub>, (<b>d</b>) O<sub>3</sub>, (<b>e</b>) NO, (<b>f</b>) HONO, (<b>g</b>) HNO<sub>3,</sub> (<b>h</b>) NH<sub>3</sub>, (<b>i</b>) CH<sub>3</sub>COOH, (<b>j</b>) HCOOH measured in the three metal cabinets (MCA, MCN, and MUF) and in the two rooms (SR and OSR) (see <a href="#atmosphere-15-01409-t001" class="html-table">Table 1</a>).</p>
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<p>Average concentrations of (<b>a</b>) SO<sub>2</sub>, (<b>b</b>) NO<sub>2,</sub> (<b>c</b>) NO<sub>x</sub>, (<b>d</b>) O<sub>3</sub>, (<b>e</b>) NO, (<b>f</b>) HONO, (<b>g</b>) HNO<sub>3,</sub> (<b>h</b>) NH<sub>3</sub>, (<b>i</b>) CH<sub>3</sub>COOH, (<b>j</b>) HCOOH measured in the three metal cabinets (MCA, MCN, and MUF) and in the two rooms (SR and OSR) (see <a href="#atmosphere-15-01409-t001" class="html-table">Table 1</a>).</p>
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<p>Average concentrations of (<b>a</b>) SO<sub>2</sub>, (<b>b</b>) NO<sub>2,</sub> (<b>c</b>) NO<sub>x</sub>, (<b>d</b>) O<sub>3</sub>, (<b>e</b>) NO, (<b>f</b>) HONO, (<b>g</b>) HNO<sub>3,</sub> (<b>h</b>) NH<sub>3</sub>, (<b>i</b>) CH<sub>3</sub>COOH, (<b>j</b>) HCOOH measured in the three metal cabinets (MCA, MCN, and MUF) and in the two rooms (SR and OSR) (see <a href="#atmosphere-15-01409-t001" class="html-table">Table 1</a>).</p>
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<p>ER-FTIR spectrum collected on the body of the bag (in red, where the plastic material appears sound), in comparison to the ER-FTIR spectrum of cellulose acetate (in black).</p>
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<p>ER-FTIR spectrum collected on the cellulose acetate bag in correspondence of those parts where the surface appears decayed and covered by white crystals (in red), in comparison to the ER-FTIR spectrum of cellulose nitrate (in black).</p>
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18 pages, 390 KiB  
Review
Contributions of Medical Greenhouse Gases to Climate Change and Their Possible Alternatives
by Joyce Wang and Shiladitya DasSarma
Int. J. Environ. Res. Public Health 2024, 21(12), 1548; https://doi.org/10.3390/ijerph21121548 - 22 Nov 2024
Viewed by 812
Abstract
Considerable attention has recently been given to the contribution of the greenhouse gas (GHG) emissions of the healthcare sector to climate change. GHGs used in medical practice are regularly released into the atmosphere and contribute to elevations in global temperatures that produce detrimental [...] Read more.
Considerable attention has recently been given to the contribution of the greenhouse gas (GHG) emissions of the healthcare sector to climate change. GHGs used in medical practice are regularly released into the atmosphere and contribute to elevations in global temperatures that produce detrimental effects on the environment and human health. Consequently, a comprehensive assessment of their global warming potential over 100 years (GWP) characteristics, and clinical uses, many of which have evaded scrutiny from policy makers due to their medical necessity, is needed. Of major interest are volatile anesthetics, analgesics, and inhalers, as well as fluorinated gases used as tamponades in retinal detachment surgery. In this review, we conducted a literature search from July to September 2024 on medical greenhouse gases and calculated estimates of these gases’ GHG emissions in metric tons CO2 equivalent (MTCO2e) and their relative GWP. Notably, the anesthetics desflurane and nitrous oxide contribute the most emissions out of the major medical GHGs, equivalent to driving 12 million gasoline-powered cars annually in the US. Retinal tamponade gases have markedly high GWP up to 23,500 times compared to CO2 and long atmospheric lifetimes up to 10,000 years, thus bearing the potential to contribute to climate change in the long term. This review provides the basis for discussions on examining the environmental impacts of medical gases with high GWP, determining whether alternatives may be available, and reducing emissions while maintaining or even improving patient care. Full article
(This article belongs to the Special Issue Climate Change and Medical Responses)
24 pages, 4370 KiB  
Article
Analysis of Carbon Footprint Including Process-Level Calculation and Its Influencing Factors of Process for Low-Carbon and Sustainable Textile Industry
by Hakan Alıcı, Beyza Nur Yiğit, Betül Menemencioğlu, Kübra Tümay Ateş, Özge Demirdelen, Tuğçe Demirdelen and Ziya Kıvanç
Sustainability 2024, 16(23), 10168; https://doi.org/10.3390/su162310168 - 21 Nov 2024
Viewed by 909
Abstract
Climate change stands out as a significant environmental issue on a global scale, with greenhouse gases being one of its primary drivers. The greenhouse gas process provides a critical framework for understanding the sources, emissions, and environmental impacts of these gases. This article [...] Read more.
Climate change stands out as a significant environmental issue on a global scale, with greenhouse gases being one of its primary drivers. The greenhouse gas process provides a critical framework for understanding the sources, emissions, and environmental impacts of these gases. This article presents an overview of the fundamental elements of the greenhouse gas process in the textile sector and discusses how it should be managed in line with sustainability goals. Carbon dioxide (CO2), methane (CH4), nitrous oxides (N2O), and fluorinated gases are the most common greenhouse gases, each derived from different sources. The textile sector is particularly associated with high greenhouse gas emissions, especially in areas such as energy consumption, water usage, and waste management. Therefore, measurements taken in factories are crucial for identifying emission sources and developing reduction strategies. This article examines in detail the greenhouse gas emissions resulting from various activities at Kıvanç Textile. Energy consumption, particularly the emissions resulting from the fuels used in electricity and heating processes, is evaluated. Additionally, emissions from other important sources such as refrigerant gas leaks, waste management, and transportation are analyzed. The measurement process was carried out in accordance with national and international standards. The greenhouse gas inventory includes data on energy consumption, fuel consumption, refrigerant gas usage, transportation, production process management, and waste management throughout the factory. Based on these data, the total amount and sources of emissions were determined. This study presents a systematic method for calculating a company’s carbon footprint, with data collected in accordance with national and international standards. Such data can provide a reference point for other companies when making similar calculations. All of the businesses of the facility where the study was conducted were examined and calculations were made on a total of 1350 employees. As a result of the detailed study, Kıvanç Textile’s corporate carbon footprint for 2023 was calculated as a total of 68,746.86 tons CO2e. According to this data obtained, Kıvanç Textile emitted 50.92 tons of CO2e greenhouse gases per employee. At the same time, it was determined that the production in 2023 was 4,427,082 tons and a greenhouse gas emission of 15.53 tons of CO2e per production (ton) was calculated. This study also includes proposed strategies for reducing emissions. These strategies include energy efficiency measures, the use of renewable energy sources, waste reduction, and the adoption of efficient production processes. In conclusion, this article emphasizes the importance of efforts to measure and reduce greenhouse gas emissions in textile factories. Kıvanç Textile’s greenhouse gas measurements provide a fundamental reference for achieving sustainability goals in the sector. The data obtained will support the factory’s efforts to reduce its carbon footprint and minimize its environmental impacts. Full article
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<p>General process steps of Kıvanç Textile production.</p>
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<p>Localization of the Kıvanç Textile building.</p>
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<p>The GHG Protocol scopes establish the elements of the business carbon footprint.</p>
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<p>Distribution of electricity supply in 2023.</p>
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<p>Distribution of electricity consumption by months on an annual basis in 2023.</p>
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<p>Natural gas monthly distribution is detailed in 2023.</p>
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<p>Percentage distributions of refrigerant gas in 2023.</p>
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<p>Product-based distributions in 2023.</p>
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<p>Distribution of the CO<sub>2</sub>-eq by 5 scopes.</p>
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<p>Flow diagram of Kıvanç Textile production steps.</p>
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17 pages, 2766 KiB  
Article
Scenario-Based Modeling of Agricultural Nitrous Oxide Emissions in China
by Miaoling Bu, Weiming Xi, Yu Wang and Guofeng Wang
Agriculture 2024, 14(11), 2074; https://doi.org/10.3390/agriculture14112074 - 18 Nov 2024
Viewed by 770
Abstract
Agricultural land in China represents a major source of nitrous oxide (N2O) emissions, and as population growth and technological advancements drive agricultural intensification, these emissions are projected to increase. A thorough understanding of historical trends and future dynamics of these emissions [...] Read more.
Agricultural land in China represents a major source of nitrous oxide (N2O) emissions, and as population growth and technological advancements drive agricultural intensification, these emissions are projected to increase. A thorough understanding of historical trends and future dynamics of these emissions is critical for formulating effective mitigation strategies and advancing progress toward the Sustainable Development Goals. This study quantifies N2O emissions across 31 provinces in China from 2000 to 2021, employing the IPCC coefficient method alongside China’s provincial greenhouse gas inventory guidelines. The spatiotemporal evolution of emission intensities was examined, with the Stochastic Impacts by Regression on Population, Affluence, and Technology (STIRPAT) model employed to assess the influence of population, technological development, economic growth, and energy structure. The findings confirm that agricultural land remains the primary source of N2O emissions, with significantly higher levels observed in eastern coastal regions compared to western inland areas. Implementing targeted mitigation strategies, such as enhanced agricultural- and manure-management practices and region-specific interventions, is imperative to effectively curb the rising emission trends. Full article
(This article belongs to the Section Agricultural Economics, Policies and Rural Management)
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<p>Processes and key drivers of agricultural N<sub>2</sub>O production.</p>
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<p>Cumulative agricultural N<sub>2</sub>O emissions by province in periods from 2000 to 2021.</p>
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<p>Cumulative N<sub>2</sub>O emissions from agricultural sources by region and period (2000–2021).</p>
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<p>Intensity of agricultural N<sub>2</sub>O emissions per unit of agricultural value added and per unit of agricultural land area in 2000, 2010, and 2021.</p>
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<p>Trends in N<sub>2</sub>O emission intensity by province (2000–2021).</p>
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<p>Simulation of regional agricultural N<sub>2</sub>O gas emission scenarios.</p>
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16 pages, 3427 KiB  
Systematic Review
Slow-Release Fertilisers Control N Losses but Negatively Impact on Agronomic Performances of Pasture: Evidence from a Meta-Analysis
by Gunaratnam Abhiram
Nitrogen 2024, 5(4), 1058-1073; https://doi.org/10.3390/nitrogen5040068 - 17 Nov 2024
Viewed by 606
Abstract
High nitrogen (N) losses and low nitrogen utilisation efficiency (NUE) of conventional-nitrogen fertilisers (CNFs) are due to a mismatch between N-delivery and plant demand; thus, slow-release N fertilisers (SRNFs) are designed to improve the match. A quantitative synthesis is lacking to provide the [...] Read more.
High nitrogen (N) losses and low nitrogen utilisation efficiency (NUE) of conventional-nitrogen fertilisers (CNFs) are due to a mismatch between N-delivery and plant demand; thus, slow-release N fertilisers (SRNFs) are designed to improve the match. A quantitative synthesis is lacking to provide the overall assessment of SRNFs on pasture. This meta-analysis analyses application rate and type of SRNFs on N losses and agronomic performances with 65 data points from 14 studies in seven countries. Standardized mean difference of SRNFs for nitrate leaching losses and N2O emission were −0.87 and −0.69, respectively, indicating their effectiveness in controlling losses. Undesirably, SRNFs had a more negative impact on dry matter (DM) yield and NUE than CNFs. Subgroup analysis showed that SRNF type and application rate had an impact on all tested parameters. The biodegradable coating-type of SRNF outperformed other types in controlling N losses and improving agronomic performances. High application rates (>100 kg N ha−1) of SRNFs are more effective in controlling N losses. In conclusion, SRNFs are more conducive to controlling N losses, but they showed a negative impact on yield and NUE in pasture. Further studies are recommended to assess the efficacy of SRNFs developed using advanced technologies to understand their impact on pastoral agriculture. Full article
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<p>Schematic diagram for inclusion criteria of articles for this systematic review and meta-analysis (PRISMA) [<a href="#B32-nitrogen-05-00068" class="html-bibr">32</a>].</p>
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<p>The summary of the reported parameters from each study included in this meta-analysis [<a href="#B10-nitrogen-05-00068" class="html-bibr">10</a>,<a href="#B24-nitrogen-05-00068" class="html-bibr">24</a>,<a href="#B25-nitrogen-05-00068" class="html-bibr">25</a>,<a href="#B27-nitrogen-05-00068" class="html-bibr">27</a>,<a href="#B35-nitrogen-05-00068" class="html-bibr">35</a>,<a href="#B36-nitrogen-05-00068" class="html-bibr">36</a>,<a href="#B37-nitrogen-05-00068" class="html-bibr">37</a>,<a href="#B38-nitrogen-05-00068" class="html-bibr">38</a>,<a href="#B39-nitrogen-05-00068" class="html-bibr">39</a>,<a href="#B40-nitrogen-05-00068" class="html-bibr">40</a>,<a href="#B41-nitrogen-05-00068" class="html-bibr">41</a>,<a href="#B42-nitrogen-05-00068" class="html-bibr">42</a>,<a href="#B43-nitrogen-05-00068" class="html-bibr">43</a>,<a href="#B44-nitrogen-05-00068" class="html-bibr">44</a>].</p>
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<p>The nitrate leaching losses of conventional nitrogen fertilisers (CNFs) and slow-release nitrogen fertilisers (SRNFs) based on (<b>a</b>) SRNF types (PC—polymer coating, BC—biodegradable coating, IC—inorganic coating, and PCH—polymer chain), (<b>b</b>) fertiliser application rates (kg N/ha) and (<b>c</b>) overall studies. SMD stands for standard mean difference. Numbers next to range graph indicate the number of studies included for analysis.</p>
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<p>The correlation between effect size (standardized mean difference: SMD) and application rate of SRNFs for (<b>a</b>) nitrate leaching losses, (<b>b</b>) ammonium leaching losses, (<b>c</b>) N<sub>2</sub>O emission, (<b>d</b>) dry matter yield, (<b>e</b>) nitrogen utilisation efficiency (NUE) and (<b>f</b>) herbage nitrogen. Dark shade and light shades indicate a 95% confidence interval and a 95% prediction level, respectively.</p>
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<p>The effect of SRNF on ammonium leaching losses. SRNF and CNF refer to slow-release nitrogen fertiliser and conventional nitrogen fertiliser, respectively [<a href="#B10-nitrogen-05-00068" class="html-bibr">10</a>,<a href="#B27-nitrogen-05-00068" class="html-bibr">27</a>,<a href="#B36-nitrogen-05-00068" class="html-bibr">36</a>].</p>
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<p>The effect of SRNF on N<sub>2</sub>O emission. SRNF and CNF refer to slow-release nitrogen fertiliser and conventional nitrogen fertiliser, respectively [<a href="#B10-nitrogen-05-00068" class="html-bibr">10</a>,<a href="#B27-nitrogen-05-00068" class="html-bibr">27</a>,<a href="#B42-nitrogen-05-00068" class="html-bibr">42</a>,<a href="#B44-nitrogen-05-00068" class="html-bibr">44</a>].</p>
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<p>Dry matter yield of conventional nitrogen fertilisers (CNFs) and slow-release nitrogen fertilisers (SRNFs) based on (<b>a</b>) SRNF types (PC—polymer coating, BC—biodegradable coating, IC—inorganic coating, and PCH—polymer chain), (<b>b</b>) fertiliser application rates (kg N/ha), and (<b>c</b>) overall studies. SMD stands for standard mean difference. Numbers next to range graph indicate the number of studies included for analysis.</p>
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<p>The plant nutrient demand (PND) and nutrient delivery by slow-release nitrogen fertiliser (NDSRNF) for (<b>a</b>) other crops and (<b>b</b>) pasture. The blue shaded area shows the PND of pasture during continuous grass grazing.</p>
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<p>Herbage nitrogen (HN) in a pasture of conventional nitrogen fertilisers (CNFs) and slow-release nitrogen fertilisers (SRNFs) based on (<b>a</b>) SRNF types (PC—polymer coating, BC—biodegradable coating, IC—inorganic coating, and PCH—polymer chain), (<b>b</b>) fertiliser application rates (kg N/ha), and (<b>c</b>) overall studies. SMD stands for standard mean difference. Numbers next to range graph indicate the number of studies included for analysis.</p>
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<p>Nitrogen utilisation efficiency (NUE) in a pasture of conventional nitrogen fertilisers (CNFs) and slow-release nitrogen fertilisers (SRNFs) based on (<b>a</b>) SRNF types (PC—polymer coating, BC—biodegradable coating, IC—inorganic coating, and PCH—polymer chain), (<b>b</b>) fertiliser application rates (kg N/ha), and (<b>c</b>) overall studies. SMD stands for standard mean difference. Numbers next to range graph indicate the number of studies included for analysis.</p>
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