[go: up one dir, main page]

Next Issue
Volume 13, February-2
Previous Issue
Volume 13, January-2
 
 
water-logo

Journal Browser

Journal Browser

Water, Volume 13, Issue 3 (February-1 2021) – 146 articles

Cover Story (view full-size image): The red colored waters of the heavily modified Lake Koronia are caused by the huge numbers of Daphnia magna reaching the water surface during daytime. Daphnia species display high sensitivity to pollutants and adaptation to various environmental changes, and are thus considered biomarkers of environmental health. Under a great diversity of stressors, heat shock proteins (HSPs) and mitogen-activated protein kinases (MAPKs) can be triggered, providing benefits to develop stress resistance and adaptation. In our study, we present, for the first time, the expression HSPs and MAPKs in a Daphnia natural population and their role in the stress response to heavy environmental degradation. View this paper
  • Issues are regarded as officially published after their release is announced to the table of contents alert mailing list.
  • You may sign up for e-mail alerts to receive table of contents of newly released issues.
  • PDF is the official format for papers published in both, html and pdf forms. To view the papers in pdf format, click on the "PDF Full-text" link, and use the free Adobe Reader to open them.
Order results
Result details
Section
Select all
Export citation of selected articles as:
17 pages, 6042 KiB  
Article
Using Isotopic and Hydrochemical Indicators to Identify Sources of Sulfate in Karst Groundwater of the Niangziguan Spring Field, China
by Chunlei Tang, Hua Jin and Yongping Liang
Water 2021, 13(3), 390; https://doi.org/10.3390/w13030390 - 3 Feb 2021
Cited by 16 | Viewed by 5828
Abstract
Karst groundwater in the Niangziguan spring fields is the main source to supply domestic and industrial water demands in Yangquan City, China. However, the safety of water supply in this region has recently suffered from deteriorating quality levels. Therefore, identifying pollution sources and [...] Read more.
Karst groundwater in the Niangziguan spring fields is the main source to supply domestic and industrial water demands in Yangquan City, China. However, the safety of water supply in this region has recently suffered from deteriorating quality levels. Therefore, identifying pollution sources and causes is crucial for maintaining a reliable water supply. In this study, a systematic sample collection for the karst groundwater in the Niangziguan spring fields was implemented to identify hydrochemical characteristics of the karst groundwater through comprehensive analyses of hydrochemistry (piper diagram, and ion ratios,) and stable isotopes (S and H-O). The results show that the karst groundwater in the Niangziguan spring fields was categorized as SO4·HCO3-Ca·Mg, HCO3·SO4-Ca·Mg, and SO4-Ca types. K+, Cl-, and Na+ are mainly sourced from urban sewage and coal mine drainage. In addition, SO42− was mainly supplied by the dissolution of gypsum and the oxidation of FeS2 in coal-bearing strata. It is noteworthy that, based on H-O and S isotopes, 75% of the karst groundwater was contaminated by acidic water in coal mines at different degrees. In the groundwater of the Niangziguan spring field, the proportions of SO42− derived from FeS2 oxidation were 60.6% (N50, Chengxi spring), 30.3% (N51, Wulong spring), and 26.0% (N52, Four springs mixed with water). Acid mine drainage directly recharges and pollutes karst groundwater through faults or abandoned boreholes, or discharges to rivers, and indirectly pollutes karst groundwater through river infiltration in carbonate exposed areas. The main source of rapid increase of sulfate in karst groundwater is acid water from abandoned coal mines. Full article
(This article belongs to the Section Hydrology)
Show Figures

Figure 1

Figure 1
<p>Hydrogeological map of Niangziguan spring catchment.</p>
Full article ">Figure 2
<p>Box chart of ionic concentration in karst groundwater of Niangziguan spring catchment.</p>
Full article ">Figure 3
<p>Piper diagram of ionic concentrations in the karst groundwater.</p>
Full article ">Figure 4
<p>Box chart of ionic concentration in Acidic Mine Drainage (AMD).</p>
Full article ">Figure 5
<p>Box chart of ionic concentrations in the river.</p>
Full article ">Figure 6
<p>Piper diagram of ionic concentrations in the AMD or river.</p>
Full article ">Figure 7
<p>Box chart of stable isotopes in the AMD, river, or karst groundwater.</p>
Full article ">Figure 8
<p>Box chart of K<sup>+</sup>, Na<sup>+</sup>, and Cl<sup>−</sup>.</p>
Full article ">Figure 9
<p>Relationships between (<b>a</b>) K<sup>+</sup> vs. Cl<sup>−</sup> in karst groundwater (<b>b</b>) Na<sup>+</sup> vs. Cl<sup>−</sup> in karst groundwater.</p>
Full article ">Figure 10
<p>(<b>a</b>) Relationships between Mg<sup>2+</sup> vs. Ca<sup>2+</sup> (<b>b</b>) Relationships between SO<sub>4</sub><sup>2+</sup> vs. Ca<sup>2+</sup>.</p>
Full article ">Figure 11
<p>Relationships between SO<sub>4</sub><sup>2−</sup> vs. Mg<sup>2+</sup>.</p>
Full article ">Figure 12
<p>Ion relationship involving karst groundwater in the Niangziguan Spring Catchment (<b>a</b>) Relationships between Mg<sup>2+</sup> vs. SO<sub>4</sub><sup>2−</sup>, (<b>b</b>) SO<sub>4</sub><sup>2−</sup>+HCO<sub>3</sub><sup>−</sup> vs. Ca<sup>2+</sup>+Mg<sup>2+</sup>, (<b>c</b>) Na<sup>+</sup>+K<sup>+</sup>-Cl<sup>−</sup> vs. Ca<sup>2+</sup>+Mg<sup>2+</sup>-SO<sub>4</sub><sup>2+</sup>-CO<sub>3</sub><sup>−</sup>, (<b>d</b>) Ca<sup>2+</sup>/Na<sup>+</sup> vs. HCO<sub>3</sub><sup>−</sup>/Na<sup>+</sup>.</p>
Full article ">Figure 13
<p>Relationships between TDS vs. SO<sub>4</sub><sup>2−</sup>.</p>
Full article ">Figure 14
<p>Relationships between <span class="html-italic">δ</span>D vs. <span class="html-italic">δ</span><sup>18</sup>O for the karst groundwater.</p>
Full article ">Figure 15
<p>Box chart of SO<sub>4</sub><sup>2−</sup>.</p>
Full article ">Figure 16
<p>Box chart of <span class="html-italic">δ</span><sup>34</sup>S values of SO<sub>4</sub><sup>2−</sup> forming the dissolution of gypsum and forming the oxidation of FeS<sub>2.</sub></p>
Full article ">
23 pages, 5575 KiB  
Article
Structural Changes in French VF Treatment Wetland Porous Media during the Rest Period: An Ex Situ Study Using X-ray Tomography
by German Dario Martinez-Carvajal, Laurent Oxarango, Jérôme Adrien, Pascal Molle and Nicolas Forquet
Water 2021, 13(3), 389; https://doi.org/10.3390/w13030389 - 2 Feb 2021
Viewed by 2308
Abstract
Clogging constitutes a major operational issue for treatment wetlands. The rest period is a key feature of French Vertical Flow (VF) treatment wetlands and serves to mitigate clogging. An ex-situ drying experiment was performed to mimic the rest period and record structural changes [...] Read more.
Clogging constitutes a major operational issue for treatment wetlands. The rest period is a key feature of French Vertical Flow (VF) treatment wetlands and serves to mitigate clogging. An ex-situ drying experiment was performed to mimic the rest period and record structural changes in the porous media using X-ray Computed Tomography (CT). Samples containing the deposit and gravel layers of a first stage French VF treatment wetland were extracted and left to dry in a control environment. Based on CT scans, three phases were identified (voids, biosolids, and gravels). The impact of the rest period was assessed by means of different pore-scale variables. Ultimately, the volume of biosolids had reduced to 58% of its initial value, the deposit layer thickness dropped to 68% of its initial value, and the void/biosolid specific surface area ratio increased from a minimum value of 1.1 to a maximum of 4.2. Cracks greater than 3 mm developed at the uppermost part of the deposit layer, while, in the gravel layer, the rise in void volume corresponds to pores smaller than 2 mm in diameter. Lastly, the air-filled microporosity is estimated to have increased by 0.11 v/v. Full article
(This article belongs to the Section Wastewater Treatment and Reuse)
Show Figures

Graphical abstract

Graphical abstract
Full article ">Figure 1
<p>A sketch of the drying chamber.</p>
Full article ">Figure 2
<p>Mass changes vs. time (<b>left</b>), cumulative mass losses (<b>top right</b>) and evaporation rates (<b>bottom right</b>) during the experiment.</p>
Full article ">Figure 3
<p>Horizontal slices in the deposit layer (<b>a</b>–<b>c</b>) and in the gravel layer (<b>d</b>–<b>f</b>) for MON1 sample. (<b>a</b>) MON1, deposit layer (day 0, height = 116 mm), (<b>b</b>) MON1, deposit layer (day 3, height = 115 mm), (<b>c</b>) MON1, deposit layer (day 10, height = 112 mm), (<b>d</b>) MON1, gravel layer (day 0, height = 33 mm), (<b>e</b>) MON1, gravel layer (day 3, height = 33 mm), (<b>f</b>) MON1, gravel layer (day 10, height = 33 mm).</p>
Full article ">Figure 4
<p>Evolution of vertical phase volume fraction profiles and snapshot on a vertical slice of the 3D scan. Computation were performed for a ROI of 60%. (<b>a</b>) MON1, day 0, (<b>b</b>) MON1, day 3, (<b>c</b>) MON1, day 10, (<b>d</b>) MON2, day 0, (<b>e</b>) MON2, day 3, (<b>f</b>) MON2, day 10, (<b>g</b>) MON3, day 0, (<b>h</b>) MON3, day 3, (<b>i</b>) MON3, day 10.</p>
Full article ">Figure 5
<p>Evolution of the void phase volume fraction profiles. The deposit layer is represented by a wider trace in the curves. Computations were performed for a region of interest (ROI) of 60%. (<b>a</b>) MON1, (<b>b</b>) MON2, (<b>c</b>) MON3.</p>
Full article ">Figure 6
<p>Cumulative Pore Size Distributions (PSD) associated to snapshots highlighting the ROI on which computation are performed (on the right). (<b>a</b>) MON1, gravel layer, (<b>b</b>) MON1, deposit layer ROI = 100%, (<b>c</b>) MON1, deposit layer ROI = 60%, (<b>d</b>) MON2, gravel layer, (<b>e</b>) MON2, deposit layer ROI = 100%, (<b>f</b>) MON 2, deposit layer ROI = 60%, (<b>g</b>) MON3, gravel layer, (<b>h</b>) MON3, deposit layer ROI = 100%, (<b>i</b>) MON3, deposit layer ROI = 60%.</p>
Full article ">Figure 7
<p>Specific Surface Areas (SSA) profiles. The deposit layer is represented by a wider trace in the curves. Computations were performed for a ROI of 60%. (<b>a</b>) MON1, (<b>b</b>) MON2, (<b>c</b>) MON3.</p>
Full article ">Figure 8
<p>Cumulative void phase connectivity profiles: computations were performed for an ROI of 60%.</p>
Full article ">Figure 9
<p>Comparison of mass and volume losses.</p>
Full article ">Figure A1
<p>Evolution of deposit and gravel layer thicknesses during the drying experiment: computations were performed for an ROI of 60%.</p>
Full article ">
20 pages, 11514 KiB  
Article
Neural Network Approach to Retrieving Ocean Subsurface Temperatures from Surface Parameters Observed by Satellites
by Hao Cheng, Liang Sun and Jiagen Li
Water 2021, 13(3), 388; https://doi.org/10.3390/w13030388 - 2 Feb 2021
Cited by 18 | Viewed by 4057
Abstract
The extraction of physical information about the subsurface ocean from surface information obtained from satellite measurements is both important and challenging. We introduce a back-propagation neural network (BPNN) method to determine the subsurface temperature of the North Pacific Ocean by selecting the optimum [...] Read more.
The extraction of physical information about the subsurface ocean from surface information obtained from satellite measurements is both important and challenging. We introduce a back-propagation neural network (BPNN) method to determine the subsurface temperature of the North Pacific Ocean by selecting the optimum input combination of sea surface parameters obtained from satellite measurements. In addition to sea surface height (SSH), sea surface temperature (SST), sea surface salinity (SSS) and sea surface wind (SSW), we also included the sea surface velocity (SSV) as a new component in our study. This allowed us to partially resolve the non-linear subsurface dynamics associated with advection, which improved the estimated results, especially in regions with strong currents. The accuracy of the estimated results was verified with reprocessed observational datasets. Our results show that the BPNN model can accurately estimate the subsurface (upper 1000 m) temperature of the North Pacific Ocean. The corresponding mean square errors were 0.868 and 0.802 using four (SSH, SST, SSS and SSW) and five (SSH, SST, SSS, SSW and SSV) input parameters and the average coefficients of determination were 0.952 and 0.967, respectively. The input of the SSV in addition to the SSH, SST, SSS and SSW therefore has a positive impact on the BPNN model and helps to improve the accuracy of the estimation. This study provides important technical support for retrieving thermal information about the ocean interior from surface satellite remote sensing observations, which will help to expand the scope of satellite measurements of the ocean. Full article
(This article belongs to the Section Oceans and Coastal Zones)
Show Figures

Figure 1

Figure 1
<p>Surface parameters and temperature at 500 m depth in the study area with a spatial resolution of 0.25° × 0.25° in March 2015. The sea surface wind (SSW)<sub>u</sub>, SSW<sub>v</sub>, sea surface velocity (SSV)<sub>u</sub> and SSV<sub>v</sub> are the meridional and latitudinal components of the SSW and SSV, respectively.</p>
Full article ">Figure 2
<p>Flow chart of the back-propagation neural network (BPNN) approach for the estimation of subsurface temperatures at different depths (e.g., 500 m depth). The sea surface height (SSH), sea surface temperature (SST), sea surface salinity (SSS), SSW and SSV datasets were used for training and the SSH<sub>p</sub>, SST<sub>p</sub>, SSS<sub>p</sub>, SSW<sub>p</sub> and SSV<sub>p</sub> datasets were used for estimation.</p>
Full article ">Figure 3
<p>Estimated temperature based on five sea surface parameters (SSH, SST, SSS, SSW and SSV) compared with the observed temperature at different depths (<b>a1</b>) and (<b>a2</b>) for 100 m; (<b>b1</b>) and (<b>b2</b>) for 300 m; (<b>c1</b>) and (<b>c2</b>) for 500 m; (<b>d1</b>) and (<b>d2</b>) for 700 m; (<b>e1</b>) and (<b>e2</b>) for 1000 m) in the North Pacific Ocean (NPO) during January 2015.</p>
Full article ">Figure 4
<p>Estimated temperature based on five sea surface parameters (SSH, SST, SSS, SSW, SSV) compared with the observed temperature at different depth levels (<b>a1</b>) and (<b>a2</b>) for 100 m; (<b>b1</b>) and (<b>b2</b>) for 300 m; (<b>c1</b>) and (<b>c2</b>) for 500 m; (<b>d1</b>) and (<b>d2</b>) for 700 m; (<b>e1</b>) and (<b>e2</b>) for 1000 m) in the NPO during July 2015.</p>
Full article ">Figure 5
<p>Evaluation of the accuracy of the temperature estimation results at 16 different depths in the NPO based on the BPNN model. MSE5 and MSE4 are the MSE for the five- and four-parameter BPNN model; <span class="html-italic">R</span>²<sub>5</sub> and <span class="html-italic">R</span>²<sub>4</sub> are <span class="html-italic">R</span>² for the five- and four-parameter BPNN model, respectively.</p>
Full article ">Figure 6
<p>Density scatter plots of the correlation between the temperature estimated by the five-parameter BPNN model and the observed temperature at different depths (<b>a</b>) for 200 m; (<b>b</b>) for 400 m; (<b>c</b>) for 600 m; (<b>d</b>) for 800 m.</p>
Full article ">Figure 7
<p>Vertical temperature profiles (VTP) ((<b>a</b>) for case (a); (<b>b</b>) for case (b); (<b>c</b>) for case (c); (<b>d</b>) for case (d)) of four randomly selected pixels at 16 different depths during March 2015.</p>
Full article ">Figure 8
<p>(<b>a</b>–<b>g</b>) are surface parameters around case (<b>a</b>) and (<b>h</b>–<b>i</b>) are VTP with the four- and five-parameter models during March 2015.</p>
Full article ">Figure 9
<p>(<b>a</b>–<b>g</b>) are surface parameters around case (<b>b</b>) and (<b>h</b>–<b>i</b>) are VTP with the four- and five-parameter models during March 2015.</p>
Full article ">Figure 10
<p>Temperature fields at 100, 300 and 500 m depth in four seasons (using January, April, July and October to represent winter, spring, summer and autumn).</p>
Full article ">
17 pages, 2280 KiB  
Article
Plasticity in Reproductive Traits, Condition and Energy Allocation of the Non-Native Pyrenean Gudgeon Gobio lozanoi in a Highly Regulated Mediterranean River Basin
by Fátima Amat-Trigo, Mar Torralva, Daniel González-Silvera, Francisco Javier Martínez-López and Francisco José Oliva-Paterna
Water 2021, 13(3), 387; https://doi.org/10.3390/w13030387 - 2 Feb 2021
Cited by 3 | Viewed by 2666
Abstract
The invasion success of non-native fish, such as Pyrenean gudgeon Gobio lozanoi in several Iberian rivers, is often explained by the expression of its life history traits. This study provides the first insights into the reproductive traits, fish condition, and energy allocation (protein [...] Read more.
The invasion success of non-native fish, such as Pyrenean gudgeon Gobio lozanoi in several Iberian rivers, is often explained by the expression of its life history traits. This study provides the first insights into the reproductive traits, fish condition, and energy allocation (protein and lipid contents of tissues) of this species, along a longitudinal gradient in one of the most regulated river basins in the Iberian Peninsula, the Segura river. Larger sizes of first maturity, higher fecundity and larger oocytes were found in fluvial sectors with the most natural flow regimes, characterised by a low base flow with high flow peaks in spring and autumn. A delay in the reproductive period, lower fish condition and no differences in sex-ratio were observed in fluvial sectors with a high increase in base flow and notable inversion in the seasonal pattern of flow regime. Lipid contents in the liver and gonads were stable during the reproductive cycle and decreases in muscle were noted, whereas ovarian and liver proteins increased. In relation to energy allocation for G. lozanoi, an intermediate energy strategy was observed between income and capital breeding. Our results support the hypothesis that the high plasticity of G. lozanoi population traits plays a significant role in its success in a highly regulated Mediterranean river basin. Understanding the mechanisms by which flow regulation shapes fish populations in Mediterranean type-rivers could inform management actions. Full article
(This article belongs to the Special Issue Ecology and Conservation of Freshwater Fishes Biodiversity)
Show Figures

Figure 1

Figure 1
<p>Sampling sites location for <span class="html-italic">Gobio lozanoi</span> in the Segura River basin at south-eastern Iberian Peninsula, Spain.</p>
Full article ">Figure 2
<p>Temporal variation in gonad activity (predicted <span class="html-italic">M</span><sub>G</sub> values, <span class="html-italic">M</span><sub>G</sub> is gonad mass) along the study period for the five studied populations (TUS, SE1, SE2, SE3 and SE4) for both sexes of <span class="html-italic">Gobio lozanoi</span>. The lines represent the adjusted model <span class="html-italic">Loess</span> for each population.</p>
Full article ">Figure 3
<p>Mean predicted <span class="html-italic">M</span><sub>G,</sub> <span class="html-italic">M</span><sub>E</sub> and <span class="html-italic">M</span><sub>H</sub> values by ANCOVA (<span class="html-italic">L</span><sub>F</sub> as covariate) in each reproductive stage (quiescence, maturation, spawning and postspawning) for both sexes of <span class="html-italic">Gobio lozanoi</span>. Letters show significant differences (Welch’s analysis of variance <span class="html-italic">p</span> &lt; 0.05 and T3 of Dunnett post hoc tests) among reproductive stages in females (capital letters) and in males (lowercase letters).</p>
Full article ">Figure 4
<p>Predicted probability of maturity according to fork length for females and males for the five studied populations (TUS, SE1, SE2, SE3 and SE4) of <span class="html-italic">Gobio lozanoi</span>.</p>
Full article ">Figure 5
<p>Estimated marginal means (by ANCOVA) ± IC 95% at 9.0 cm of fork length for oocyte number and diameter of opaque plus vitelogenic oocytes (potential fecundity; white bars), and of vitelogenic oocytes (absolute fecundity; grey bars) and oocytes of batch fecundity (dark grey bars). Letters show significant differences (ANCOVA, Bonferroni post hoc tests) among sampling sites.</p>
Full article ">Figure 6
<p>Mean and ± IC 95% percentages of proteins and lipids in muscle, liver and gonads by reproductive stages. White bars represent female values and grey bars represent the male ones. The letters show significant differences (ANOVA, <span class="html-italic">p</span> &lt; 0.05) among reproductive stages by post hoc comparison Tukey test. Capital letters for female data and lower case letters for male data.</p>
Full article ">
19 pages, 7039 KiB  
Article
Did the Construction of the Bhumibol Dam Cause a Dramatic Reduction in Sediment Supply to the Chao Phraya River?
by Matharit Namsai, Warit Charoenlerkthawin, Supakorn Sirapojanakul, William C. Burnett and Butsawan Bidorn
Water 2021, 13(3), 386; https://doi.org/10.3390/w13030386 - 2 Feb 2021
Cited by 9 | Viewed by 4950
Abstract
The Bhumibol Dam on Ping River, Thailand, was constructed in 1964 to provide water for irrigation, hydroelectric power generation, flood mitigation, fisheries, and saltwater intrusion control to the Great Chao Phraya River basin. Many studies, carried out near the basin outlet, have suggested [...] Read more.
The Bhumibol Dam on Ping River, Thailand, was constructed in 1964 to provide water for irrigation, hydroelectric power generation, flood mitigation, fisheries, and saltwater intrusion control to the Great Chao Phraya River basin. Many studies, carried out near the basin outlet, have suggested that the dam impounds significant sediment, resulting in shoreline retreat of the Chao Phraya Delta. In this study, the impact of damming on the sediment regime is analyzed through the sediment variation along the Ping River. The results show that the Ping River drains a mountainous region, with sediment mainly transported in suspension in the upper and middle reaches. By contrast, sediment is mostly transported as bedload in the lower basin. Variation of long-term total sediment flux data suggests that, while the Bhumibol Dam does effectively trap sediment, there was only a 5% reduction in sediment supply to the Chao Phraya River system because of sediment additions downstream. Full article
Show Figures

Figure 1

Figure 1
<p>Map of the Chao Phraya River Basin, Thailand: (<b>a</b>) Ping River Basin and location of the Bhumibol Dam, the largest dam in the Chao Phraya River system; (<b>b</b>) locations of observation sites and hydrological stations operated by the Royal Irrigation Department (RID) and the Electricity Generating Authority of Thailand (EGAT).</p>
Full article ">Figure 2
<p>Longitudinal profile of the Ping River showing locations of RID hydrological stations (red triangles) and observation sites (grey diamonds). The zero mark on the <span class="html-italic">x</span>-axis represents the confluence of the Ping and Nan Rivers.</p>
Full article ">Figure 3
<p>Time series of annual runoff at hydrological stations along the Ping River between 1921 and 2019.</p>
Full article ">Figure 4
<p>Time series data of annual suspended sediment load at RID hydrological stations along the Ping River between 1965 and 2019.</p>
Full article ">Figure 5
<p>Observations along the Ping River during 2019: (<b>a</b>) river discharge; (<b>b</b>) median size bed material (d<sub>50</sub>); (<b>c</b>) suspended sediment load and bedload.</p>
Full article ">Figure 6
<p>Plots of average annual river runoff and annual total sediment load along the Ping River and C.2 between 1999 and 2019.</p>
Full article ">Figure 7
<p>Cumulative annual runoff and total sediment load of the Ping River: (<b>a</b>) P.1; (<b>b</b>) P.17; (<b>c</b>) C.2.; the green and red points represent the data during the pre- and post-construction of the Bhumibol Dam, respectively.</p>
Full article ">Figure 8
<p>Time series of total sediment at Stations P.1, P.17 and C.2.</p>
Full article ">Figure 9
<p>Location of sand mines along the Ping River.</p>
Full article ">
22 pages, 5528 KiB  
Article
Physicochemical Interactions in Systems C.I. Direct Yellow 50—Weakly Basic Resins: Kinetic, Equilibrium, and Auxiliaries Addition Aspects
by Monika Wawrzkiewicz and Ewelina Polska-Adach
Water 2021, 13(3), 385; https://doi.org/10.3390/w13030385 - 2 Feb 2021
Cited by 11 | Viewed by 3901
Abstract
Intensive development of many industries, including textile, paper or plastic, which consume large amounts of water and generate huge amounts of wastewater-containing toxic dyes, contribute to pollution of the aquatic environment. Among many known methods of wastewater treatment, adsorption techniques are considered the [...] Read more.
Intensive development of many industries, including textile, paper or plastic, which consume large amounts of water and generate huge amounts of wastewater-containing toxic dyes, contribute to pollution of the aquatic environment. Among many known methods of wastewater treatment, adsorption techniques are considered the most effective. In the present study, the weakly basic anion exchangers such as Amberlyst A21, Amberlyst A23 and Amberlyst A24 of the polystyrene, phenol-formaldehyde and polyacrylic matrices were used for C.I. Direct Yellow 50 removal from aqueous solutions. The equilibrium adsorption data were well fitted to the Langmuir adsorption isotherm. Kinetic studies were described by the pseudo-second order model. The pseudo-second order rate constants were in the range of 0.0609–0.0128 g/mg·min for Amberlyst A24, 0.0038–0.0015 g/mg·min for Amberlyst A21 and 1.1945–0.0032 g/mg·min for Amberlyst A23, and decreased with the increasing initial concentration of dye from 100–500 mg/L, respectively. There were observed auxiliaries (Na2CO3, Na2SO4, anionic and non-ionic surfactants) impact on the dye uptake. The polyacrylic resin Amberlyst A24 can be promising sorbent for C.I. Direct Yellow 50 removal as it is able to uptake 666.5 mg/g of the dye compared to the phenol-formaldehyde Amberlyst A23 which has a 284.3 mg/g capacity. Full article
(This article belongs to the Special Issue New Aspects of Occurrence and Removal of Emerging Pollutants)
Show Figures

Graphical abstract

Graphical abstract
Full article ">Figure 1
<p>Application of dyes and their impact on living organisms and human body [<a href="#B11-water-13-00385" class="html-bibr">11</a>,<a href="#B12-water-13-00385" class="html-bibr">12</a>,<a href="#B13-water-13-00385" class="html-bibr">13</a>].</p>
Full article ">Figure 2
<p>Physicochemical properties of the anion exchangers [<a href="#B52-water-13-00385" class="html-bibr">52</a>,<a href="#B53-water-13-00385" class="html-bibr">53</a>] and dye.</p>
Full article ">Figure 3
<p>Influence of phase contact time and initial concentrations of DY50 on the amount of dye adsorbed by (<b>a</b>) A21, (<b>b</b>) A23 and (<b>c</b>) A24 resins and the fitting of experimental data to the kinetic models.</p>
Full article ">Figure 3 Cont.
<p>Influence of phase contact time and initial concentrations of DY50 on the amount of dye adsorbed by (<b>a</b>) A21, (<b>b</b>) A23 and (<b>c</b>) A24 resins and the fitting of experimental data to the kinetic models.</p>
Full article ">Figure 4
<p>The <span class="html-italic">t</span>/<span class="html-italic">q<sub>t</sub></span> vs. <span class="html-italic">t</span> dependences determined from the linear form of the PSO model in (<b>a</b>) DY50—A24, (<b>b</b>) DY50—A24 and (<b>c</b>) DY50—A24 systems.</p>
Full article ">Figure 4 Cont.
<p>The <span class="html-italic">t</span>/<span class="html-italic">q<sub>t</sub></span> vs. <span class="html-italic">t</span> dependences determined from the linear form of the PSO model in (<b>a</b>) DY50—A24, (<b>b</b>) DY50—A24 and (<b>c</b>) DY50—A24 systems.</p>
Full article ">Figure 5
<p>Intraparticle diffusion model applied for adsorption of DY50 on (<b>a</b>) A21, (<b>b</b>) A23 and (<b>c</b>) A24.</p>
Full article ">Figure 6
<p>The effects of (<b>a</b>) Na<sub>2</sub>CO<sub>3</sub> and (<b>b</b>) Na<sub>2</sub>SO<sub>4</sub> presence on DY50 adsorption on A21, A23 and A24 anion exchangers.</p>
Full article ">Figure 7
<p>The effects of (<b>a</b>) anionic SDS and (<b>b</b>) non-ionic TX-100 surfactants presence on DY50 adsorption on A21, A23 and A24 anion exchangers.</p>
Full article ">Figure 8
<p>Fitting of the experimental data to the Langmuir and Freundlich isotherm models in the (<b>a</b>) DY50-A21, (<b>b</b>) DY50-A23 and (<b>c</b>) DY50-A24 systems as well as (<b>d</b>) the dimensionless separation factor as a function of DY50 initial concentration.</p>
Full article ">Figure 9
<p>Proposed mechanism of DY50 interaction with the weakly basic anion exchangers of the polystyrene, phenol-formaldehyde and polyacrylic matrices.</p>
Full article ">Figure 10
<p>ATR–FT-IR spectra of (<b>a</b>) A21 and (<b>b</b>) A24 before and after sorption of DY50.</p>
Full article ">Figure 11
<p>Influence of initial solution pH on DY50 uptake by the A21, A23 and A24 anion exchangers.</p>
Full article ">Figure 12
<p>Desorption effectiveness of DY50 from the A21, A23 and A24 anion exchangers.</p>
Full article ">
23 pages, 1947 KiB  
Article
Influence of the Drag Force on the Average Absorbed Power of Heaving Wave Energy Converters Using Smoothed Particle Hydrodynamics
by Nicolas Quartier, Pablo Ropero-Giralda, José M. Domínguez, Vasiliki Stratigaki and Peter Troch
Water 2021, 13(3), 384; https://doi.org/10.3390/w13030384 - 2 Feb 2021
Cited by 23 | Viewed by 4637
Abstract
In this paper, we investigated how the added mass, the hydrodynamic damping and the drag coefficient of a Wave Energy Converter (WEC) can be calculated using DualSPHysics. DualSPHysics is a software application that applies the Smoothed Particle Hydrodynamics (SPH) method, a Lagrangian meshless [...] Read more.
In this paper, we investigated how the added mass, the hydrodynamic damping and the drag coefficient of a Wave Energy Converter (WEC) can be calculated using DualSPHysics. DualSPHysics is a software application that applies the Smoothed Particle Hydrodynamics (SPH) method, a Lagrangian meshless method used in a growing range of applications within the field of Computational Fluid Dynamics (CFD). Furthermore, the effect of the drag force on the WEC’s motion and average absorbed power is analyzed. Particularly under controlled conditions and in the resonance region, the drag force becomes significant and can greatly reduce the average absorbed power of a heaving point absorber. Once the drag coefficient has been determined, it is used in a modified equation of motion in the frequency domain, taking into account the effect of the drag force. Three different methods were compared for the calculation of the average absorbed power: linear potential flow theory, linear potential flow theory modified to take the drag force into account and DualSPHysics. This comparison showed the considerable effect of the drag force in the resonance region. Calculations of the drag coefficient were carried out for three point absorber WECs: one spherical WEC and two cylindrical WECs. Simulations in regular waves were performed for one cylindrical WEC with two different power take-off (PTO) systems: a linear damping and a Coulomb damping PTO system. The Coulomb damping PTO system was added in the numerical coupling between DualSPHysics and Project Chrono. Furthermore, we considered the optimal PTO system damping coefficient taking the effect of the drag force into account. Full article
Show Figures

Figure 1

Figure 1
<p>Schematic overview of the applied theories and equations in the current study.</p>
Full article ">Figure 2
<p>Schematic overview of different drag forces acting on the Wave Energy Converter (WEC).</p>
Full article ">Figure 3
<p>Vorticity in DualSPHysics surrounding a heaving cylindrical WEC in regular waves with <math display="inline"><semantics> <mrow> <mi>H</mi> <mo>=</mo> <mn>0.16</mn> </mrow> </semantics></math> m, <math display="inline"><semantics> <mrow> <mi>T</mi> <mo>=</mo> <mn>1.5</mn> </mrow> </semantics></math> s, <math display="inline"><semantics> <mrow> <msub> <mi>B</mi> <mrow> <mi>P</mi> <mi>T</mi> <mi>O</mi> <mo>,</mo> <mi>l</mi> </mrow> </msub> <mo>=</mo> <mn>1100</mn> </mrow> </semantics></math> Ns/m (<b>left</b>), compared to experimental measurements of the heaving WEC, as performed in [<a href="#B56-water-13-00384" class="html-bibr">56</a>] (<b>right</b>).</p>
Full article ">Figure 4
<p>Vertical force <math display="inline"><semantics> <msub> <mi>F</mi> <mi>z</mi> </msub> </semantics></math> acting on a sphere with prescribed heave motion, <math display="inline"><semantics> <mrow> <mi>a</mi> <mo>=</mo> <mn>1.5</mn> </mrow> </semantics></math> m <math display="inline"><semantics> <mrow> <mi>T</mi> <mo>=</mo> <mn>9</mn> </mrow> </semantics></math> s.</p>
Full article ">Figure 5
<p>Dimensions of the numerical wave basin for hydrodynamic coefficients and drag coefficient test for a heaving sphere.</p>
Full article ">Figure 6
<p>Hydrodynamic coefficients <math display="inline"><semantics> <msub> <mi>A</mi> <mn>33</mn> </msub> </semantics></math> and <math display="inline"><semantics> <msub> <mi>B</mi> <mn>33</mn> </msub> </semantics></math> calculated with NEMOH and with Smoothed Particle Hydrodynamics (SPH)–DualSPHysics for a sphere with a diameter of 5 m.</p>
Full article ">Figure 7
<p>Convergence test for drag coefficient <math display="inline"><semantics> <msub> <mi>C</mi> <mi>d</mi> </msub> </semantics></math> using a varying resolution for (i) a sphere with <math display="inline"><semantics> <mrow> <mi>a</mi> <mo>=</mo> <mn>1.5</mn> </mrow> </semantics></math> m, <math display="inline"><semantics> <mrow> <mi>T</mi> <mo>=</mo> <mn>9</mn> </mrow> </semantics></math> s [<a href="#B32-water-13-00384" class="html-bibr">32</a>], (ii) a cylinder with <math display="inline"><semantics> <mrow> <mi>a</mi> <mo>=</mo> <mn>0.045</mn> </mrow> </semantics></math> m, <math display="inline"><semantics> <mrow> <mi>T</mi> <mo>=</mo> <mn>1.5</mn> </mrow> </semantics></math> s (cylinder1, [<a href="#B56-water-13-00384" class="html-bibr">56</a>]) and a cylinder with <math display="inline"><semantics> <mrow> <mi>a</mi> <mo>=</mo> <mn>0.1</mn> </mrow> </semantics></math> m, <math display="inline"><semantics> <mrow> <mi>T</mi> <mo>=</mo> <mn>1.2</mn> </mrow> </semantics></math> s (cylinder2, [<a href="#B34-water-13-00384" class="html-bibr">34</a>]).</p>
Full article ">Figure 8
<p>Dimensions of a basin for a heaving cylindrical WEC in waves with <math display="inline"><semantics> <mrow> <mi>T</mi> <mo>=</mo> <mn>1.2</mn> </mrow> </semantics></math> s in DualSPHysics.</p>
Full article ">Figure 9
<p>Response amplitude operator (RAO) for the cylindrical WEC cylinder2 without a power take-off (PTO) system, calculated with (i) linear potential flow theory with <math display="inline"><semantics> <msub> <mi>C</mi> <mi>d</mi> </msub> </semantics></math> = 0.0, (ii) linear potential flow theory with <math display="inline"><semantics> <msub> <mi>C</mi> <mi>d</mi> </msub> </semantics></math> = 1.5, (iii) SPH–DualSPHysics and (iv) obtained from experiments [<a href="#B34-water-13-00384" class="html-bibr">34</a>], <span class="html-italic">H</span> = 0.08 m.</p>
Full article ">Figure 10
<p>Average absorbed power of cylinder2 with (<b>a</b>) a linear damping PTO system and (<b>b</b>) a Coulomb damping PTO system for a range of PTO system damping coefficients, calculated with linear potential flow theory with (i) <math display="inline"><semantics> <msub> <mi>C</mi> <mi>d</mi> </msub> </semantics></math> = 0.00, (ii) <math display="inline"><semantics> <msub> <mi>C</mi> <mi>d</mi> </msub> </semantics></math> = 1.50 and (iii) with DualSPHysics—<math display="inline"><semantics> <mrow> <mi>H</mi> <mo>=</mo> <mn>0.15</mn> </mrow> </semantics></math> m, <math display="inline"><semantics> <mrow> <mi>T</mi> <mo>=</mo> <mn>1.2</mn> </mrow> </semantics></math> s.</p>
Full article ">Figure 11
<p>Velocity of cylinder2 with (<b>a</b>) a linear damping PTO system, <math display="inline"><semantics> <mrow> <msub> <mi>B</mi> <mrow> <mi>P</mi> <mi>T</mi> <mi>O</mi> <mo>,</mo> <mi>l</mi> </mrow> </msub> <mo>=</mo> <mn>25</mn> </mrow> </semantics></math> Ns/m and (<b>b</b>) a Coulomb damping PTO system, <math display="inline"><semantics> <mrow> <msub> <mi>B</mi> <mrow> <mi>P</mi> <mi>T</mi> <mi>O</mi> <mo>,</mo> <mi>c</mi> </mrow> </msub> <mo>=</mo> <mn>10</mn> <mi>N</mi> </mrow> </semantics></math> calculated with linear potential flow theory with (i) <math display="inline"><semantics> <msub> <mi>C</mi> <mi>d</mi> </msub> </semantics></math> = 0.00, (ii) <math display="inline"><semantics> <msub> <mi>C</mi> <mi>d</mi> </msub> </semantics></math> = 1.50 and (iii) with DualSPHysics—<math display="inline"><semantics> <mrow> <mi>H</mi> <mo>=</mo> <mn>0.15</mn> </mrow> </semantics></math> m, <math display="inline"><semantics> <mrow> <mi>T</mi> <mo>=</mo> <mn>1.2</mn> </mrow> </semantics></math> s.</p>
Full article ">
18 pages, 2741 KiB  
Article
Optimization of the Groundwater Remediation Process Using a Coupled Genetic Algorithm-Finite Difference Method
by S. M. Seyedpour, I. Valizadeh, P. Kirmizakis, R. Doherty and T. Ricken
Water 2021, 13(3), 383; https://doi.org/10.3390/w13030383 - 1 Feb 2021
Cited by 13 | Viewed by 3881
Abstract
In situ chemical oxidation using permanganate as an oxidant is a remediation technique often used to treat contaminated groundwater. In this paper, groundwater flow with a full hydraulic conductivity tensor and remediation process through in situ chemical oxidation are simulated. The numerical approach [...] Read more.
In situ chemical oxidation using permanganate as an oxidant is a remediation technique often used to treat contaminated groundwater. In this paper, groundwater flow with a full hydraulic conductivity tensor and remediation process through in situ chemical oxidation are simulated. The numerical approach was verified with a physical sandbox experiment and analytical solution for 2D advection-diffusion with a first-order decay rate constant. The numerical results were in good agreement with the results of physical sandbox model and the analytical solution. The developed model was applied to two different studies, using multi-objective genetic algorithm to optimise remediation design. In order to reach the optimised design, three objectives considering three constraints were defined. The time to reach the desired concentration and remediation cost regarding the number of required oxidant sources in the optimised design was less than any arbitrary design. Full article
(This article belongs to the Special Issue Modeling and Prediction of Groundwater Contaminant Plumes)
Show Figures

Figure 1

Figure 1
<p>The aquifer domain and physical setting of the model.</p>
Full article ">Figure 2
<p>Schematic representation of sandbox experimental setup.</p>
Full article ">Figure 3
<p>The aquifer domain for the analytical solution.</p>
Full article ">Figure 4
<p>The comparison between observed and FD predicted plume.</p>
Full article ">Figure 5
<p>Comparison of the FD and Analytical solutions for two-dimensional transport.</p>
Full article ">Figure 6
<p>Contaminant concentration profile at: (<b>a</b>) (5,4) m Pe = 25, (<b>b</b>) (9,5) m, Pe = 45.</p>
Full article ">Figure 7
<p>The hydraulic conductivity distribution.</p>
Full article ">Figure 8
<p>(<b>a</b>) piezometric head profile and contours, (<b>b</b>) contaminant concentration profile, (<b>c</b>) oxidant concentration profile.</p>
Full article ">Figure 9
<p>Comparison between contaminant concentration at observation points located at: (<b>a</b>) (36,10) m, (<b>b</b>) (60,15) m and (<b>c</b>) (75,10) m optimized and arbitrary location of the oxidant sources.</p>
Full article ">Figure 10
<p>(<b>a</b>) Piezometric head profile and contours, (<b>b</b>) contaminant concentration profile, (<b>c</b>) oxidant concentration profile.</p>
Full article ">
18 pages, 4251 KiB  
Article
Evaluation of Rainfall Erosivity Factor Estimation Using Machine and Deep Learning Models
by Jimin Lee, Seoro Lee, Jiyeong Hong, Dongjun Lee, Joo Hyun Bae, Jae E. Yang, Jonggun Kim and Kyoung Jae Lim
Water 2021, 13(3), 382; https://doi.org/10.3390/w13030382 - 1 Feb 2021
Cited by 18 | Viewed by 5868
Abstract
Rainfall erosivity factor (R-factor) is one of the Universal Soil Loss Equation (USLE) input parameters that account for impacts of rainfall intensity in estimating soil loss. Although many studies have calculated the R-factor using various empirical methods or the USLE method, these methods [...] Read more.
Rainfall erosivity factor (R-factor) is one of the Universal Soil Loss Equation (USLE) input parameters that account for impacts of rainfall intensity in estimating soil loss. Although many studies have calculated the R-factor using various empirical methods or the USLE method, these methods are time-consuming and require specialized knowledge for the user. The purpose of this study is to develop machine learning models to predict the R-factor faster and more accurately than the previous methods. For this, this study calculated R-factor using 1-min interval rainfall data for improved accuracy of the target value. First, the monthly R-factors were calculated using the USLE calculation method to identify the characteristics of monthly rainfall-runoff induced erosion. In turn, machine learning models were developed to predict the R-factor using the monthly R-factors calculated at 50 sites in Korea as target values. The machine learning algorithms used for this study were Decision Tree, K-Nearest Neighbors, Multilayer Perceptron, Random Forest, Gradient Boosting, eXtreme Gradient Boost, and Deep Neural Network. As a result of the validation with 20% randomly selected data, the Deep Neural Network (DNN), among seven models, showed the greatest prediction accuracy results. The DNN developed in this study was tested for six sites in Korea to demonstrate trained model performance with Nash–Sutcliffe Efficiency (NSE) and the coefficient of determination (R2) of 0.87. This means that our findings show that DNN can be efficiently used to estimate monthly R-factor at the desired site with much less effort and time with total monthly precipitation, maximum daily precipitation, and maximum hourly precipitation data. It will be used not only to calculate soil erosion risk but also to establish soil conservation plans and identify areas at risk of soil disasters by calculating rainfall erosivity factors. Full article
(This article belongs to the Special Issue Soil–Water Conservation, Erosion, and Landslide)
Show Figures

Figure 1

Figure 1
<p>Study procedures.</p>
Full article ">Figure 2
<p>Weather stations in the study area.</p>
Full article ">Figure 3
<p>Illustration of the proposed Deep Neural Network (DNN) for rainfall erosivity (R-factor) prediction.</p>
Full article ">Figure 4
<p>Spatial distribution of monthly R-factor calculated by USLE, using rainfall data from 50 weather stations for the period 2013–2019.</p>
Full article ">Figure 5
<p>Comparison of (<b>a</b>) Decision Tree, (<b>b</b>) Multilayer Perceptron, (<b>c</b>) K-Nearest Neighbor, (<b>d</b>) Random Forest, (<b>e</b>) Gradient Boosting, (<b>f</b>) eXtreme Gradient Boost, and (<b>g</b>) Deep Neural Network calculated R-factor with validation data, and (<b>h</b>) comparison of machine learning accuracy.</p>
Full article ">Figure 5 Cont.
<p>Comparison of (<b>a</b>) Decision Tree, (<b>b</b>) Multilayer Perceptron, (<b>c</b>) K-Nearest Neighbor, (<b>d</b>) Random Forest, (<b>e</b>) Gradient Boosting, (<b>f</b>) eXtreme Gradient Boost, and (<b>g</b>) Deep Neural Network calculated R-factor with validation data, and (<b>h</b>) comparison of machine learning accuracy.</p>
Full article ">Figure 6
<p>The comparisons of forecasting results of R-factor using machine learning in (<b>a</b>) Chuncheon, (<b>b</b>) Gangneung, (<b>c</b>) Suwon, (<b>d</b>) Jeonju, (<b>e</b>) Busan, and (<b>f</b>) Namhae.</p>
Full article ">Figure 6 Cont.
<p>The comparisons of forecasting results of R-factor using machine learning in (<b>a</b>) Chuncheon, (<b>b</b>) Gangneung, (<b>c</b>) Suwon, (<b>d</b>) Jeonju, (<b>e</b>) Busan, and (<b>f</b>) Namhae.</p>
Full article ">Figure 7
<p>Comparison of prediction accuracy results by machine learning models in test sites.</p>
Full article ">
19 pages, 5402 KiB  
Article
Wet Meadow Plant Communities of the Alliance Trifolion pallidi on the Southeastern Margin of the Pannonian Plain
by Andraž Čarni, Mirjana Ćuk, Igor Zelnik, Jozo Franjić, Ružica Igić, Miloš Ilić, Daniel Krstonošić, Dragana Vukov and Željko Škvorc
Water 2021, 13(3), 381; https://doi.org/10.3390/w13030381 - 1 Feb 2021
Cited by 4 | Viewed by 3034
Abstract
The article deals with wet meadow plant communities of the alliance Trifolion pallidi that appear on the periodically inundated or waterlogged sites on the riverside terraces or gentle slopes along watercourses. These plant communities are often endangered by inappropriate hydrological interventions or management [...] Read more.
The article deals with wet meadow plant communities of the alliance Trifolion pallidi that appear on the periodically inundated or waterlogged sites on the riverside terraces or gentle slopes along watercourses. These plant communities are often endangered by inappropriate hydrological interventions or management practices. All available vegetation plots representing this vegetation type were collected, organized in a database, and numerically elaborated. This vegetation type appears in the southeastern part of the Pannonian Plain, which is still under the influence of the Mediterranean climate; its southern border is formed by southern outcrops of the Pannonian Plain and its northern border coincides with the influence of the Mediterranean climate (line Slavonsko Gorje-Fruška Gora-Vršačke Planine). Numerical analysis established four plant associations—Trifolio pallidi–Alopecuretum pratensis, Ventenato dubii–Trifolietum pallidi, Ranunculo strigulosi–Alopecuretum pratensis, and Ornithogalo pyramidale–Trifolietum pallidi. Each association was elaborated in detail: diagnostic plant species, nomenclature, geographical distribution, climatic and ecological conditions, and possible division into subassociations. Results are presented in a distribution map, figures resulting from numerical analysis, and a synoptic table. The hydrological gradient was found as the most important factor shaping the studied plant communities. The article also brings new field data on this vegetation type, which has not been sampled for decades and is in process of evaluation to be included as a special habitat type in the Habitat Directive. Full article
(This article belongs to the Special Issue Hydrology-Shaped Plant Communities: Diversity and Ecological Function)
Show Figures

Figure 1

Figure 1
<p>Position of the studied area (rectangle) within SE Europe.</p>
Full article ">Figure 2
<p>Dendrogram of analyzed relevés obtained with square root transformation of cover values in percentage, Beta flexible (β = −0.25) and group linkage with the relative Sørensen index. Legend: 1—<span class="html-italic">Ranunculo–Alopecuretum typicum</span>, 2—<span class="html-italic">Trifolio</span>–<span class="html-italic">Alopecuretum rhinanthetosum</span>, 3—<span class="html-italic">Trifolio</span>–<span class="html-italic">Alopecuretum typicum</span>, 4—<span class="html-italic">Ventenato–Trifolietum</span>, 5—<span class="html-italic">Ranunculo–Alopecuretum filipenduletosum</span>, 6—<span class="html-italic">Ornithogalo</span>–<span class="html-italic">Trifolietum</span>.</p>
Full article ">Figure 3
<p>The box–whisker diagram of Ellenberg indicator values (EIV) bioindicator values for moisture and nutrients and altitude (elevation): EIV moisture, EIV nutrients, and elevation. Boxes show the 25–75% quartile range and median value; whiskers indicate the range of values, except outliers. Legend: OpTp—<span class="html-italic">Ornithogalo</span>–<span class="html-italic">Trifolietum</span>, RaAfil—<span class="html-italic">Ranunculo–Alopecuretum filipenduletosum</span>, RaAtyp—<span class="html-italic">Ranunculo–Alopecuretum typicum</span>, VTp—<span class="html-italic">Ventenato–Trifolietum</span>, TpAtyp—<span class="html-italic">Trifolio</span>–<span class="html-italic">Alopecuretum typicum</span>, TpArhi—<span class="html-italic">Trifolio</span>–<span class="html-italic">Alopecuretum rhinanthetosum</span>.</p>
Full article ">Figure 4
<p>Diagram of Detrended Correspondence Analysis (DCA) of relevés with the centroid of groups and spider plots with passively projected EIV nutrient and EIV moisture and climatic variables—precipitation seasonality, mean temperature of the coldest quarter, mean annual temperature, precipitation in the driest quarter. Eigenvalues for the first two axes are 0.493 and 0.295, respectively. The legend is the same as in <a href="#water-13-00381-f003" class="html-fig">Figure 3</a>.</p>
Full article ">Figure 5
<p>Macroclimatic features represented by annual mean temperature, annual precipitation, mean temperature of the coldest quarter, precipitation of the driest quarter, and precipitation seasonality and number of species. The legend is the same as in <a href="#water-13-00381-f003" class="html-fig">Figure 3</a>.</p>
Full article ">Figure 6
<p>The geographical position of elaborated plant communities.</p>
Full article ">Figure A1
<p>The geographical position of original relevés from fieldwork sampling and relevés collected from the literature.</p>
Full article ">Figure A2
<p>Analytic table of the new field data used in the analysis. The relevés are classified in accordance with <a href="#water-13-00381-f0A3" class="html-fig">Figure A3</a>, diagnostic species of the associations are framed. The following associations were sampled: 1–13 <span class="html-italic">Trifolio pallidi–Alopecuretum pratensis</span>, 14–32 <span class="html-italic">Ranunculo strigulosi–Alopecuretum pratensis</span>, and 33–35 <span class="html-italic">Ornithogalo pyramidale–Trifolietum pallidi</span>.</p>
Full article ">Figure A3
<p>Percentage synoptic table of the <span class="html-italic">Trifolion pallidi</span> meadows. Diagnostic species of syntaxa are framed or indicated by asterisk. Diagnostic species of the <span class="html-italic">Trifolion pallidi</span> and <span class="html-italic">Trifolio–Hordeetalia</span> are from literature. Legend to columns: 1—<span class="html-italic">Trifolio pallidi</span>–<span class="html-italic">Alopecuretum rhinanthetosum rumelici</span>, 2—<span class="html-italic">Trifolio pallidi</span>–<span class="html-italic">Alopecuretum typicum</span>, 3—<span class="html-italic">Ventenato–Trifolietum pallidi</span>, 4—<span class="html-italic">Ranunculo acris–Alopecuretum typicum</span>, 5—<span class="html-italic">Ranunculo acris–Alopecuretum filipenduletosum</span>, 6—<span class="html-italic">Ornithogalo pyramidale</span>–<span class="html-italic">Trifolietum pallidi</span>.</p>
Full article ">
23 pages, 75708 KiB  
Article
Classification and Prediction of Natural Streamflow Regimes in Arid Regions of the USA
by Angela M. Merritt, Belize Lane and Charles P. Hawkins
Water 2021, 13(3), 380; https://doi.org/10.3390/w13030380 - 1 Feb 2021
Cited by 16 | Viewed by 4462
Abstract
Understanding how natural variation in flow regimes influences stream ecosystem structure and function is critical to the development of effective stream management policies. Spatial variation in flow regimes among streams is reasonably well understood for streams in mesic regions, but a more robust [...] Read more.
Understanding how natural variation in flow regimes influences stream ecosystem structure and function is critical to the development of effective stream management policies. Spatial variation in flow regimes among streams is reasonably well understood for streams in mesic regions, but a more robust characterization of flow regimes in arid regions is needed, especially to support biological monitoring and assessment programs. In this paper, we used long-term (41 years) records of mean daily streamflow from 287 stream reaches in the arid and semi-arid western USA to develop and compare several alternative flow-regime classifications. We also evaluated how accurately we could predict the flow-regime classes of ungauged reaches. Over the 41-year record examined (water years 1972–2013), the gauged reaches varied continuously from always having flow > zero to seldom having flow. We predicted ephemeral and perennial reaches with less error than reaches with an intermediate number of zero-flow days or years. We illustrate application of our approach by predicting the flow-regime classes at ungauged reaches in Arizona, USA. Maps based on these predictions were generally consistent with qualitative expectations of how flow regimes vary spatially across Arizona. These results represent a promising step toward more effective assessment and management of streams in arid regions. Full article
Show Figures

Figure 1

Figure 1
<p>Workflow describing data compilation, pre-analysis data manipulation, classification, modeling, and mapping.</p>
Full article ">Figure 2
<p>Map of the 287 basins with complete (dark blue, dark brown) and partial (light blue, light brown) USGS GAGES II reference streamflow data. Nonperennial reaches are in brown and perennial reaches are in blue.</p>
Full article ">Figure 3
<p>The dendrogram produced by the hierarchical cluster analysis with the most resolved seven-group classes shown. The number of reaches in each class were A1 (39), A2 (53), B1a (36), B1bi (60), B1bii (30), B2a (44), and B2b (25).</p>
Full article ">Figure 4
<p>Density distribution plots of the metric values for each of the seven most resolved hierarchical classes (A1 to B2b). Plots for the different metrics are presented in the same order as given in <a href="#water-13-00380-t002" class="html-table">Table 2</a>. Each panel’s dotted line represents the mean for all 287 streams. The bold intersecting line for each distribution represents the mean for each individual class.</p>
Full article ">Figure 5
<p>Dimensionless reference hydrographs (archetypes) for the seven most resolved classes (A1 to B2b). Day of year is based on water year, i.e., October 1 = day of year 1. The red line and shading trace the mean percentiles of mean daily flow values for each individual day of year calculated for each class across the full period of record. The black lines represent the maximum and minimum mean daily flows for each class on each day of record. The number of reaches in each class were A1 (39), A2 (53), B1a (36), B1bi (60), B1bii (30), B2a (44), and B2b (25).</p>
Full article ">Figure 6
<p>Plots of observed versus predicted values for the ZFY and ZFD regression models.</p>
Full article ">Figure 7
<p>Maps of the state of Arizona showing the predicted locations of the three-, three-, four-, and five-group classes derived from the hierarchical cluster analysis. Major rivers (blue lines) are superimposed.</p>
Full article ">
24 pages, 24572 KiB  
Article
Flood Suspended Sediment Transport: Combined Modelling from Dilute to Hyper-Concentrated Flow
by Jaan H. Pu, Joseph T. Wallwork, Md. Amir Khan, Manish Pandey, Hanif Pourshahbaz, Alfrendo Satyanaga, Prashanth R. Hanmaiahgari and Tim Gough
Water 2021, 13(3), 379; https://doi.org/10.3390/w13030379 - 1 Feb 2021
Cited by 34 | Viewed by 4899
Abstract
During flooding, the suspended sediment transport usually experiences a wide-range of dilute to hyper-concentrated suspended sediment transport depending on the local flow and ground conditions. This paper assesses the distribution of sediment for a variety of hyper-concentrated and dilute flows. Due to the [...] Read more.
During flooding, the suspended sediment transport usually experiences a wide-range of dilute to hyper-concentrated suspended sediment transport depending on the local flow and ground conditions. This paper assesses the distribution of sediment for a variety of hyper-concentrated and dilute flows. Due to the differences between hyper-concentrated and dilute flows, a linear-power coupled model is proposed to integrate these considerations. A parameterised method combining the sediment size, Rouse number, mean concentration, and flow depth parameters has been used for modelling the sediment profile. The accuracy of the proposed model has been verified against the reported laboratory measurements and comparison with other published analytical methods. The proposed method has been shown to effectively compute the concentration profile for a wide range of suspended sediment conditions from hyper-concentrated to dilute flows. Detailed comparisons reveal that the proposed model calculates the dilute profile with good correspondence to the measured data and other modelling results from literature. For the hyper-concentrated profile, a clear division of lower (bed-load) to upper layer (suspended-load) transport can be observed in the measured data. Using the proposed model, the transitional point from this lower to upper layer transport can be calculated precisely. Full article
(This article belongs to the Special Issue Modelling of Floods in Urban Areas)
Show Figures

Figure 1

Figure 1
<p>Type I, II and III Concentration Profiles.</p>
Full article ">Figure 2
<p>Rouse number regression analysis for coefficient <math display="inline"><semantics> <mrow> <msub> <mi mathvariant="normal">b</mi> <mn>1</mn> </msub> </mrow> </semantics></math>.</p>
Full article ">Figure 3
<p>Rouse number regression analysis for coefficient <math display="inline"><semantics> <mrow> <msub> <mi mathvariant="sans-serif">α</mi> <mn>1</mn> </msub> </mrow> </semantics></math>.</p>
Full article ">Figure 4
<p>Rouse number regression analysis for coefficient <math display="inline"><semantics> <mrow> <msub> <mi mathvariant="normal">b</mi> <mn>2</mn> </msub> </mrow> </semantics></math>.</p>
Full article ">Figure 5
<p>Rouse number regression analysis for coefficient <math display="inline"><semantics> <mrow> <msub> <mi mathvariant="sans-serif">α</mi> <mn>2</mn> </msub> </mrow> </semantics></math>.</p>
Full article ">Figure 6
<p>Size parameter regression analysis for coefficient <math display="inline"><semantics> <mrow> <msub> <mi mathvariant="normal">b</mi> <mn>1</mn> </msub> </mrow> </semantics></math>.</p>
Full article ">Figure 7
<p>Size parameter regression analysis for coefficient <math display="inline"><semantics> <mrow> <msub> <mi mathvariant="normal">b</mi> <mn>2</mn> </msub> </mrow> </semantics></math>.</p>
Full article ">Figure 8
<p>Size parameter regression analysis for coefficient <math display="inline"><semantics> <mrow> <msub> <mi mathvariant="normal">b</mi> <mn>2</mn> </msub> </mrow> </semantics></math>.</p>
Full article ">Figure 9
<p>Size parameter regression analysis for coefficient <math display="inline"><semantics> <mrow> <msub> <mi mathvariant="sans-serif">α</mi> <mn>2</mn> </msub> </mrow> </semantics></math>.</p>
Full article ">Figure 10
<p>Mean concentration regression analysis for coefficient <math display="inline"><semantics> <mrow> <msub> <mi mathvariant="normal">b</mi> <mn>1</mn> </msub> </mrow> </semantics></math>.</p>
Full article ">Figure 11
<p>Mean concentration regression analysis for coefficient <math display="inline"><semantics> <mrow> <msub> <mi mathvariant="normal">q</mi> <mn>1</mn> </msub> </mrow> </semantics></math>.</p>
Full article ">Figure 12
<p>Mean concentration regression analysis for coefficient <math display="inline"><semantics> <mrow> <msub> <mi mathvariant="normal">b</mi> <mn>2</mn> </msub> </mrow> </semantics></math>.</p>
Full article ">Figure 13
<p>Mean concentration regression analysis for coefficient <math display="inline"><semantics> <mrow> <msub> <mi mathvariant="normal">q</mi> <mn>2</mn> </msub> </mrow> </semantics></math>.</p>
Full article ">Figure 14
<p>Modelled results and comparisons against experimental data of Wang and Ni [<a href="#B31-water-13-00379" class="html-bibr">31</a>].</p>
Full article ">Figure 14 Cont.
<p>Modelled results and comparisons against experimental data of Wang and Ni [<a href="#B31-water-13-00379" class="html-bibr">31</a>].</p>
Full article ">Figure 14 Cont.
<p>Modelled results and comparisons against experimental data of Wang and Ni [<a href="#B31-water-13-00379" class="html-bibr">31</a>].</p>
Full article ">Figure 14 Cont.
<p>Modelled results and comparisons against experimental data of Wang and Ni [<a href="#B31-water-13-00379" class="html-bibr">31</a>].</p>
Full article ">Figure 15
<p>Modelled results and comparisons against experimental data of Wang and Qian [<a href="#B36-water-13-00379" class="html-bibr">36</a>].</p>
Full article ">Figure 15 Cont.
<p>Modelled results and comparisons against experimental data of Wang and Qian [<a href="#B36-water-13-00379" class="html-bibr">36</a>].</p>
Full article ">Figure 16
<p>Showing modelled results and comparisons for experimental data of Michalik [<a href="#B35-water-13-00379" class="html-bibr">35</a>].</p>
Full article ">Figure 16 Cont.
<p>Showing modelled results and comparisons for experimental data of Michalik [<a href="#B35-water-13-00379" class="html-bibr">35</a>].</p>
Full article ">Figure 16 Cont.
<p>Showing modelled results and comparisons for experimental data of Michalik [<a href="#B35-water-13-00379" class="html-bibr">35</a>].</p>
Full article ">
6 pages, 200 KiB  
Editorial
Hydrological and Hydro-Meteorological Extremes and Related Risk and Uncertainty
by Athanasios Loukas, Luis Garrote and Lampros Vasiliades
Water 2021, 13(3), 377; https://doi.org/10.3390/w13030377 - 1 Feb 2021
Cited by 3 | Viewed by 2693
Abstract
Natural hazards have caused significant damages to natural and manmade environments during the last few decades [...] Full article
17 pages, 3654 KiB  
Article
Management of Urban Stormwater at Block-Level (MUST-B): A New Approach for Potential Analysis of Decentralized Stormwater Management Systems
by Ganbaatar Khurelbaatar, Manfred van Afferden, Maximilian Ueberham, Michael Stefan, Stefan Geyler and Roland A. Müller
Water 2021, 13(3), 378; https://doi.org/10.3390/w13030378 - 31 Jan 2021
Cited by 11 | Viewed by 4137
Abstract
Cities worldwide are facing problems to mitigate the impact of urban stormwater runoff caused by the increasing occurrence of heavy rainfall events and urban re-densification. This study presents a new approach for estimating the potential of the Management of Urban STormwater at Block-level [...] Read more.
Cities worldwide are facing problems to mitigate the impact of urban stormwater runoff caused by the increasing occurrence of heavy rainfall events and urban re-densification. This study presents a new approach for estimating the potential of the Management of Urban STormwater at Block-level (MUST-B) by decentralized blue-green infrastructures here called low-impact developments (LIDs) for already existing urban environments. The MUST-B method was applied to a study area in the northern part of the City of Leipzig, Germany. The Study areas was divided into blocks smallest functional units and considering two different soil permeability and three different rainfall events, seven scenarios have been developed: current situation, surface infiltration, swale infiltration, trench infiltration, trough-trench infiltration, and three different combinations of extensive roof greening, trough-trench infiltration, and shaft infiltration. The LIDs have been simulated and their maximum retention/infiltration potential and the required area have been estimated together with a cost calculation. The results showed that even stormwater of a 100 year rainfall event can be fully retained and infiltrated within the blocks on a soil with low permeability (kf = 10−6 m/s). The cost and the required area for the LIDs differed depending on the scenario and responded to the soil permeability and rainfall events. It is shown that the MUST-B method allows a simple down- and up-scaling process for different urban settings and facilitates decision making for implementing decentralized blue-green-infrastructure that retain, store, and infiltrate stormwater at block level. Full article
(This article belongs to the Special Issue Advances of Low Impact Development Practices in Urban Watershed)
Show Figures

Figure 1

Figure 1
<p>Basic principle of the MUST-B approach.</p>
Full article ">Figure 2
<p>Data processing steps for quantification of surface area (impervious, pervious) relevant for analysis.</p>
Full article ">Figure 3
<p>LIDs considered in the scenario development. (<b>a</b>) Surface infiltration. No retention volume. (<b>b</b>) Swale infiltration. Structure height: 0.30 m. (<b>c</b>) Trench infiltration (gravel). Structure height: 1 m. Retention volume: 350 L/m<sup>2</sup>. (<b>d</b>) Trough-trench infiltration (gravel). Structure height: 1.55 m. Retention volume: 730 L/m<sup>2</sup>. (<b>e</b>) Extensive roof greening. Structure height: 0.1 m. Retention volume: 50 L/m<sup>2</sup>. (<b>f</b>) Infiltration shaft. Depth: 2 m. Min. Diameter: 1 m. Retention volume: 300 L/m<sup>2</sup>.</p>
Full article ">Figure 3 Cont.
<p>LIDs considered in the scenario development. (<b>a</b>) Surface infiltration. No retention volume. (<b>b</b>) Swale infiltration. Structure height: 0.30 m. (<b>c</b>) Trench infiltration (gravel). Structure height: 1 m. Retention volume: 350 L/m<sup>2</sup>. (<b>d</b>) Trough-trench infiltration (gravel). Structure height: 1.55 m. Retention volume: 730 L/m<sup>2</sup>. (<b>e</b>) Extensive roof greening. Structure height: 0.1 m. Retention volume: 50 L/m<sup>2</sup>. (<b>f</b>) Infiltration shaft. Depth: 2 m. Min. Diameter: 1 m. Retention volume: 300 L/m<sup>2</sup>.</p>
Full article ">Figure 4
<p>Input interface and conceptual model of a low-impact development (LID) for the illustration of infiltration and retention systems.</p>
Full article ">Figure 5
<p>Division of the study area into urban blocks, which are the functional unit of the MUST-B approach. The classification of the block depend on the pervious area.</p>
Full article ">Figure 6
<p>Simulation result depicting the current situation for a 30-year rainfall event on a soil with high permeability (k<sub>f</sub> = 10<sup>−4</sup> m/s). The columns represent the amount of runoff generated from the blocks and are not true to scale for presentation purpose.</p>
Full article ">Figure 7
<p>Simulation result of scenario 4, depicting the trough-trench infiltration for a 30-year rainfall event on a soil with high permeability (k<sub>f</sub> = 10<sup>−4</sup> m/s). The columns represent the amount of runoff from the blocks and are not true to scale for presentation purpose.</p>
Full article ">Figure 8
<p>Example regressions showing the relation between the pervious ‘net area’ and the area requirement of the Trough-Trench Infiltration system relative to the pervious ‘net area’.</p>
Full article ">
20 pages, 5280 KiB  
Article
Spatio-Temporal Coupling Coordination Analysis between Urbanization and Water Resource Carrying Capacity of the Provinces in the Yellow River Basin, China
by Ran Qiao, Huimin Li and Han Han
Water 2021, 13(3), 376; https://doi.org/10.3390/w13030376 - 31 Jan 2021
Cited by 34 | Viewed by 3597
Abstract
With the rapid expansion of the Chinese economy in recent years, the urbanization process of the provinces in the Yellow River Basin (YRB) has put serious pressure on the sustainability of the water resources carrying capacity (WRCC). It is necessary to analyze and [...] Read more.
With the rapid expansion of the Chinese economy in recent years, the urbanization process of the provinces in the Yellow River Basin (YRB) has put serious pressure on the sustainability of the water resources carrying capacity (WRCC). It is necessary to analyze and diagnose the coordination state between urbanization and the WRCC. In this study, based on the Population-Economic-Social-Spatial (PESS) framework and Pressure-State-Response (PSR) model, we developed two index systems for the urbanization and WRCC, respectively. At the basis of the two index systems, the coupling coordination degree (CCD) of the two systems is calculated by applying the improved CCD model. Based on the calculated CCD for each province, the spatio-temporal analysis was performed to analyze the characteristics of CCD in the YRB. The obstacle factor model is utilized to obtain the main obstacle factors. The results show that: (1) the coordination state between the urbanization and WRCC systems was improved to some extent in 2017, compared to 2008, but there are differences in the coordination state of the different provinces in the YRB. (2) In terms of the level of urbanization, the gap between the seven provinces’ performance levels widened because urbanization grew at different rates. The WRCC system’s performance presented a fluctuating downward trend from 2008 to 2017 in the YRB. (3) The pressure subsystem had a significant impact on the two systems’ coordination state in the YRB, while the social urbanization and response subsystem had a less significant impact on the urbanization system and the WRCC system, respectively. Due to the growth of urbanization, the imbalanced development of the WRCC and urbanization has become the principal contradiction that must be solved in order to achieve sustainability in the YRB. The analysis of the coupling relationship between urbanization and WRCC may guide the policy makers in planning for realistic goals. The results provide a guide for high-quality development in the YRB. Full article
(This article belongs to the Section Urban Water Management)
Show Figures

Figure 1

Figure 1
<p>Flow diagram of the structure.</p>
Full article ">Figure 2
<p>Provinces in the YRB.</p>
Full article ">Figure 3
<p>The framework of the method proposed in this study.</p>
Full article ">Figure 4
<p>The relationship between different states in the PSR model.</p>
Full article ">Figure 5
<p>The seven provinces’ urbanization performance trend in the YRB from 2008 to 2017.</p>
Full article ">Figure 6
<p>The water resource performance trend of the seven provinces in YRB from 2008 to 2017.</p>
Full article ">Figure 7
<p>Spatial distribution of coordination state in provinces in the YRB.</p>
Full article ">Figure 8
<p>Variation tendency of the coordination state in the YRB from 2008 to 2017.</p>
Full article ">
35 pages, 8924 KiB  
Article
Management of the Phosphorus–Cladophora Dynamic at a Site on Lake Ontario Using a Multi-Module Bioavailable P Model
by Martin T. Auer, Cory P. McDonald, Anika Kuczynski, Chenfu Huang and Pengfei Xue
Water 2021, 13(3), 375; https://doi.org/10.3390/w13030375 - 31 Jan 2021
Cited by 10 | Viewed by 4228
Abstract
The filamentous green alga Cladophora grows to nuisance proportions in Lake Ontario. Stimulated by high phosphorus concentrations, nuisance growth results in the degradation of beaches and clogging of industrial water intakes with attendant loss of beneficial uses. We develop a multi-module bioavailable phosphorus [...] Read more.
The filamentous green alga Cladophora grows to nuisance proportions in Lake Ontario. Stimulated by high phosphorus concentrations, nuisance growth results in the degradation of beaches and clogging of industrial water intakes with attendant loss of beneficial uses. We develop a multi-module bioavailable phosphorus model to examine the efficacy of phosphorus management strategies in mitigating nuisance algal growth. The model platform includes modules simulating hydrodynamics (FVCOM), phosphorus-phytoplankton dynamics (GEM) and Cladophora growth (GLCMv3). The model is applied along a 25 km stretch of the Lake Ontario nearshore, extending east from Toronto, ON and receiving effluent from three wastewater treatment plants. Simulation results identify the Duffin Creek wastewater treatment plant effluent as a driving force for nuisance conditions of Cladophora growth, as reflected in effluent bioavailable phosphorus concentrations and the dimensions of the plant’s phosphorus footprint. Simulation results demonstrate that phosphorus removal by chemically enhanced secondary treatment is insufficient to provide relief from nuisance conditions. Tertiary treatment (chemically enhanced secondary treatment with ballasted flocculation) is shown to eliminate phosphorus-saturated conditions associated with the Duffin Creek wastewater treatment plant effluent, providing local relief from nuisance conditions. Management guidance presented here has wider application at sites along the highly urbanized Canadian nearshore of Lake Ontario. Full article
(This article belongs to the Special Issue Water-Quality Modeling)
Show Figures

Graphical abstract

Graphical abstract
Full article ">Figure 1
<p>Study site and modeling domain along the Lake Ontario nearshore, centered on Pickering, Ajax and Whitby ON. Triangles identify the location of in-lake wastewater treatment plant discharges. Tributary entry to Lake Ontario is indicated as T1 (Rouge River), T2 (Duffins Creek) and T3 (Carruthers Creek). The solid line represents the 20 m depth contour, the approximate offshore limit to colonization by <span class="html-italic">Cladophora</span>. The inset includes the position of the study site model grid within the whole-lake grid used in hydrodynamic simulations. The locations of the Regional Municipalities of York and Durham, containing the area served by the Duffin Creek wastewater treatment plant are indicated in the inset as well.</p>
Full article ">Figure 2
<p>Impacts of nuisance growth of <span class="html-italic">Cladophora</span>: (<b>a</b>) beach deposition at Veterans Point, Ajax, ON (image by Paul Wealleans) and (<b>b</b>) algal debris captured at the cooling water intake for the Ontario Power Generation (OPG) Pickering Nuclear Generating Station (image by Long Vu, OPG).</p>
Full article ">Figure 3
<p>The modeling platform utilized in this work illustrating the three component modules (hydrodynamics, biokinetics and <span class="html-italic">Cladophora</span> nutritional status) and their inputs, outputs and interactions.</p>
Full article ">Figure 4
<p>Performance testing of the hydrodynamic model (FVCOM): (<b>a</b>) daily averaged longshore current velocity at 5 m; positive values are W→E and negative values E→W, (<b>b</b>) cross-shore current; positive values are onshore, N, and negative values are offshore, S and (<b>c</b>) surface temperature measured at National Data Buoy Center (NDBC) Buoy 45159 (<a href="#app1-water-13-00375" class="html-app">Supplementary Material, Figure S1</a>).</p>
Full article ">Figure 5
<p>Conceptualization of the phosphorus–phytoplankton dynamics (GEM) model as applied (<b>a</b>) by Rowe et al. [<a href="#B29-water-13-00375" class="html-bibr">29</a>] and (<b>b</b>) in this work.</p>
Full article ">Figure 6
<p>Determination of boundary conditions: (<b>a</b>) soluble reactive phosphorus and (<b>b</b>) chlorophyll; with bars representing the standard deviation of the mean daily value.</p>
Full article ">Figure 7
<p>GLCMv3 model fit to field measurements made at a depth of 6m at the Lake Ontario study site in 2020. Dots are the mean of triplicate measurements and bars represent the standard deviation for those means for each sampling date. Data used with permission of Ontario Power Generation, Inc.</p>
Full article ">Figure 8
<p>Results of model performance testing for soluble reactive phosphorus concentrations in 2016: (<b>a</b>) surface water and (<b>b</b>) bottom water. Diamonds represent observed median concentrations with the 25th and 75th percentiles indicated by bars. Dashed line represents daily median modeled concentrations with the 25th and 75th percentiles for each daily median shaded in gray.</p>
Full article ">Figure 9
<p>Results of model performance testing for surface water chlorophyll. Circles represent 2016 observed concentrations and the dashed line represents 2016 median modeled concentrations. The gray shaded area represents the 25th and 75th percentiles for daily observations over the (expanded) 2012–2016 interval, included to reflect observed interannual variability.</p>
Full article ">Figure 10
<p>Management metric for the phosphorus–<span class="html-italic">Cladophora</span> dynamic: the relationship between ambient soluble reactive phosphorus concentration and normalized seasonal maximum <span class="html-italic">Cladophora</span> biomass, illustrating the departure from P-limited growth as concentrations exceed an upper bound of 1.5 μgP⋅L<sup>−1</sup>.</p>
Full article ">Figure 11
<p>Model-simulated SRP concentrations with the Duffin Creek WWTP as a sole-source discharge at contemporary levels of phosphorus removal and flow: (<b>a</b>) for bottom water at a station proximate to the wastewater treatment plant (WWTP) outfall and at stations to the east and west. Station depths are &gt;5 and &lt;10 m; the red line represents the metric for P-limited growth (1.5 μgP⋅L<sup>−1</sup>) and (<b>b</b>) vertical profiles at the station most proximate to the Duffin Creek WWTP outfall. Profiles presented left to right are not a progressive time series, but are ordered to systematically illustrate variability in the position and magnitude of the plume as mediated by the vertical density gradient and turbulence.</p>
Full article ">Figure 12
<p>Simulations of the bottom water SRP footprint for (<b>a</b>) the Highland Creek WWTP, (<b>b</b>) the Duffin Creek WWTP and (<b>c</b>) the Corbett Creek WWTP as sole-source discharges with contemporary treatment levels and flows and (<b>d</b>) the resulting multiple source discharge. The green line represents the maximum lakeward extent of <span class="html-italic">Cladophora</span> colonization (to the 20 m depth).</p>
Full article ">Figure 13
<p>Sole-source simulation of the bottom water SRP footprint for the Duffin Creek WWTP under contemporary treatment (Baseline; panels (<b>a</b>,<b>b</b>)) and two engineered treatment options (Optimized 2°, panels (<b>c</b>,<b>d</b>) and Tertiary, panels (<b>e</b>,<b>f</b>)), each for contemporary and maximum permitted design flow.</p>
Full article ">Figure 14
<p>Model-simulated, multiple-source, bottom water SRP footprint for the Pickering–Ajax–Whitby nearshore receiving discharges from the Highland Creek, Duffin Creek and Corbett Creek WWTPs before and after implementation of tertiary treatment at the Duffin Creek WWTP: (<b>a</b>) pre-implementation, contemporary flow, (<b>b</b>) post-implementation contemporary flow and (<b>c</b>) post implementation maximum permitted design flow.</p>
Full article ">Figure 15
<p>Model-simulated, multiple-source, bottom water SRP concentrations proximate to the Duffin Creek WWTP outfall and stations to the east and west. Simulations are for contemporary (baseline) treatment (black) and tertiary treatment (dark red), both with contemporary flow. Conditions are the contemporary case for discharges from the Highland Creek and Corbett Creek WWTPs. The red line represents the metric for P-limited growth (1.5 μgP⋅L<sup>−1</sup>).</p>
Full article ">Figure 16
<p>Model-simulated surface water SRP concentrations at a station proximate to the Duffin Creek WWTP outfall (see map inset, <a href="#water-13-00375-f015" class="html-fig">Figure 15</a>). Simulations represent a multiple-source discharge with contemporary treatment and flow at the Highland Creek and Corbett Creek WWTPs and tertiary treatment and contemporary flow at the Duffin Creek WWTP (black line) and a sole-source discharge at the Duffin Creek WWTP with tertiary treatment and contemporary flow (red line). The dashed line represents the metric for P-limited growth (1.5 μgP⋅L<sup>−1</sup>)<b>.</b></p>
Full article ">
15 pages, 8362 KiB  
Article
Analysis of the Arbovirosis Potential Occurrence in Dobrogea, Romania
by Carmen Maftei, Alina Bărbulescu, Sorin Rugina, Cristian Dorin Nastac and Irina Magdalena Dumitru
Water 2021, 13(3), 374; https://doi.org/10.3390/w13030374 - 31 Jan 2021
Cited by 7 | Viewed by 3331
Abstract
Climate change creates new challenges for preventing and protecting human health against different diseases that could appear and propagate. The Aedes albopictus mosquito species is an important vector for different diseases like dengue fever or zika. Although this species is not “indigenous” in [...] Read more.
Climate change creates new challenges for preventing and protecting human health against different diseases that could appear and propagate. The Aedes albopictus mosquito species is an important vector for different diseases like dengue fever or zika. Although this species is not “indigenous” in Europe, its presence is noticed in many countries on the continent. The Ae. albopictus establishment is conditioned by the species’ characteristics and environmental factors. To assess the possible spread of Ae. albopictus in the Dobrogea region (situated in the Southeast of Romania), we conducted the following analysis: (1) Investigation of the current distribution and climatic factors favoring Ae. albopictus’ establishment in Europe; (2) Analysis of climate dynamics in Dobrogea in terms of the parameters identified at stage (1); (3) Testing the hypothesis that the climate from Dobrogea favors Ae. albopictus’ establishment in the region; (4) Building a Geographic Information System (GIS)-based model of the potential geographic distribution of Ae. albopictus in Dobrogea. Results show that the climate of Dobrogea favors the apparition of the investigated species and its proliferation. Full article
Show Figures

Figure 1

Figure 1
<p>The number of imported cases of dengue fever reported in Romania.</p>
Full article ">Figure 2
<p>The map of the Dobrogea region (DEM: Digital Elevation Model).</p>
Full article ">Figure 3
<p>Scheme of a Geographic Information System (GIS) model.</p>
Full article ">Figure 4
<p>The mean multiannual temperatures in the geographical area where the <span class="html-italic">Ae. albopictus</span> was discovered.</p>
Full article ">Figure 5
<p>The mean multiannual precipitation in the area where the <span class="html-italic">Ae. albopictus</span> was discovered.</p>
Full article ">Figure 6
<p>Principal climatic parameters at weather stations in the Dobrogea region (average 1998–2019).</p>
Full article ">Figure 7
<p>Multiannual precipitation data set reclassified.</p>
Full article ">Figure 8
<p>Suitable locations of <span class="html-italic">Ae. albopictus</span> establishment.</p>
Full article ">
18 pages, 6576 KiB  
Article
Modeling the Effectiveness of Cooling Trenches for Stormwater Temperature Mitigation
by Scott A. Wells
Water 2021, 13(3), 373; https://doi.org/10.3390/w13030373 - 31 Jan 2021
Viewed by 2725
Abstract
Due to elevated runoff stormwater temperatures from impervious areas, one management strategy to reduce stormwater temperature is the use of underground flow through rock media termed a cooling trench. This paper examines the governing equations for the liquid phase and media phases for [...] Read more.
Due to elevated runoff stormwater temperatures from impervious areas, one management strategy to reduce stormwater temperature is the use of underground flow through rock media termed a cooling trench. This paper examines the governing equations for the liquid phase and media phases for modeling the temperature leaving a cooling trench assuming that changes in temperature occurred longitudinally through the cooling trench. This model is dependent on parameters such as the media type, porosity, media initial temperature, inflow rate, and inflow temperature. Several approaches were explored mathematically for evaluating the change in temperature of the water and the cooling trench media. Typical soil–water heat transfer coefficients were summarized. Examples of predictions of outflow temperatures were shown for different modeling assumptions, such as well-mixed conditions, batch mixing and subsequent release, and steady-state and dynamic conditions. Several of these examples evaluated how long rock media would cool following a stormwater event and how the cooling trench would respond to multiple stormwater events. Full article
(This article belongs to the Special Issue Water-Quality Modeling)
Show Figures

Figure 1

Figure 1
<p>Flow of stormwater into and out of a rock crib or cooling trench with rock media.</p>
Full article ">Figure 2
<p>Temperature conceptual model.</p>
Full article ">Figure 3
<p>Predictions of temperature of the water at three locations in the infiltration gallery as a function of time for the solution of Equation (1) and (2) for a flow rate of 0.03 m<sup>3</sup>/s.</p>
Full article ">Figure 4
<p>Predictions of sediment or rock media temperature at three locations in the infiltration gallery as a function of time for the solution of Equation (1) and (2) for a flow rate of 0.03 m<sup>3</sup>/s.</p>
Full article ">Figure 5
<p>Rock media temperature as a function of position in the cooling trench during and after a storm event ends after 60 min using Equation (2).</p>
Full article ">Figure 6
<p>Equilibrium temperature of the stormwater and rock in a batch cooling trench as a function of porosity (Equation (8) in <a href="#water-13-00373-t002" class="html-table">Table 2</a>) with stormwater initially at 30 °C and rock media at 10 °C.</p>
Full article ">Figure 7
<p>Equilibrium temperature for rock and water for a batch reactor (Equation (6) in <a href="#water-13-00373-t002" class="html-table">Table 2</a>). The initial rock media temperature was 10 °C and the initial stormwater temperature was 30 °C.</p>
Full article ">Figure 8
<p>Temperature of rock and water for a well-mixed flow through reactor at flow rates of 0.03, 0.52, and 2.72 m<sup>3</sup>/s (Equation (5); <a href="#water-13-00373-t002" class="html-table">Table 2</a>).</p>
Full article ">Figure 9
<p>Variation of stormwater temperature as a function of position through a 25 m long cooling trench with an inflow flow rate of 0.031 m<sup>3</sup>/s (Equation (4) in <a href="#water-13-00373-t002" class="html-table">Table 2</a>).</p>
Full article ">Figure 10
<p>Variation of rock temperature as a function of position for a stormwater inflow flow rate of 0.031 m<sup>3</sup>/s through a 25 m long cooling trench (Equation (4) in <a href="#water-13-00373-t002" class="html-table">Table 2</a>).</p>
Full article ">Figure 11
<p>Variation of stormwater temperature as a function of position through a 25 m long cooling trench for a flow of 0.52 m<sup>3</sup>/s (Equation (4) in <a href="#water-13-00373-t002" class="html-table">Table 2</a>).</p>
Full article ">Figure 12
<p>Variation of rock temperature as a function of position for a stormwater flow of 0.52 m<sup>3</sup>/s through a 25 m long infiltration trench (Equation (4) in <a href="#water-13-00373-t002" class="html-table">Table 2</a>).</p>
Full article ">Figure 13
<p>Water and rock temperature within cooling trench with a flow rate of about 10,080 m<sup>3</sup>/day over a 10 min period every 2 days assuming cooling by soil in contact with the cooling trench (Equation (9) <a href="#water-13-00373-t002" class="html-table">Table 2</a>).</p>
Full article ">Figure 14
<p>Water and sediment temperature in cooling trench after 1 storm event (Equation (9) <a href="#water-13-00373-t002" class="html-table">Table 2</a>).</p>
Full article ">
21 pages, 4725 KiB  
Article
Evolution of Salinity and Water Table Level of the Phreatic Coastal Aquifer of the Emilia Romagna Region (Italy)
by Beatrice Maria Sole Giambastiani, Assaye Kidanemariam, Addisu Dagnew and Marco Antonellini
Water 2021, 13(3), 372; https://doi.org/10.3390/w13030372 - 31 Jan 2021
Cited by 15 | Viewed by 4056
Abstract
The coastal aquifers of the Mediterranean region are highly susceptible to seawater intrusion due to a combination of challenges such as land subsidence, high aquifer permeability, urbanization, drainage, and an unsustainable use of water during the dry summer months. The present study is [...] Read more.
The coastal aquifers of the Mediterranean region are highly susceptible to seawater intrusion due to a combination of challenges such as land subsidence, high aquifer permeability, urbanization, drainage, and an unsustainable use of water during the dry summer months. The present study is focused on a statistical analysis of groundwater data to evaluate the spatial changes of water level and electrical conductivity in the coastal phreatic aquifer of the Emilia-Romagna (Northeast Italy) for the period from 2009 to 2018. Data from 35 wells distributed across the entire regional coastal area are used to establish a temporal trend, as well as correlations between salinity, water table level, and rainfall. Water table and salinity distribution maps for the entire study area are discussed regarding surface geology and water management. Most of the wells are in the beach wedge sand unit, which allows for easy connectivity between groundwater and surface water. Surface water and groundwater salinization are enhanced along the surface water bodies connected to the sea. The lowest water table level occurs in the western and northern parts of the study area, because of the semiconfined behavior of the aquifer. Only in the northernmost, close to the Po River, and in the southernmost parts of the study area does the groundwater remain fresh for the whole period considered due to river aquifer recharge. In the rest of the region, the thickness of freshwater lenses, where present, is less than 4.5 m. The existence of a water table level below sea level and high saline water at the bottom of the aquifer in most of the study area suggest that the aquifer is in unstable hydrodynamic conditions and groundwater quality is not fit for human consumption or for irrigation. This study is the first to provide a regional overview of the state of groundwater level and salinization within the coastal aquifer of the Emilia-Romagna Region; it also suggests that, overall, the salinization trend has slightly decreased from 2009 to 2018. Full article
(This article belongs to the Special Issue Focus on the Salinization Issue in the Mediterranean Area)
Show Figures

Figure 1

Figure 1
<p>Location of the coastal phreatic aquifer (<b>c</b>) of the Emilia-Romagna region (<b>b</b>), Northeast Italy (<b>a</b>). All monitoring points of surface and ground waters, weather stations and the main hydrology are also shown. Note: scale bar refers to the coastal study area only (<b>c</b>); coordinate reference system: WGS 1984 UTM Zone 32 N.</p>
Full article ">Figure 2
<p>Schematic stratigraphic section of the phreatic coastal aquifer (modified from Antonellini et al., 2008).</p>
Full article ">Figure 3
<p>Correlation map of electrical conductivity (EC), water table level (WT) and rainfall (RF) parameters. (Key: +Ve_corre_EC_&amp;_WT_RF: positive correlation between EC and with both WT and RF; −Ve_corre_EC_&amp;_WT_RF: negative correlation between EC and with both WT and RF; −Ve_corre_EC_RF: negative correlation between EC and RF, and positive correlation between EC and WT; −Ve_corre_EC_WT: negative correlation between EC and WT; −Ve_corre_WT_RF: negative correlation between WT and RF).</p>
Full article ">Figure 4
<p>Map of the significant EC trend of groundwater over the period 2009–2018.</p>
Full article ">Figure 5
<p>Map of the significant annual trend of WT level over the period 2009–2018.</p>
Full article ">Figure 6
<p>Surface geology of the coastal phreatic aquifer (modified from the Emilia-Romagna surface geology map 1:50,000).</p>
Full article ">Figure 7
<p>Average WT map in the unconfined coastal aquifer over the period 2009–2018.</p>
Full article ">Figure 8
<p>Average EC distribution map in the unconfined coastal aquifer over the period 2009–2018.</p>
Full article ">Figure 9
<p>Average water quality map of the unconfined aquifer showing the areal extent of freshwater, brackish, and saline water from 2009 to 2018.</p>
Full article ">Figure 10
<p>The freshwater–saltwater interface depth over the period 2009–2018.</p>
Full article ">
45 pages, 1042 KiB  
Review
The Biological Assessment and Rehabilitation of the World’s Rivers: An Overview
by Maria João Feio, Robert M. Hughes, Marcos Callisto, Susan J. Nichols, Oghenekaro N. Odume, Bernardo R. Quintella, Mathias Kuemmerlen, Francisca C. Aguiar, Salomé F.P. Almeida, Perla Alonso-EguíaLis, Francis O. Arimoro, Fiona J. Dyer, Jon S. Harding, Sukhwan Jang, Philip R. Kaufmann, Samhee Lee, Jianhua Li, Diego R. Macedo, Ana Mendes, Norman Mercado-Silva, Wendy Monk, Keigo Nakamura, George G. Ndiritu, Ralph Ogden, Michael Peat, Trefor B. Reynoldson, Blanca Rios-Touma, Pedro Segurado and Adam G. Yatesadd Show full author list remove Hide full author list
Water 2021, 13(3), 371; https://doi.org/10.3390/w13030371 - 31 Jan 2021
Cited by 109 | Viewed by 23727
Abstract
The biological assessment of rivers i.e., their assessment through use of aquatic assemblages, integrates the effects of multiple-stressors on these systems over time and is essential to evaluate ecosystem condition and establish recovery measures. It has been undertaken in many countries since the [...] Read more.
The biological assessment of rivers i.e., their assessment through use of aquatic assemblages, integrates the effects of multiple-stressors on these systems over time and is essential to evaluate ecosystem condition and establish recovery measures. It has been undertaken in many countries since the 1990s, but not globally. And where national or multi-national monitoring networks have gathered large amounts of data, the poor water body classifications have not necessarily resulted in the rehabilitation of rivers. Thus, here we aimed to identify major gaps in the biological assessment and rehabilitation of rivers worldwide by focusing on the best examples in Asia, Europe, Oceania, and North, Central, and South America. Our study showed that it is not possible so far to draw a world map of the ecological quality of rivers. Biological assessment of rivers and streams is only implemented officially nation-wide and regularly in the European Union, Japan, Republic of Korea, South Africa, and the USA. In Australia, Canada, China, New Zealand, and Singapore it has been implemented officially at the state/province level (in some cases using common protocols) or in major catchments or even only once at the national level to define reference conditions (Australia). In other cases, biological monitoring is driven by a specific problem, impact assessments, water licenses, or the need to rehabilitate a river or a river section (as in Brazil, South Korea, China, Canada, Japan, Australia). In some countries monitoring programs have only been explored by research teams mostly at the catchment or local level (e.g., Brazil, Mexico, Chile, China, India, Malaysia, Thailand, Vietnam) or implemented by citizen science groups (e.g., Southern Africa, Gambia, East Africa, Australia, Brazil, Canada). The existing large-extent assessments show a striking loss of biodiversity in the last 2–3 decades in Japanese and New Zealand rivers (e.g., 42% and 70% of fish species threatened or endangered, respectively). A poor condition (below Good condition) exists in 25% of South Korean rivers, half of the European water bodies, and 44% of USA rivers, while in Australia 30% of the reaches sampled were significantly impaired in 2006. Regarding river rehabilitation, the greatest implementation has occurred in North America, Australia, Northern Europe, Japan, Singapore, and the Republic of Korea. Most rehabilitation measures have been related to improving water quality and river connectivity for fish or the improvement of riparian vegetation. The limited extent of most rehabilitation measures (i.e., not considering the entire catchment) often constrains the improvement of biological condition. Yet, many rehabilitation projects also lack pre-and/or post-monitoring of ecological condition, which prevents assessing the success and shortcomings of the recovery measures. Economic constraints are the most cited limitation for implementing monitoring programs and rehabilitation actions, followed by technical limitations, limited knowledge of the fauna and flora and their life-history traits (especially in Africa, South America and Mexico), and poor awareness by decision-makers. On the other hand, citizen involvement is recognized as key to the success and sustainability of rehabilitation projects. Thus, establishing rehabilitation needs, defining clear goals, tracking progress towards achieving them, and involving local populations and stakeholders are key recommendations for rehabilitation projects (Table 1). Large-extent and long-term monitoring programs are also essential to provide a realistic overview of the condition of rivers worldwide. Soon, the use of DNA biological samples and eDNA to investigate aquatic diversity could contribute to reducing costs and thus increase monitoring efforts and a more complete assessment of biodiversity. Finally, we propose developing transcontinental teams to elaborate and improve technical guidelines for implementing biological monitoring programs and river rehabilitation and establishing common financial and technical frameworks for managing international catchments. We also recommend providing such expert teams through the United Nations Environment Program to aid the extension of biomonitoring, bioassessment, and river rehabilitation knowledge globally. Full article
(This article belongs to the Special Issue The Ecological Assessment of Rivers and Estuaries: Present and Future)
Show Figures

Figure 1

Figure 1
<p>Countries referred in this study regarding their status in biological monitoring and rehabilitation of rivers.</p>
Full article ">
26 pages, 1698 KiB  
Article
Jacobian Free Methods for Coupling Transport with Chemistry in Heterogenous Porous Media
by Laila Amir and Michel Kern
Water 2021, 13(3), 370; https://doi.org/10.3390/w13030370 - 31 Jan 2021
Cited by 3 | Viewed by 3393
Abstract
Reactive transport plays an important role in various subsurface applications, including carbon dioxide sequestration, nuclear waste storage, biogeochemistry and the simulation of hydro–thermal reservoirs. The model couples a set of partial differential equations, describing the transport of chemical species, to nonlinear algebraic or [...] Read more.
Reactive transport plays an important role in various subsurface applications, including carbon dioxide sequestration, nuclear waste storage, biogeochemistry and the simulation of hydro–thermal reservoirs. The model couples a set of partial differential equations, describing the transport of chemical species, to nonlinear algebraic or differential equations, describing the chemical reactions. Solution methods for the resulting large nonlinear system can be either fully coupled or can iterate between transport and chemistry. This paper extends previous work by the authors where an approach based on the Newton–Krylov method applied to a reduced system has been developed. The main feature of the approach is to solve the nonlinear system in a fully coupled manner while keeping transport and chemistry modules separate. Here we extend the method in two directions. First, we take into account mineral precipitation and dissolution reactions by using an interior point Newton method, so as to avoid the usual combinatorial approach. Second, we study two-dimensional heterogeneous geometries. We show how the method can make use of an existing transport solver, used as a black box. We detail the methods and algorithms for the individual modules, and for the coupling step. We show the performance of the method on synthetic examples. Full article
Show Figures

Figure 1

Figure 1
<p>Triangular submesh for a cell <span class="html-italic">K</span>.</p>
Full article ">Figure 2
<p>Number of iterations for the iron precipitation example. (<b>Left</b>) map as a function of pH and pE, (<b>Right</b>) histogram of iteration number.</p>
Full article ">Figure 3
<p>pH–pE diagram (Pourbaix diagram) for iron. In each region, the dominant species is shown.</p>
Full article ">Figure 4
<p>Total aqueous concentrations for <span class="html-italic">y</span> = 0.0075, at <span class="html-italic">t</span> = 6 h.</p>
Full article ">Figure 5
<p>Evolution of concentrations at the end of the column.</p>
Full article ">Figure 6
<p>Total aqueous concentrations at <span class="html-italic">t</span> = 6 h.</p>
Full article ">Figure 7
<p>Total aqueous concentrations for <math display="inline"><semantics> <mrow> <mi>y</mi> <mo>=</mo> <mn>0.0075</mn> <mspace width="3.33333pt"/> <mi mathvariant="normal">m</mi> </mrow> </semantics></math>, at <math display="inline"><semantics> <mrow> <mi>t</mi> <mo>=</mo> <mn>6</mn> </mrow> </semantics></math> h.</p>
Full article ">Figure 8
<p>Number of iterations per time-step for the first 20 time-steps for the various solution methods.</p>
Full article ">Figure 9
<p>Number of Iterations as a function of the mesh size for the various solution methods at <span class="html-italic">t</span> = 0.5 h.</p>
Full article ">Figure 10
<p>Geometry of domain for the SHPCO2 Benchmark.</p>
Full article ">Figure 11
<p>Pressure and velocity for the SHPCO2 model.</p>
Full article ">Figure 12
<p>Concentrations of the gas CO<sub>2</sub>(g), the calcite CaCO<sub>3</sub>, H<sup>+</sup> and the tracer Cl<sup>−</sup> at <span class="html-italic">t</span> = 0 year.</p>
Full article ">Figure 13
<p>Concentrations of the gas CO<sub>2</sub>(g), the calcite CaCO<sub>3</sub>, H<sup>+</sup> and the tracer Cl<sup>−</sup> at <span class="html-italic">t</span> = 302 year.</p>
Full article ">Figure 14
<p>Concentrations of the gas CO<sub>2</sub>(g), the calcite CaCO<sub>3</sub>, H<sup>+</sup> and the tracer Cl<sup>−</sup> at <span class="html-italic">t</span> = 1352 year.</p>
Full article ">Figure 15
<p>Concentrations of the gas CO<sub>2</sub>(g), the calcite CaCO<sub>3</sub>, H<sup>+</sup> and the tracer Cl<sup>−</sup> at <span class="html-italic">t</span> = 1852 year.</p>
Full article ">Figure 16
<p>CO<sub>2</sub>(g), at <span class="html-italic">t</span> = 302 y (left image: coarse mesh, right image: fine mesh).</p>
Full article ">Figure 17
<p>CO<sub>2</sub>(g), at <span class="html-italic">t</span> = 800 y (left image: coarse mesh, right image: fine mesh).</p>
Full article ">
13 pages, 5261 KiB  
Article
A Highly Packed Biofilm Reactor with Cycle Cleaning for the Efficient Treatment of Rural Wastewater
by Yanan Luan, Chen Qiu, Yaoxian Li, Weichang Kang, Jianhua Zhang, Zuliang Liao and Xuejun Bi
Water 2021, 13(3), 369; https://doi.org/10.3390/w13030369 - 31 Jan 2021
Cited by 4 | Viewed by 3374
Abstract
Biological treatment processes perform satisfactory in wastewater treatment, but the relatively high cost and complicated maintenance limit its application in rural areas. In this study, a highly packed biofilm reactor (HPBR), with a 90% packing ratio of carriers in the bioreactor, was designed [...] Read more.
Biological treatment processes perform satisfactory in wastewater treatment, but the relatively high cost and complicated maintenance limit its application in rural areas. In this study, a highly packed biofilm reactor (HPBR), with a 90% packing ratio of carriers in the bioreactor, was designed for rural wastewater treatment. The results showed that the removal rates for chemical oxygen demand (COD) and ammonia were 3.04 ± 1.81 kg/m3/d and 0.49 ± 0.18 kg/m3/d, respectively. Besides, the removal efficiency of total inorganic nitrogen (TIN) was 35.4% by the HPBR. The removal capacity of the HPBR is higher than other reported systems with fewer operational costs and maintenance. High-throughput sequencing was applied to further investigate the kinetics and principals. Microorganisms capable of simultaneous nitrification-denitrification were found to be dominant species in the HPBR system, which indicated that the nitrogen removal in HPBR is governed by simultaneous nitrification-denitrification. These findings suggest that HPBR can be used as an efficient reactor for rural wastewater treatment, demonstrating its feasibility in real applications. Full article
(This article belongs to the Section Wastewater Treatment and Reuse)
Show Figures

Figure 1

Figure 1
<p>Schematic diagram of the highly packed biofilm reactor (HPBR) under (<b>a</b>) normal operation and (<b>b</b>) cycle cleaning process.</p>
Full article ">Figure 2
<p>Nutrients removal performance in the bioreactor.</p>
Full article ">Figure 3
<p>Digital photos of biofilm on the carriers in (<b>a</b>) aeration section and (<b>b</b>) filtration section.</p>
Full article ">Figure 4
<p>The average nitrification rate before and after cycle cleaning process (<span class="html-italic">p</span> = 0.037, <span class="html-italic">n</span> = 7) (<b>a</b>), the average soluble chemical oxygen demand (SCOD) removal rate before and after cycle cleaning process (<span class="html-italic">p</span> = 0.044, <span class="html-italic">n</span> = 7) (<b>b</b>), digital photo of biofilm before cycle cleaning (<b>c</b>), and digital photo of biofilm after cycle cleaning process (<b>d</b>).</p>
Full article ">Figure 5
<p>A typical cyclic test for degradation of SCOD and nitrogen before and after cycle cleaning process.</p>
Full article ">Figure 6
<p>Microbial community profiles of three biofilm samples at phylum level. The coordinate scale refers to the relative abundance of the microbial distribution in the samples (%).</p>
Full article ">Figure 7
<p>Relative abundance of nitrogen removal functional bacterial communities at genus level of biofilm before cleaning (BC) and after cleaning (AC).</p>
Full article ">
12 pages, 4717 KiB  
Technical Note
Damage Characteristics and Mechanism of the 2017 Groundwater Inrush Accident That Occurred at Dongyu Coalmine in Taiyuan, Shanxi, China
by Bin Luo, Yajun Sun, Zhimin Xu, Ge Chen, Li Zhang, Weining Lu, Xianming Zhao and Huiqing Yuan
Water 2021, 13(3), 368; https://doi.org/10.3390/w13030368 - 31 Jan 2021
Cited by 11 | Viewed by 2482
Abstract
On 22 May 2017, a groundwater inrush accident occurred in the gob area of coal floor at Dongyu Coal Mine in Qingxu County, Shanxi Province, China. The water inrush accident caused great damage, among which six people died and the direct economic loss [...] Read more.
On 22 May 2017, a groundwater inrush accident occurred in the gob area of coal floor at Dongyu Coal Mine in Qingxu County, Shanxi Province, China. The water inrush accident caused great damage, among which six people died and the direct economic loss was about CNY 5.05 million. An elliptical permeable passage appeared at the floor of the water inrush point, and the lithology of the outburst is mainly fragmented sandy mudstone and siltstone of coal roof No.2 in the lower layer of coal seam No.3, which is currently being mined, with a peak inflow of 500 m3/h. The water inrush happened due to following reasons: There is an abandoned stagnant water-closed roadway in coal seam No.2, which is the lower mine group of coal seam No.3. The abandoned roadway of coal seam No.2 is an inclined roadway. The water level of the roadway far away from the accident point is higher than the floor elevation of coal seam No.3. Under the joint action of water pressure, mining disturbance, and weakening of goaf water immersion, the original equilibrium state was broken, resulting in the destruction of the only 7 m water-barrier rock pillar between coal seam No.3 and coal seam No.2. The water in the goaf led upward along the roof crack, gradually evolved from seepage to gushing water, and a large amount of goaf water poured into the roadway in the working face of the 03304 panel, finally leading to the occurrence of catastrophic water inrush. Technically, the miners did not implement the technical provisions of the coal mine water control regulations, leading to the accident. In addition, the failure to arrange evacuees to a safe location after apparent signs of water inrush also increased the catastrophic level of the accident. Full article
(This article belongs to the Special Issue Groundwater Sustainable Exploitation)
Show Figures

Figure 1

Figure 1
<p>Details of some properties of water inrush accidents from 2000 to 2020 in China.</p>
Full article ">Figure 2
<p>Distribution of 11 water inrush accidents in Shanxi and location relation diagram of adjacent mines of Dongyu coal mine.</p>
Full article ">Figure 3
<p>Strata and aquifer distribution at Dongyu coal mine.</p>
Full article ">Figure 4
<p>Schematic diagram of plane analysis of the water inrush point.</p>
Full article ">Figure 5
<p>Sandy mudstone, siltstone, and other broken rock deposits in the water inrush site. (<b>a</b>) Board marked by the investigation team at the scene of the accident; (<b>b</b>) gravel with different particle sizes.</p>
Full article ">Figure 6
<p>A collapse pit formed at the outlet point. (<b>a</b>) Power switches and cables that fell into the collapse pits; (<b>b</b>) integrated tunneling machine that fell into the collapse crater.</p>
Full article ">Figure 7
<p>Profile diagram of the water inrush location in the heading direction.</p>
Full article ">Figure 8
<p>Section diagram of the water inrush position perpendicular to the excavation direction.</p>
Full article ">Figure 9
<p>Horizon structure of coal seams No.3 and No.2.</p>
Full article ">Figure 10
<p>Relationship curve between water pressure and thickness of the floor safety barrier.</p>
Full article ">
18 pages, 6407 KiB  
Article
Using AHP and Spatial Analysis to Determine Water Surface Storage Suitability in Cambodia
by Michael Ward, Cristina Poleacovschi and Michael Perez
Water 2021, 13(3), 367; https://doi.org/10.3390/w13030367 - 31 Jan 2021
Cited by 9 | Viewed by 3487
Abstract
Cambodia suffers from devastating droughts in the dry season and floods in the wet season. These events’ impacts are further amplified by ineffective water resources infrastructure that cannot retain water during the dry season. Water harvesting (the collection and management of floodwater or [...] Read more.
Cambodia suffers from devastating droughts in the dry season and floods in the wet season. These events’ impacts are further amplified by ineffective water resources infrastructure that cannot retain water during the dry season. Water harvesting (the collection and management of floodwater or rainwater runoff to increase water supply for domestic and agricultural use) is an approach that could improve Cambodia’s resiliency against droughts and floods. Despite the known benefits of water harvesting, there are currently few studies on water harvesting suitability in Cambodia. This research argues that suitable water harvesting sites can be identified by combining various expertise and evaluating hydrologic site conditions. Thirty-one local and USA water infrastructure experts made pairwise comparisons between essential engineering criteria: soil drainage, geologic porosity, precipitation, land cover, and slope. Then, model weights were calculated based on the comparisons. Using the model weights, a water harvesting suitability model showed that 19% of Cambodian land has high suitability, and about 13% of the land has the best suitability. This water harvesting model can help guide future water infrastructure projects to improve climate resiliency by identifying suitable sites for water harvesting reservoirs. Full article
(This article belongs to the Section Hydrology)
Show Figures

Figure 1

Figure 1
<p>Soil drainage map of Cambodia. Adapted from FAO’s [<a href="#B30-water-13-00367" class="html-bibr">30</a>] Harmonized World Soil Database.</p>
Full article ">Figure 2
<p>Geologic porosity map of Cambodia. Adapted from Gleeson’s et al. [<a href="#B31-water-13-00367" class="html-bibr">31</a>] GLMYPHS database.</p>
Full article ">Figure 3
<p>Annual precipitation map of Cambodia. Adapted from UCSB’s [<a href="#B32-water-13-00367" class="html-bibr">32</a>] CHIRPS database.</p>
Full article ">Figure 4
<p>Calculated slope map of Cambodia. Adapted from Open Development Cambodia’s [<a href="#B33-water-13-00367" class="html-bibr">33</a>] georelief map.</p>
Full article ">Figure 5
<p>Land cover map of Cambodia. Adapted from ADPC’s [<a href="#B34-water-13-00367" class="html-bibr">34</a>] land use database.</p>
Full article ">Figure 6
<p>Water retention suitability hierarchy.</p>
Full article ">Figure 7
<p>Cambodia water harvesting suitability.</p>
Full article ">Figure 8
<p>Distribution of suitable land in Cambodia for water harvesting.</p>
Full article ">Figure 9
<p>Identified watershed and potential reservoir location. Location highlighted in red. Adapted from WWF’s [<a href="#B37-water-13-00367" class="html-bibr">37</a>] HydroSHEDs database.</p>
Full article ">
18 pages, 3104 KiB  
Article
Evaluating the Potential of a Water-Energy-Food Nexus Approach toward the Sustainable Development of Bangladesh
by Mohammad Nahidul Karim and Bassel Daher
Water 2021, 13(3), 366; https://doi.org/10.3390/w13030366 - 31 Jan 2021
Cited by 4 | Viewed by 4952
Abstract
In pursuit of continuous economic development, Bangladesh has undertaken long-term plans to boost its productivity in the agriculture, energy, and industrial sectors and to align with the United Nations Sustainable Development Goals (SDGs). Unless these strong interconnections and cross sectoral impacts are recognized, [...] Read more.
In pursuit of continuous economic development, Bangladesh has undertaken long-term plans to boost its productivity in the agriculture, energy, and industrial sectors and to align with the United Nations Sustainable Development Goals (SDGs). Unless these strong interconnections and cross sectoral impacts are recognized, achievement of the future policy goals and national priorities of the concerned ministries regarding food self-sufficiency, cleaner energy sources, and water availability will be compromised. This study focuses on evaluating the impacts of cross-sectoral policy decisions on the interconnected resource systems at a national scale in Bangladesh. A quantitative analysis is performed to identify resource requirements, synergies, and trade-offs related to a set of future strategies. The analysis concludes by showing that land is the most limiting resource for future expansion and that fresh water will become a critical resource if alternative sources of water are not explored, and, that energy generation, if coal and other fossil fuels are favored over alternative energy sources, will significantly add to the total carbon emissions. Given the limitations of land available for agricultural expansion, of renewable water resources, and the challenges in meeting increasing water, energy, and food demands, the strong interdependencies among the interconnected resource systems must be accounted for. The SDG and national priority indicators are found to improve under scenarios for which resources are conserved via alternative sources. Full article
(This article belongs to the Special Issue Water Systems Using Affordable and Clean Energy)
Show Figures

Graphical abstract

Graphical abstract
Full article ">Figure 1
<p>Resource balance and future resource demand of Bangladesh.</p>
Full article ">Figure 2
<p>Identified resource interactions of the system for the developed analytical tool.</p>
Full article ">Figure 3
<p>Conceptual framework for water, energy, and food assessment.</p>
Full article ">Figure 4
<p>Assessment of resource requirements projected for year 2030 and 2041 under BAU scenario. The percentage change in SDG and NPI indicators for the BAU scenario, compared to base year 2016.</p>
Full article ">Figure 5
<p>Comparative evaluation of scenarios. (<b>a</b>) Land demand, (<b>b</b>) fresh water demand, and (<b>c</b>) food import. (<b>d</b>) Emission from crop production, (<b>e</b>) renewable energy share in electricity production, and (<b>f</b>) carbon emission for listed scenarios.</p>
Full article ">Figure 6
<p>Comparative impact on indicators, both SDG and national priority indicators (NPI) attributed to each of the assessed scenarios. (<b>a</b>) Variation in yield, (<b>b</b>) land required for food production, (<b>c</b>) fresh water withdrawal as the percent of national renewable water reserve, (<b>d</b>) treated waste water as a percentage of the total water usage, (<b>e</b>) carbon emission from electricity generation, and (<b>f</b>) renewable energy share in electricity.</p>
Full article ">Figure 7
<p>Second Filter-SDG Performance by an assessed value of the indicators.</p>
Full article ">
18 pages, 2507 KiB  
Article
Technological Spaces in the Semi-Arid High Plains: Examining Well Ownership and Investment in Water-Saving Appliances
by Brock Ternes
Water 2021, 13(3), 365; https://doi.org/10.3390/w13030365 - 31 Jan 2021
Cited by 2 | Viewed by 3640
Abstract
Groundwater depletion has been a consequential problem in Kansas, a drought-prone state widely reliant on the High Plains aquifer. This manuscript explores well ownership’s moderating effects on the relationships between awareness of water supplies and the use of water-saving devices. It assesses one [...] Read more.
Groundwater depletion has been a consequential problem in Kansas, a drought-prone state widely reliant on the High Plains aquifer. This manuscript explores well ownership’s moderating effects on the relationships between awareness of water supplies and the use of water-saving devices. It assesses one of the only quantitative datasets of private water well owners used in social scientific research (n = 864) and discusses the intricate results of multi-group structural equation models with respondents organized by their water supplies. Well ownership and water literacy are significantly correlated to owning water-conservation technologies, and well ownership combined with access to municipal water weakens the correlations between awareness and owning water-saving appliances. Full article
Show Figures

Figure 1

Figure 1
<p>The High Plains aquifer [<a href="#B9-water-13-00365" class="html-bibr">9</a>].</p>
Full article ">Figure 2
<p>Model of owning water-saving appliances for indoor and outdoor usage regressed on well ownership (<span class="html-italic">n</span> = 847). CFI: comparative fit index; RMSEA: root mean square error of approximation.</p>
Full article ">Figure 3
<p>Model of owning water-saving appliances for indoor and outdoor usage regressed on awareness of water supplies for non-well owners (<span class="html-italic">n</span> = 448).</p>
Full article ">Figure 4
<p>Model of owning water-saving appliances for indoor and outdoor usage regressed on awareness of water supplies for well owners (<span class="html-italic">n</span> = 407).</p>
Full article ">Figure 5
<p>Model of owning water-saving appliances for indoor and outdoor usage regressed on awareness of water supplies for well owners without municipal connections (<span class="html-italic">n</span> = 141).</p>
Full article ">Figure 6
<p>Model of owning water-saving appliances for indoor and outdoor usage regressed on awareness of water supplies for well owners with municipal connections (<span class="html-italic">n</span> = 246).</p>
Full article ">Figure 7
<p>Model of owning water-saving appliances for indoor and outdoor usage regressed on awareness of water supplies for domestic well owners (<span class="html-italic">n</span> = 145).</p>
Full article ">Figure 8
<p>Model of owning water-saving appliances for indoor and outdoor usage regressed on awareness of water supplies for lawn and garden well owners (<span class="html-italic">n</span> = 135).</p>
Full article ">Figure 9
<p>Model of owning water-saving appliances for indoor and outdoor usage regressed on awareness of water supplies for feedlot well owners (<span class="html-italic">n</span> = 66).</p>
Full article ">Figure 10
<p>Model of owning water-saving appliances for indoor and outdoor usage regressed on awareness of water supplies for irrigation well owners (<span class="html-italic">n</span> = 61).</p>
Full article ">
24 pages, 6512 KiB  
Article
Potential Dam Breach Analysis and Flood Wave Risk Assessment Using HEC-RAS and Remote Sensing Data: A Multicriteria Approach
by Emmanouil Psomiadis, Lefteris Tomanis, Antonis Kavvadias, Konstantinos X. Soulis, Nikos Charizopoulos and Spyros Michas
Water 2021, 13(3), 364; https://doi.org/10.3390/w13030364 - 31 Jan 2021
Cited by 53 | Viewed by 8859
Abstract
Dam breach has disastrous consequences for the economy and human lives. Floods are one of the most damaging natural phenomena, and some of the most catastrophic flash floods are related to dam collapses. The goal of the present study is to analyse the [...] Read more.
Dam breach has disastrous consequences for the economy and human lives. Floods are one of the most damaging natural phenomena, and some of the most catastrophic flash floods are related to dam collapses. The goal of the present study is to analyse the impact of a possible failure–collapse on a potentially affected area downstream of the existing Bramianos dam on southern Crete Island. HEC-RAS hydraulic analysis software was used to study the dam breach, the flood wave propagation, and estimate the extent of floods. The analysis was performed using two different relief datasets of the same area: a digital elevation model (DEM) taken from very high-resolution orthophoto images (OPH) of the National Cadastre and Mapping Agency SA and a detailed digital surface model (DSM) extracted from aerial images taken by an unmanned aerial vehicle (UAV). Remote sensing data of the Sentinel-2 satellite and OPH were utilised to create the geographic information system (GIS) layers of a thorough land use/cover classification (LULC) for the potentially flooded area, which was used to assess the impact of the flood wave. Different dam breach and flood scenarios, where the water flows over man-made structures, settlements, and olive tree cultivations, were also examined. The study area is dominated mainly by three geological formations with different hydrogeological characteristics that dictated the positioning and structure of the dam and determine the processes that shape the geomorphology and surface roughness of the floodplain, affecting flow conditions. The results show that the impact of a potential dam break at Bramianos dam is serious, and appropriate management measures should be taken to reduce the risk. The water flow downstream of the collapsed dam depends on the water volume stored in the reservoir. Moreover, the comparison of DSM and DEM cases shows that the detailed DSM may indicate more accurately the surface relief and existing natural obstacles such as vegetation, buildings, and greenhouses, enabling more realistic hydraulic simulation results. Dam breach flood simulations and innovative remote sensing data can provide valuable outcomes for engineers and stakeholders for decision-making and planning in order to confront the consequences of similar incidents worldwide. Full article
Show Figures

Figure 1

Figure 1
<p>(<b>a</b>) Location of the study area; (<b>b</b>) Bramianos basin and drainage network; (<b>c</b>) representation of Bramianos basin downstream area in very high-resolution orthophotos, showing the LULC, the Gra-Lygia settlement, the Bramianos stream and the adjacent torrents as well as the dam and the lake position and its spillway.</p>
Full article ">Figure 2
<p>Cross-section of the Bramianos dam.</p>
Full article ">Figure 3
<p>The geological map of the Bramianos basin.</p>
Full article ">Figure 4
<p>(<b>a</b>) Orthomosaic of Bramianos dam reservoir derived from unmanned aerial vehicle (UAV) aerial data; (<b>b</b>) 3D mesh file of the dam’s downstream area that created from a 3D point cloud; (<b>c</b>,<b>d</b>) digital elevation model (DEM) and digital surface model (DSM) from a selected part of the basin (2.5 km downstream of the dam).</p>
Full article ">Figure 5
<p>Land use/cover classification (LULC) classification image of the broader area.</p>
Full article ">Figure 6
<p>Illustration of the comparison between (<b>a</b>) flood extents and (<b>b</b>) the discharge hydrographs obtained with the diffusion wave approximation and the complete set of Saint-Venant equations.</p>
Full article ">Figure 7
<p>Hydrographs of water flow quantity in the downstream area of the dam after the dam breach in the two different scenarios (overtopping and piping).</p>
Full article ">Figure 8
<p>Maps of flow depth and velocity, utilising DEM and DSM in the overtopping scenario. (<b>a</b>) Flow depth using DEM; (<b>b</b>) flow depth using DSM; (<b>c</b>) flow velocity using DEM; (<b>d</b>) Flow velocity using DSM.</p>
Full article ">Figure 9
<p>Maps of flow depth and velocity, utilising DEM and DSM in the piping scenario. (<b>a</b>) Flow depth using DEM; (<b>b</b>) flow depth using DSM; (<b>c</b>) flow velocity using DEM; (<b>d</b>) flow velocity using DSM.</p>
Full article ">Figure 10
<p>Maps of arrival time, utilising DEM and DSM in (<b>a</b>,<b>b</b>) overtopping and (<b>c</b>,<b>d</b>) piping scenarios.</p>
Full article ">Figure 11
<p>Hazard analysis maps according to the ASCE flood intensity criterion for the two fracture scenarios using the two-different 3D digital models. (<b>a</b>) Overtopping scenario using DEM; (<b>b</b>) overtopping scenario using DSM; (<b>c</b>) piping scenario using DEM; (<b>d</b>) piping scenario using DSM.</p>
Full article ">
13 pages, 4276 KiB  
Article
On Neglecting Free-Stream Turbulence in Numerical Simulation of the Wind-Induced Bias of Snow Gauges
by Arianna Cauteruccio, Matteo Colli and Luca G. Lanza
Water 2021, 13(3), 363; https://doi.org/10.3390/w13030363 - 31 Jan 2021
Cited by 4 | Viewed by 2545
Abstract
Numerical studies of the wind-induced bias of precipitation measurements assume that turbulence is generated by the interaction of the airflow with the gauge body, while steady and uniform free-stream conditions are imposed. However, wind is turbulent in nature due to the roughness of [...] Read more.
Numerical studies of the wind-induced bias of precipitation measurements assume that turbulence is generated by the interaction of the airflow with the gauge body, while steady and uniform free-stream conditions are imposed. However, wind is turbulent in nature due to the roughness of the site and the presence of obstacles, therefore precipitation gauges are immersed in a turbulent flow. Further to the turbulence generated by the flow-gauge interaction, we investigated the natural free-stream turbulence and its influence on precipitation measurement biases. Realistic turbulence intensity values at the gauge collector height were derived from 3D sonic anemometer measurements. Large Eddy Simulations of the turbulent flow around a chimney-shaped gauge were performed under uniform and turbulent free-stream conditions, using geometrical obstacles upstream of the gauge to provide the desired turbulence intensity. Catch ratios for dry snow particles were obtained using a Lagrangian particle tracking model, and the collection efficiency was calculated based on a suitable particle size distribution. The collection efficiency in turbulent conditions showed stronger undercatch at the investigated wind velocity and snowfall intensity below 10 mm h−1, demonstrating that adjustment curves based on the simplifying assumption of uniform free-stream conditions do not accurately portray the wind-induced bias of snow measurements. Full article
Show Figures

Figure 1

Figure 1
<p>(<b>a</b>) The Nafferton (U.K.) field test site with the 3D Sonic anemometer and EML<sup>©</sup> aerodynamic rain gauges installed at the ground surface, and (<b>b</b>) high-frequency wind measurements (black line) and moving average with N = 125 (grey line).</p>
Full article ">Figure 2
<p>(<b>a</b>) Portion of the geometric setup with the three pillars positioned upstream of the gauge, and the wind direction indicated by the white arrow. (<b>b</b>) Horizontal section (<span class="html-italic">x</span>,<span class="html-italic">y</span> plane) and gradual refinement of the computational mesh close to one sample pillar at a generic elevation.</p>
Full article ">Figure 3
<p>(<b>a</b>) Refinement region around the Geonor gauge body in the central vertical section (<span class="html-italic">x</span>,<span class="html-italic">z</span> plane at <span class="html-italic">y</span> = 0) and (<b>b</b>) gradual refinement close to its surface in the horizontal section at the gauge collector elevation (<span class="html-italic">x</span>,<span class="html-italic">y</span> plane at <span class="html-italic">z</span> = −2 m).</p>
Full article ">Figure 4
<p>Mean values and standard deviations of turbulent fluctuations (left-hand axis) and sample size (right-hand axis) for each wind class, measured by a 3D sonic anemometer at the Nafferton (U.K.) field test site.</p>
Full article ">Figure 5
<p>Relative turbulence intensity for the three Cartesian directions for each wind class, measured by a 3D sonic anemometer at the Nafferton (U.K.) field test site.</p>
Full article ">Figure 6
<p>Decrease of the three numerical relative turbulence intensity profiles at the gauge collector elevation along the spatial domain between the position of the obstacles (<span class="html-italic">x/D</span> = −70) and the gauge (<span class="html-italic">x/D</span> = 0).</p>
Full article ">Figure 7
<p>Normalized magnitude (<span class="html-italic">U<sub>mag</sub>/U<sub>ref</sub></span>) of the instantaneous flow velocity in the vertical plane (<span class="html-italic">x</span>,<span class="html-italic">z</span>) at <span class="html-italic">y</span>/<span class="html-italic">D</span> = 0 for the turbulent free-stream conditions.</p>
Full article ">Figure 8
<p>Normalized magnitude of the instantaneous flow velocity (<span class="html-italic">U<sub>mag</sub></span>/<span class="html-italic">U<sub>ref</sub></span>) in the horizontal plane (<span class="html-italic">x</span>,<span class="html-italic">y</span>) at the gauge collector elevation for the turbulent free-stream conditions.</p>
Full article ">Figure 9
<p>Normalized transversal component <span class="html-italic">(U<sub>y</sub></span>/<span class="html-italic">U<sub>ref</sub></span>) of the instantaneous flow velocity in the horizontal plane (<span class="html-italic">x</span>,<span class="html-italic">y</span>) at the gauge collector elevation for the turbulent free-stream conditions.</p>
Full article ">Figure 10
<p>CE curves as a function of <span class="html-italic">SI</span>, obtained under uniform and turbulent free-stream conditions at <span class="html-italic">U<sub>ref</sub></span> = 2.5 m s<sup>−1</sup>.</p>
Full article ">Figure 11
<p>Percentage number and volume of particles having a diameter less than 2 mm within a unit volume of the atmosphere, based on the assumed particle size distribution (PSD).</p>
Full article ">
37 pages, 4636 KiB  
Article
Pollen Geochronology from the Atlantic Coast of the United States during the Last 500 Years
by Margaret A. Christie, Christopher E. Bernhardt, Andrew C. Parnell, Timothy A. Shaw, Nicole S. Khan, D. Reide Corbett, Ane García-Artola, Jennifer Clear, Jennifer S. Walker, Jeffrey P. Donnelly, Tobias R. Hasse and Benjamin P. Horton
Water 2021, 13(3), 362; https://doi.org/10.3390/w13030362 - 31 Jan 2021
Cited by 2 | Viewed by 4246
Abstract
Building robust age–depth models to understand climatic and geologic histories from coastal sedimentary archives often requires composite chronologies consisting of multi-proxy age markers. Pollen chronohorizons derived from a known change in vegetation are important for age–depth models, especially those with other sparse or [...] Read more.
Building robust age–depth models to understand climatic and geologic histories from coastal sedimentary archives often requires composite chronologies consisting of multi-proxy age markers. Pollen chronohorizons derived from a known change in vegetation are important for age–depth models, especially those with other sparse or imprecise age markers. However, the accuracy of pollen chronohorizons compared to other age markers and the impact of pollen chronohorizons on the precision of age–depth models, particularly in salt marsh environments, is poorly understood. Here, we combine new and published pollen data from eight coastal wetlands (salt marshes and mangroves) along the Atlantic Coast of the United States (U.S.) from Florida to Connecticut to define the age and uncertainty of 17 pollen chronohorizons. We found that 13 out of 17 pollen chronohorizons were consistent when compared to other age markers (radiocarbon, radionuclide 137Cs and pollution markers). Inconsistencies were likely related to the hyperlocality of pollen chronohorizons, mixing of salt marsh sediment, reworking of pollen from nearby tidal flats, misidentification of pollen signals, and inaccuracies in or misinterpretation of other age markers. Additionally, in a total of 24 models, including one or more pollen chronohorizons, increased precision (up to 41 years) or no change was found in 18 models. Full article
(This article belongs to the Special Issue Climate Change and Anthropogenic Impact on Coastal Environments)
Show Figures

Figure 1

Figure 1
<p>Conceptual diagram of dating techniques and their age ranges highlighting the potential chronological gap between radiocarbon dating and pollution markers that pollen chronohorizons may circumvent.</p>
Full article ">Figure 2
<p>Map of U.S. Atlantic Coast (<b>A</b>) showing the relative location of eight published and unpublished study sites, as well as individual site maps for Connecticut (<b>B</b>), Delaware (<b>C</b>), Maryland (<b>D</b>), and Southern Florida (<b>E</b>). Maps of other sites can be found in the original publications.</p>
Full article ">Figure 3
<p>Timing of pollen chronohorizons documented in the literature at each study site. Pollen data from published sites are available in the original publications.</p>
Full article ">Figure 4
<p>Pollen stratigraphic diagrams plotted against the NP Bchron predicted ages to compare the age plus uncertainty of the pollen chronohorizons with the ages derived from other age markers at the depth where the pollen chronohorizon occurred for Connecticut (<b>A</b>), Delaware (<b>B</b>), Maryland (<b>C</b>), and Southern Florida (<b>D</b>). Lines indicate the pollen chronohorizons; shading indicates the uncertainty associated with each pollen chronohorizon. The chronohorizons are as follows: (3a) chestnut blight; (1d) beginning of the forestry industry; (1a) initial land clearance; (1c) lowest amount of forest cover; (1b) peak deforestation; and (3b) <span class="html-italic">Casuarina</span> introduction (<a href="#water-13-00362-t003" class="html-table">Table 3</a>).</p>
Full article ">Figure 5
<p>Comparison of the difference in width of the 50% UI between the WP (all chronohorizon in red) and NP (blue) models over the interval from 1500 CE through the present (see also <a href="#water-13-00362-f0A2" class="html-fig">Figure A2</a>). The red and blue lines are plotted transparently so that lighter areas represent widths that are predicted less frequently by Bchron, while darker areas represent widths that are predicted more frequently. The depth of the pollen chronohorizons is plotted using colored triangles which correspond to <a href="#water-13-00362-f003" class="html-fig">Figure 3</a>.</p>
Full article ">Figure 6
<p>Median Bchron age–depth models for all study sites with 50% UIs showing the WP model in red and the NP model in blue. These were calculated based on the median of all 31 replicates. UMV refers to lead pollution originating in the Upper Mississippi Valley.</p>
Full article ">Figure A1
<p>Pollen stratigraphic diagrams for published data plotted against the NP Bchron predicted ages to compare the age plus uncertainty of the pollen chronohorizons with the ages derived from other age markers at the depth where the pollen chronohorizon occurred for New York (<b>A</b>), New Jersey (<b>B</b>), North Carolina (<b>C</b>), and Northern Florida (<b>D</b>). Colored lines indicate the pollen chronohorizons; colored shading indicates the uncertainty associated with each pollen chronohorizon. The colors refer to <a href="#water-13-00362-f003" class="html-fig">Figure 3</a>. The chronohorizons are as follows: (2a) reforestation; (1d) beginning of the forestry industry; (1a) initial land clearance; (1c) lowest amount of forest cover; and (1e) railroad expansion (<a href="#water-13-00362-t003" class="html-table">Table 3</a>).</p>
Full article ">Figure A2
<p>Comparison of the difference in width of the 50% UI between the WP (red) and the NP (blue) models for each of the individual chronohorizon models over the interval from 1500 CE through the present. The red and blue lines are plotted transparently so that lighter areas represent widths that are predicted less frequently by Bchron, while darker areas represent widths that are predicted more frequently.</p>
Full article ">
14 pages, 9964 KiB  
Article
Effect of Shallow-Buried High-Intensity Mining on Soil Water Content in Ningtiaota Minefield
by Fan Cui, Yunfei Du, Jianyu Ni, Zhirong Zhao and Shiqi Peng
Water 2021, 13(3), 361; https://doi.org/10.3390/w13030361 - 30 Jan 2021
Cited by 7 | Viewed by 2747
Abstract
Shallow-buried high-intensity mining (SHM) activities commonly in China’s western mining area will lead to the decrease of groundwater level and soil water content (SWC), which will aggravate the further deterioration of the local fragile ecological environment. In this study, the applicability and limitations [...] Read more.
Shallow-buried high-intensity mining (SHM) activities commonly in China’s western mining area will lead to the decrease of groundwater level and soil water content (SWC), which will aggravate the further deterioration of the local fragile ecological environment. In this study, the applicability and limitations of six typical soil dielectric models were comprehensively evaluated based on ground penetrating radar (GPR) technology and shallow drilling methods. Moreover, experiments were performed to test the variation of SWC in Ningtiaota minefield affected by the SHM. The results show that the fitting effect of the four empirical models and two semi-empirical models on the clay is better than that of the medium sand. Among the six models, the Ledieu model has the best performance for medium sand, and the Topp model for clay. After SHM, the shallow SWC decreases as a whole. The decreasing range is 4.37–15.84%, showing a gradual downward trend compared with the one before mining. The shorter the lagging working face distance, the greater the drop of SWC will be. The longer the lagging working face distance, the smaller the drop of SWC will be showing a gradual and stable trend. Full article
(This article belongs to the Special Issue Recent Progress in Linking Soil Science and Hydrology)
Show Figures

Figure 1

Figure 1
<p>Geographical location map of Ningtiaota minefield.</p>
Full article ">Figure 2
<p>Schematic plan view of the study area. (<b>a</b>) The location of the study area. (<b>b</b>) Layout of survey lines and sampling points in the study area.</p>
Full article ">Figure 3
<p>Real shots of the sampling tools and sampling process. (<b>a</b>) The staff are conducting radar detection. (<b>b</b>) The cutting ring and aluminum box used for sampling. (<b>c</b>) Luoyang shovel.</p>
Full article ">Figure 4
<p>Comparison of calculated soil water content (SWC) and the measured SWC. The calculated SWC value represents the water content value obtained using the typical empirical models. The measured SWC value represents the water content value obtained using the gravimetric method. (<b>a</b>) Comparison of medium sand SWC calculated by dielectric models with that measured by gravimetric method. (<b>b</b>) Comparison of clay SWC calculated by dielectric models with that measured by gravimetric method.</p>
Full article ">Figure 5
<p>The change of SWC obtained by two samplings at No. 8 and No. 9 measuring points located in the area not affected by mining. (<b>a</b>) Change of SWC obtained from two samplings at No. 8 measuring point. (<b>b</b>) Change of SWC obtained from two samplings at No. 9 measuring point.</p>
Full article ">Figure 6
<p>Overall average water content of the soil obtained by sampling at different times. The overall average water content is the average of all deep SWC at each sample.</p>
Full article ">Figure 7
<p>Regression curve of the increase rate of the overall average water content after mining.</p>
Full article ">
Previous Issue
Back to TopTop