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Article

Design of an Enhanced SAT Using Zeolite for the Removal of Ammonia Nitrogen at a Bengbu Aquatic Farm in China

by
Ge Zhang
1,2,*,
Jinhao Zhu
2,
Ke Yang
2,
Yinhao Zhu
2 and
Zijie Sang
2
1
Engineering Research Center of Agricultural Microbiology Technology, Ministry of Education, Heilongjiang University, Harbin 150500, China
2
School of Hydraulic and Electric Power, Heilongjiang University, Harbin 150080, China
*
Author to whom correspondence should be addressed.
Sustainability 2022, 14(24), 16983; https://doi.org/10.3390/su142416983
Submission received: 2 October 2022 / Revised: 14 December 2022 / Accepted: 16 December 2022 / Published: 18 December 2022
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Abstract

:
As one of the artificial recharge technologies, the soil–aquifer treatment (SAT) system is used for the removal of nitrogen pollution from aquaculture wastewater. An adsorption-enhanced SAT system was designed to reduce the level of nitrogen pollution below the threshold stipulated by the standards. Adsorption kinetics experiments were used to measure the adsorption capacity of zeolite and activated carbon for ammonia nitrogen. Both adsorbents can be well described by the Lagergren pseudo-second-order model, and the adsorption rates of zeolite and activated carbon for ammonia nitrogen were 72.16% and 31.40%, respectively. Combining the experimental data and the actual situation, the medium-packing method was determined and the influence of wastewater characteristics and hydrodynamic conditions on the adsorption and retention capacity of the SAT system were considered. Finally, the feasibility of the adsorption-enhanced SAT site design scheme was verified by Hydrus-1D model simulation. The study found that the design scheme for the situation in the study area was feasible; however, the surrounding underground environment still had a risk of pollution during the operation of the site. Therefore, further research is needed for the nitrogen pollution to be completely removed within the scope of the SAT site.

1. Introduction

Aquaculture supports the high nutritional protein demand of the world’s population; however, aquaculture wastewater pollution has also become a global ecological problem that cannot be ignored [1]. Nitrogen pollution in aquaculture wastewater is the most prevalent, which primarily comes from undigested feed and fish residual feces. Ammonia nitrogen and nitrite nitrogen, even at low concentrations, are highly toxic, accelerating fish mortality and human disease risk [2,3]. As the largest aquaculture country in the world, China’s aquaculture volume is anticipated to reach 150 Mt by 2030. With the continuous expansion of the aquaculture range, a large amount of aquaculture wastewater will subsequently be produced. However, the arbitrary discharge of untreated aquaculture wastewater is bound to have a certain impact on the water and soil environment [4]. Therefore, research on the denitrification, purification, and reuse of aquaculture wastewater has become a focus of scholars [5].
At present, nitrogen in aquaculture wastewater can mainly be removed by the electrochemical method [6], the membrane treatment method [7], or constructed wetland [8]. The electrochemical treatment technology has the advantages of high treatment efficiency and little impact on the environment [9,10,11]. However, due to the high cost and small surface area of the electrode, it is less used in the actual treatment of large-scale aquaculture wastewater [12]. The membrane-treatment technology covers a small area and has a high retention capacity [13,14,15]. However, due to the high cost and easy contamination of the membrane, it is limited in application [16]. The constructed wetland technology has high treatment efficiency and low economic cost in treating nitrogen containing wastewater [17,18,19]. However, it requires a long treatment period and a considerable area to remove pollutants [20]. Therefore, it is particularly important to measure the advantages of each technology and find an economical and reasonable method for the denitrification of aquaculture wastewater with high treatment efficiency.
As a kind of artificial recharge technology, the soil–aquifer treatment (SAT) system can be evaluated as a good method to repair aquaculture wastewater pollution. It mainly uses the physical, chemical, and biological purification functions of soil to remove, transform, or utilize the pollution in wastewater, so as to achieve the purpose of water resource regeneration. Compared with the traditional wastewater treatment technology, it has the characteristics of low cost, high treatment efficiency, simple operation, etc. [21,22]. Studies have shown that the SAT system mainly relies on the adsorption of medium to intercept nitrogen in wastewater and decrease its concentration to the reference discharge standard. The removal efficiency of the SAT system for nitrogen in sewage is impacted by the hydraulic load, medium type, and other factors, and the average rejection rate is between 50 and 75% [23,24]. If a repair mechanism in the SAT system is enhanced, its removal effect on specific pollutants will be improved [25,26]. Previous studies have found that zeolite and activated carbon are often used to remove nitrogen pollution from wastewater [27,28,29]. Therefore, this paper explored the feasibility of using zeolite and activated carbon as an adsorbent to optimize the adsorption capacity of the SAT system for nitrogen pollution in aquaculture wastewater.
As porous materials, zeolite and activated carbon are characterized by strong adsorption capacities, large specific surface areas, and consistent chemical properties, which have been widely used in the transformation and treatment of water pollution [30,31]. The zeolite has a good performance in wastewater denitrification, whether it is applied alone or combined with other remediation technologies; for example, Wan et al. [32] used zeolite to reduce the concentration of ammonia nitrogen in fermentation broth from the initial 756.9 mg/L to 201.1 mg/L, and the recovery rate was up to 70.5%, and Liu et al. [33] combined zeolite with constructed wetland and found that the removal rate of ammonia nitrogen was as high as 95.68%. The activated carbon is mostly combined with microbial technology in wastewater denitrification, such as being prepared in an iron-containing biological activated carbon filter (Fe-BACF) [34] and constructed wetlands-microbial fuel cell [35].
The focus of this study was to design an enhanced SAT system to remove nitrogen pollution in aquaculture wastewater of the study area. The specific objectives of the study were to: (1) compare the adsorption efficiency of activated carbon and zeolite on ammonia nitrogen in water and choose the best as the enhanced adsorbent of the SAT system, (2) design an adsorption-enhanced SAT system site to meet the needs of the study area, and (3) verify the feasibility of the site design scheme by simulation using Hydrus-1D.

2. Materials and Methods

2.1. Description of the Study Area

The study area is located on Bengbu Aquaculture Farm, Anhui Province, China. The farm is dominated by soft-shelled turtle and crayfish farming; nitrogen pollution in the region mainly comes from a large number of untreated direct discharges of aquaculture wastewater. At the beginning of the study, indoor soft-shelled turtle aquaculture water (S-1), outdoor soft-shelled turtle aquaculture water (S-2), and crayfish aquaculture water (C-1) were collected. The analysis results are shown in Table 1. It can be seen that the nitrogen pollution in each water sample was detected to varying degrees; the concentration of ammonia nitrogen in S-1 was the most prominent. The main reason may be that, compared with outdoors, the breeding density of indoor fishponds is higher, and the aquaculture water had not been replaced for a long time, resulting in a large accumulation of high-protein feed and fecal excretion [36]. Therefore, this paper mainly took ammonia nitrogen as an example to design and study the adsorption-enhanced SAT system.

2.2. Screening of the Enhanced Adsorbent of SAT System

Due to the small study area, the stratigraphic structure and composition are relatively simple, and the aquifer medium is mainly composed of medium-coarse sand and gravel, so the medium sand was selected as the indoor SAT simulation column medium. The adsorption efficiency of activated carbon (Fuchen Chemical Reagent Co., Ltd., Tianjin, China) and zeolite (Fuchen Chemical Reagent Co., Ltd., Tianjin, China) for ammonia nitrogen were compared by the adsorption kinetics method and compared with simulated column medium. A measure of 0.1 mg zeolite was accurately weighed and added into 100 mL of 10 mg L−1 ammonia nitrogen solution in a 250 mL Erlenmeyer flask. The flasks were shaken at a constant speed of 180 rpm at room temperature (25 ± 1 °C) in a temperature-controlled shaking incubator (Shanghai Min Quan Instruments Co., Ltd., Shanghai, China) for predetermined time intervals of 5 min, 10 min, 30 min, 60 min, 90 min, 120 min, 150 min, and 180 min. For evaluating the ammonia nitrogen–activated carbon or ammonia nitrogen–medium sand system, the experiments were performed under similar conditions: 0.1 mg of activated carbon or 0.5 mg of medium sand instead of 0.1 mg zeolite.
The Lagergren pseudo-first-order and pseudo-second-order kinetic models were used to examine the adsorption mechanism and equilibrium time [37].
The pseudo-first-order model is given as:
l n ( q e − q t ) = l n q e − k 1 t ,
The pseudo-second-order model can be presented as:
t / q t = 1 / k 2 q e 2 + t / q e ,
where qe (mg g−1) and qt (mg g−1) are the ammonia nitrogen adsorption capacities at equilibrium and at time t (min), respectively. k1 is the pseudo-first-order rate constant (min−1); k2 is the pseudo-second-order rate constant (g (mg min)−1).

2.3. Laboratory Simulation of SAT System

The SAT system soil column setup is shown in Figure 1. In addition to the original soil column (SC), the same mass of zeolite was filled in the adsorption-optimized soil column outlet (ESC-1), inlet (ESC-2), and uniformly mixed with medium sand (ESC-3). Plexiglass columns, 5 cm in length with inner diameters of 1.2 cm, were packed to a density of 1.99 g cm−3. In order to prevent the outflow of fine particles, 200 stainless-steel meshes were laid at the top and bottom of the column, and a polytetrafluoroethylene gasket was fixed between the column top and body to prevent leakage.
All columns were operated under saturated conditions at 15 ± 1 °C (to simulate an underground environment). The saturated condition was achieved by continuously supplying water from the bottom to the top of the column through the peristaltic pump and keeping the liquid level higher than the upper surface of the column. The simulated ammonia nitrogen wastewater used in the experiment was prepared from NH4Cl (Sinopharm Chemical Reagent Co., Ltd., Shanghai, China) to study the effects of different optimization schemes, water environments, and hydrodynamic conditions on the removal efficiency of ammonia nitrogen in the SAT system. The water samples collected from the outlet were detected by ultraviolet spectrophotometry (Shanghai Jinghua Technology Instrument Co., Ltd., Shanghai, China) after pretreatment.

3. Results and Discussion

3.1. Comparison of Adsorption Efficiency of Adsorbents

The experiments were conducted for the adsorption capacity of medium sand, activated carbon, and zeolite on ammonia nitrogen in water. The data of the adsorption capacity with time were fitted using Lagergren pseudo-first-order and pseudo-second-order kinetic equations, and the results are shown in Figure 2. The medium sand, activated carbon, and zeolite can quickly reach adsorption equilibrium within 60 min. In the initial stage of the adsorption reaction, the adsorption rates of ammonia nitrogen were relatively high, which was mainly due to the high concentration of ammonia nitrogen and the large number of unoccupied adsorption sites on the adsorbent surface, so the adsorption reaction proceeded faster. Thereafter, as the ammonia nitrogen was continuously adsorbed, the concentration of the contaminated liquid decreased, and the adsorption sites on the adsorbent surface were gradually saturated, so the adsorption rate gradually decreased until the adsorption equilibrium. The fitting results of adsorption kinetics of three adsorbents for ammonia nitrogen are listed in Table 2. By comparing the correlation coefficient (R2), it can be seen that the pseudo-second-order equation has a high degree of fitting, and the equilibrium adsorption capacity qe,cal calculated by the pseudo-second-order equation is close to the measured maximum adsorption capacity qe,exp, indicating that the adsorption process of ammonia nitrogen by the three adsorbents conforms to the pseudo-second-order kinetic model, and the adsorption process is mainly physical and chemical adsorption.
Even if the qualities of activated carbon and zeolite were lower than that of medium sand, they also showed significantly better adsorption capacities than that of medium sand, and their removal rates of ammonia nitrogen were 31.40% and 72.16%, respectively. The adsorption effect of activated carbon was not satisfactory, probably because it is a non-polar adsorbent material and has poor adsorption capacity for polar pollution in water without optimized treatment. However, zeolite showed excellent adsorption efficiency, which is consistent with Huang’s research on the removal of ammonia nitrogen from water by zeolite adsorption [38]. Therefore, in this study, zeolite was selected as the adsorption enhancer for the SAT system to optimize the capacity for retention of ammonia nitrogen.

3.2. Analysis of the Removal Efficiency of SAT System for Ammonia Nitrogen

3.2.1. Analysis of the Removal Efficiency of Ammonia Nitrogen under Different Packing Methods

An ammonia nitrogen solution of 10 mg L−1 was continuously supplied to each simulated column from bottom to top at a flow rate of 1 mL min−1. Figure 3 shows the breakthrough curves of ammonia nitrogen under different packing methods. Compared with the original column breakthrough at 45 PV (pore volume), the breakthrough curve of the optimized column moves to the right in varying degrees, with breakthroughs at 55 PV, 60 PV, and 65 PV, respectively, indicating that the ammonia nitrogen retention capacity of the optimized column is better than that of the original column, and the optimization effect is ESC-3 > ESC-2 > ESC-1. However, since the actual scale of the SAT site is much larger than that of the laboratory simulated column, the adsorption of pollutants during the infiltration of wastewater into the site mostly occurs within 1 m from the surface. In order to avoid material waste, zeolite was chosen to be laid near the surface area after uniform mixing with the site medium.

3.2.2. Effect of Water Environment and Hydrodynamic Conditions on the Removal Efficiency of Ammonia Nitrogen

The adsorption capacity of the SAT system for the target contamination is not only related to the physicochemical properties of the filling medium but also influenced by the characteristics of the water source and the infiltration hydrodynamic conditions of the recharge effluent. Based on the background of aquaculture wastewater sources and the purpose of this study, it was decided to consider the impact on the SAT system in terms of both the pollution concentration and the infiltration rate. Considering that the above SAT site adsorption optimization scheme is closer to the packing method of ESC-2, SC and ESC-2 were selected for the infiltration simulation. The operating conditions of each simulated column are shown in Table 3.
The breakthrough curves of ammonia nitrogen at different infiltration rates are shown in Figure 4. Compared with the infiltration rate of 1 mL min−1, the breakthrough in both simulated columns was delayed at lower infiltration rates. This shows that the low speed was more conducive to the removal of ammonia nitrogen in the SAT system. This is mainly due to the fact that low-speed infiltration will increase the residence time of wastewater in the system so that ammonia nitrogen can be in full contact with the medium, which is more conducive to the occurrence of adsorption. ESC-2 retains ammonia nitrogen better than the original soil column in both cases, even at higher infiltration flow rates. Therefore, this method has good prospects for application in the design of SAT sites in the study area.
Figure 5 shows the breakthrough curves of ammonia nitrogen at different infiltration concentrations. The breakthroughs in SC and ESC-2 were advanced by 10 PV and 12.5 PV, respectively, at higher concentrations of infiltrating contamination. This indicates that the high contamination concentration accelerates the adsorption equilibrium in the SAT system medium, thus weakening the system’s ability to intercept pollution. This corroborates the need to optimize the adsorption performance of the SAT system.

3.3. Design and Simulation of SAT

3.3.1. Design of SAT Site

According to the preliminary survey, the number of farmed soft-shelled turtles was 25–30 per square meter, the fishpond water was changed every 7–10 days, and the daily sewage treatment volume in the study area was about 321 m3. Therefore, the aim of this study was to establish small-scale SAT systems in a limited area for rapid treatment of large quantities of wastewater from aquaculture. As shown in Figure 6, a seeping pool with an area of 9 m2 was designed for the middle of the SAT site; it had impermeable barriers, and an enhanced adsorption layer composed of zeolite and site medium was set at a depth of 0.5 m from the surface. Water samples can be collected from the pumping wells downstream of the groundwater in the SAT site area to study the treatment efficiency of the optimized SAT system for the target sewage.

3.3.2. Simulation of SAT Site

The target aquifer medium for this simulation was medium-coarse sand with a thickness of 6m, and there was an enhanced adsorption layer at 0.5 m. However, as the thickness of the enhanced adsorption layer was small and the zeolite was uniformly mixed with the site medium, the target area could be approximately generalized as an aquifer with uniform hydraulic characteristics. The aquifer in the simulation area was provided with an impermeable shield in the transverse direction. The hydraulic gradient of wastewater infiltration was set to use the laboratory simulation value. The seepage conformed to Darcy’s law [39], and it was assumed that the wastewater continuously infiltrated and the water head remained unchanged. Therefore, the whole wastewater recharge process could be generalized as a one-dimensional stable flow, the upper boundary of the simulation area was a constant head boundary, and the lower boundary was a free drainage boundary.
Soil–water movement parameters included the saturated permeability coefficient (Ks), saturated water content (θs), and residual water content (θr). Fitting parameters included α, N, etc. The solute transport parameters included partition coefficient Kd, soil density r, dispersion DL, etc. Soil–water movement and solute transport parameters were obtained by the inversion of the model parameters from the VG model [40] and laboratory soil column experimental data, which are shown in Table 4.
Observation points were set at the lower boundary of the soil columns. The ammonia nitrogen transport in the SAT soil columns was simulated using Hydrus-1D software. Figure 7 shows the fitting curves of the simulated results with the measured values. The simulated curves were basically consistent with the measured curves, and the fit coefficient R2 was greater than 0.99. This indicated that the model could effectively simulate the transport of ammonia nitrogen in the soil. Therefore, it could be used to predict the transport of ammonia nitrogen in SAT sites.
For the convenience of model simulation, it was assumed that the wastewater would continuously infiltrate for a certain period (90 days) at the SAT site. According to the measured wastewater concentration at the site, the ammonia nitrogen concentration in the infiltration wastewater was 66.41 mg/L. The simulation results are shown in Figure 8a. At the end of the operation period (90 days) of the SAT site, the concentration of ammonia nitrogen in the outflow from the lower boundary of the site did not reach the initial concentration of ammonia nitrogen. This showed that the site still had adsorption capacity for ammonia nitrogen at that time, which further indicates that the optimization scheme for the adsorption capacity of the SAT site is feasible according to the situation of the study area. However, when only considering the adsorption of ammonia nitrogen at the SAT site, it was found that ammonia nitrogen will flow out of the site at the initial stage of operation. In order to better observe the transport of ammonia nitrogen in the site, observation points N1, N2, and N3 were set at 300 cm, 450 cm, and the lower boundary of the simulated column, and the simulation was carried out from the beginning of site operation to 40 days. The simulation results are shown in Figure 8b.
Although the SAT site has the ability to absorb ammonia nitrogen throughout its operation period, ammonia nitrogen flows out of the lower boundary into the original soil environment from the 15th day of site operation, posing a threat to the underground environment near the site. In order to ensure that nitrogen pollution is intercepted and removed within the site, in addition to increasing the adsorption capacity of the site, it is also necessary to make use of microorganisms in the original soil or added oxidants to completely remove nitrogen pollution in the SAT site.

4. Conclusions

Compared with activated carbon, zeolite was more suitable as the enhanced adsorbent of the SAT system. The kinetics parameters of the two adsorbents can be well described by the Lagergren pseudo-second-order model, and the adsorption rates of zeolite and activated carbon for ammonia nitrogen were 72.16% and 31.40%, respectively. Considering the experimental data and the actual situation, it was decided to mix the zeolite with the site medium uniformly and then lay it in the near-surface area to optimize the adsorption efficiency of the SAT site. When the wastewater pollution concentration was high or the infiltration rate was fast, the adsorption and interception capacity of the SAT system was restricted.
An adsorption-enhanced SAT system with a 9 m2 seeping pool was designed to achieve the target of aquaculture wastewater regeneration in the study area. The simulation results using Hydrus-1D software verified that the optimization scheme for the adsorption capacity of the SAT site is feasible. However, in order to ensure that nitrogen pollution is intercepted and removed within the site, in addition to increasing the adsorption capacity of the site, it is also necessary to make use of microorganisms in the original soil or added oxidants to completely remove nitrogen pollution in the SAT site.

Author Contributions

Conceptualization, G.Z. and J.Z.; methodology, G.Z.; software, K.Y.; validation, J.Z. and Y.Z.; formal analysis, G.Z.; investigation, J.Z.; resources, G.Z.; data curation, J.Z.; writing—original draft preparation, J.Z.; writing—review and editing, G.Z.; visualization, K.Y. and Z.S.; supervision, G.Z.; project administration, G.Z.; funding acquisition, G.Z. All authors have read and agreed to the published version of the manuscript.

Funding

This research was supported by the Basic Scientific Research Fund of Heilongjiang Provincial Universities (2020-KYYWF-1043).

Informed Consent Statement

Not applicable.

Data Availability Statement

The data that support the findings of this study are available from the corresponding author, G.Z., upon reasonable request.

Acknowledgments

This work was supported by the School of Hydraulic and Electric Power, Heilongjiang University, and the Key Laboratory of Molecular Biology, College of Heilongjiang Province.

Conflicts of Interest

The authors declare no conflict of interest regarding the publication of this paper.

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Figure 1. Soil–aquifer treatment (SAT) soil column setup.
Figure 1. Soil–aquifer treatment (SAT) soil column setup.
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Figure 2. Effect of contact time on ammonia nitrogen adsorption by medium sand, activated carbon, and zeolite. (a) Lagergren pseudo-first-order model. (b) Lagergren pseudo-second-order model (concentration of ammonia nitrogen 10 mg L−1, and temperature 25 °C).
Figure 2. Effect of contact time on ammonia nitrogen adsorption by medium sand, activated carbon, and zeolite. (a) Lagergren pseudo-first-order model. (b) Lagergren pseudo-second-order model (concentration of ammonia nitrogen 10 mg L−1, and temperature 25 °C).
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Figure 3. Breakthrough curves of ammonia nitrogen in (a) column SC, (b) column ESC-1, (c) column ESC-2, and (d) column ESC-3.
Figure 3. Breakthrough curves of ammonia nitrogen in (a) column SC, (b) column ESC-1, (c) column ESC-2, and (d) column ESC-3.
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Figure 4. The breakthrough curves of ammonia nitrogen at different infiltration rates in (a) column SC and (b) column ESC-2.
Figure 4. The breakthrough curves of ammonia nitrogen at different infiltration rates in (a) column SC and (b) column ESC-2.
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Figure 5. The breakthrough curves of ammonia nitrogen at different infiltration concentrations in (a) column SC and (b) column ESC-2.
Figure 5. The breakthrough curves of ammonia nitrogen at different infiltration concentrations in (a) column SC and (b) column ESC-2.
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Figure 6. SAT site design diagram.
Figure 6. SAT site design diagram.
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Figure 7. Measured and simulated values of ammonia nitrogen concentration in (a) column SC, and (b) column ESC-2.
Figure 7. Measured and simulated values of ammonia nitrogen concentration in (a) column SC, and (b) column ESC-2.
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Figure 8. Transport simulation of ammonia nitrogen at (a) SAT site, and (b) different observation points.
Figure 8. Transport simulation of ammonia nitrogen at (a) SAT site, and (b) different observation points.
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Table
Table 1. Tri-nitrogen detection results of water samples in the study area.
Table 1. Tri-nitrogen detection results of water samples in the study area.
NitrogenS-1 (mg L−1)S-2 (mg L−1)C-1 (mg L−1)
Nitrate nitrogen0.064 L a0.160.064 L
Nitrite nitrogen0.540.064 L0.064 L
Ammonia nitrogen66.410.600.76
a The detection limit is 0.064 mg L−1, and the detection result is lower than the detection limit.
Table
Table 2. Kinetic model parameters for the ammonia nitrogen adsorption by medium sand, activated carbon, and zeolite.
Table 2. Kinetic model parameters for the ammonia nitrogen adsorption by medium sand, activated carbon, and zeolite.
Adsorbentqe,exp
(mg g−1)		Lagergren Pseudo-First-Order ModelLagergren Pseudo-Second-Order Model
qe,cal
(mg g−1)		k1
(min−1)		R2qe,cal
(mg g−1)		k2
(g (mg·min)−1)		R2
Medium sand0.6650.6580.29380.99340.6721.75760.9993
Activated carbon3.1403.0890.25120.99073.1750.22800.9991
Zeolite7.2167.0620.25230.98537.2770.08940.9998
Table
Table 3. Operating conditions of simulated columns.
Table 3. Operating conditions of simulated columns.
Column NameInfiltration Concentration (mg L−1)Infiltration Rate (mL min−1)
SC101
20
100.5
1
ESC-2101
20
100.5
1
Table
Table 4. The parameters of soil–water movement and solute transport.
Table 4. The parameters of soil–water movement and solute transport.
Column NameSCESC-2
Soil Depth (cm)0–50–11–5
R (g cm−3)1.991.991.99
θr (cm3 cm−3)0.0450.0450.045
θs (cm3 cm−3)0.430.430.43
n2.682.682.68
α0.1450.1450.145
Ks (cm min−1)0.4950.4950.495
Kd4.300428.1054.3004
DL (cm)0.0782210.0494380.078221
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Zhang, G.; Zhu, J.; Yang, K.; Zhu, Y.; Sang, Z. Design of an Enhanced SAT Using Zeolite for the Removal of Ammonia Nitrogen at a Bengbu Aquatic Farm in China. Sustainability 2022, 14, 16983. https://doi.org/10.3390/su142416983

AMA Style

Zhang G, Zhu J, Yang K, Zhu Y, Sang Z. Design of an Enhanced SAT Using Zeolite for the Removal of Ammonia Nitrogen at a Bengbu Aquatic Farm in China. Sustainability. 2022; 14(24):16983. https://doi.org/10.3390/su142416983

Chicago/Turabian Style

Zhang, Ge, Jinhao Zhu, Ke Yang, Yinhao Zhu, and Zijie Sang. 2022. "Design of an Enhanced SAT Using Zeolite for the Removal of Ammonia Nitrogen at a Bengbu Aquatic Farm in China" Sustainability 14, no. 24: 16983. https://doi.org/10.3390/su142416983

APA Style

Zhang, G., Zhu, J., Yang, K., Zhu, Y., & Sang, Z. (2022). Design of an Enhanced SAT Using Zeolite for the Removal of Ammonia Nitrogen at a Bengbu Aquatic Farm in China. Sustainability, 14(24), 16983. https://doi.org/10.3390/su142416983

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