Research Article

Journal of Agricultural, Life and Environmental Sciences. 30 September 2023. 247-258
https://doi.org/10.22698/jales.20230020

ABSTRACT


MAIN

  • Introduction

  • Materials and Methods

  •   Sampling methods for solid-liquid separation (SLS)

  •   Solid-liquid separation techniques

  • Results and Discussion

  •   Changes in pH, EC, and NaCl content

  •   Changes in TS and SS contents

  •   Changes in nutrient content (TN, TP, and K), BOD5, and CODMn

  •   Changes in Zn and Cu

  • Conclusions

Introduction

Livestock manure is a valuable nutrient source for both plants and crops. However, livestock manure only contributes positively and replaces mineral and chemical fertilizers when used properly, with minimal loss of nutrients such as nitrogen (N), phosphorus (P), and potassium (K) (Bouwman and Booij, 1998; Le, 1998). The P and K contents of livestock manure are similar to those of commercial fertilizers, but the N content is much lower than that in commercial fertilizers (Hjorth et al., 2010). Excessive application of livestock manure as a fertilizer and untreated and/or poorly treated manure causes nutrient leaching and runoff, ultimately polluting the surface and groundwater and salinizing semi-arid regions, resulting in toxic concentrations of heavy metals and decreased soil aeration (Bernal et al., 1992; 1993; Burton and Turner, 2003; Steinfeld et al., 2006). Before utilizing manure as a fertilizer, it should be properly treated to ensure environmental safety with high fertilizer values. However, recovering energy and nutrients from liquid manure is difficult because of the lower concentrations of organic matter and nutrients (Møller et al., 2006; Teira-Esmatges and Flotats, 2003). Therefore, liquid manure separation is a key process in nutrient recovery strategies (Møller et al., 2000). Pig manure is a combination of pig urine, feces, and water spillage, as well as undigested food, antimicrobial drug residues, and pathogenic microorganisms (Vanotti et al., 2018). It is commonly characterized by a high content of suspended solids, organic matter, phosphorus, and nitrogen (Steinmetz et al., 2009), which results in high density and viscosity. Unlike cow and chicken manure, pig manure is more than 90% liquid, therefore, it has limited options for treatment by composting.

Solid-liquid separation (SLS) is a part of the organic and inorganic solid removal processes from manure slurry and most commonly separates manure into two streams, known as the liquid and solid fractions. The SLS process accelerates manure treatment and reduces environmental impacts (Aguirre-Villegas et al., 2019). According to Hjorth et al. (2010), the efficiency of an SLS system depends on (1) the chemical and physical properties of the slurry, (2) the desired end products, and (3) potential separation techniques, including pre-and post-treatments and combinations of different techniques. Typically, the separation efficiencies of mechanical SLS processes range between 34% and 68% (Chastain et al., 2001; Riaño and García-González, 2014). Owing to its operational and environmental benefits, the SLS system is often accompanied by multistep advanced manure treatment processes to improve the subsequent treatment steps and achieve environmental standards and nutrient recovery targets for livestock manure (Cantrell et al., 2008; Vanotti et al., 2018). For pig manure, SLS is a pre-treatment option that helps separate N-rich liquids from P-rich solids and allows the separated liquid to be used as a source of N for crops without oversupplying P (Kumaragamage et al., 2013). Consequently, SLS in the manure pretreatment process creates high processing efficiency by mobilizing biological processes due to particulate solids. A high concentration of pig manure in the slurry can reduce the processing load when solids are effectively removed (separated) by SLS. SLS processes are mainly mechanical pretreatment processes; however, not all are designed to perform in the same fashion. The most common mechanical SLS systems are screen separators (inclined screens, vibrating screens, and rotating screens), centrifuges (vertical and horizontal centrifuges), and presses (roller press, belt press, and screw press).

Because landfilling and ocean dumping of livestock manure and food waste have been prohibited in South Korea since 2005 and 2012, respectively (KMOE, 2008), several manure treatment technologies have been adopted at the farm and public levels, and often consist of several coupled treatment processes (SLS, composting, aeration, anaerobic digestion, liquid fertilization, and purification discharge). In addition, proper SLS processes at the farm level can remove a substantial amount of organic solids from fresh liquid and nutrients to reach liquid manure, which leads to ease of handling and transport of separated manure and reduces the odor in liquid manure solids. To increase the utilization of liquid manure as a biofertilizer, it is important to extract highly concentrated nutrients from the slurry and reduce odorous substances (Bernet and Béline, 2009).

The aim of this study was to investigate the performance of conventional SLS technologies that can produce liquid manure and liquid manure influent suitable for generating nutrient-rich and environmentally safe liquid manure fertilizers in Korea. To do so, we evaluated the separation efficiency of various SLS processes from different farms based on essential mature properties, such as biological oxygen demand (BOD), chemical oxygen demand (COD), nutrients (N, P, and K), and heavy metals (Cu and Zn).

Materials and Methods

Sampling methods for solid-liquid separation (SLS)

Sampling of the influent, effluent, and solid materials of the SLS was conducted after pre-operation of each device for 5-30 min, in accordance with the characteristics of the respective equipment. The sampling method adhered to specific regulations and guidelines regarding turbidity sampling criteria and testing methods for liquid fractions. In the case of liquid samples, such as the influent and effluent, a T-valve was installed at the inlet and outlet points to facilitate sample collection upon request (note that in pig farms where the installation of a T-valve was physically impractical, sampling was conducted directly from the inlet and outlet pipes). Influent and effluent samples were collected at the midpoint of predetermined time intervals. For the collection of solid samples, the sampler designated an arbitrary time frame (ranging from 1 to 30 min) and employed an appropriate container to collect the entire discharge from the solid outlet of the SLS. The weight of the collected sample was measured on-site, followed by the extraction of a portion of the solid sample from the collection container.

Solid-liquid separation techniques

Samples were collected from 13 pig farms that used seven different kinds of SLS processes. Table 1 shows the sampling sites, pig populations (heads), and technologies used while this study was being conducted.

Table 1.

List of the sampling sites and the solid-liquid separation (SLS) techniques used by them

Sampling site Number of Pigs (× 10x) Solid-liquid separation (SLS) Abbreviations
Pig farm A (Nonsan) 2.0 × 103 Drum screen (+Screw Press) D/S
Pig farm B (Yeoju) 2.2 × 103
Pig farm C (Gongju) 1.0 × 103 Inclined screen (+Screw Press) I/S
Pig farm D (Jincheon) 6.0 × 103
Pig farm E (Yeongcheon) 1.0 × 104
Pig farm F (Icheon) 1.6 × 103 Vibration screen (+Screw Press) V/S
Pig farm G (Gumi) 3.0 × 103 Screw Press S/P
Pig farm H (Boeun) 1.0 × 103
Pig farm I (Hapcheon) 2.0 × 103 Centrifuge Cf
Pig farm J (Yeongju) 3.8 × 103
Pig farm I (Hapcheon) 2.0 × 103 Centrifuge (+coagulation agent) Cf (+Cog)
Pig farm J (Yeongju) 3.8 × 103
Pig farm K (Changwon) 4.2 × 103 Belt Press (+coagulation agent) B/P (+Cog)

The average livestock population was 3,233 heads in the surveyed farms and finishing pig slurry was used in this study. Six of the 12 farms in this study paired screw pressing with other SLS processes, and three farms used coagulation agents. Samples were collected 5-30 min after pre-operation based on the characteristics of each solid-liquid separator from individual pig farms. The separated solids were sampled from the solid containers after 30 min of solid-liquid separator operation, and the collected solids were mixed uniformly and weighed on-site. The influent and separated liquids were collected by installing T-shaped valves at the inlet and outlet. On farms without valves, influents and treated liquids were collected from the inlet and discharge pipes. The influents and separated liquids were collected when the treated solids were past their half-time.

The potential of hydrogen (pH), electrical conductivity (EC), total nitrogen (TN), total phosphate (TP), potassium (K), total solids (TS), suspended solids (SS), salt (NaCl), and heavy metals were analyzed for the influents and separated liquids and solids. The pH and EC were immediately measured in the field using a multi-item measuring instrument YSI meter (Multilab IDS 4010-2, Xylem Inc., USA). The salt concentration was calculated by quantifying it with ICP (Spectro Blue, SPECTRO Analytical Instruments, Germany) and converting it into NaCl. Total nitrogen (TN), Total phosphorus (TP), potassium (K), Chemical oxygen demand (COD), and Biochemical Oxygen Demand (BOD) were analyzed after storing and transferred to the laboratory by following the standard method (APHA, 2005). In addition, CODMn, and BOD5 were measured by sulfuric acid, manganese, and distillation methods in compliance with the 「Fertilizer Quality Inspection Method and Sampling Standards」. The heavy metal content (Cu and Zn) were acid-pyrolyzed with microwaves (QWave1000, Questron Technologies, USA) and measured with ICP (Spectro Blue, SPECTRO Analytical Instruments, Germany) based on the US EPA method 200.7 and 200.8 (US EPA, 1994).

All sampling processes were repeated thrice (n = 3), the collected physical and chemical data were analyzed using Microsoft Excel, and the reduction efficiency rates were calculated according to Equation 1.

(1)
η=1-BA×100

Where, η: removal rate (%), A: Concentration before treatment, B: Concentration after treatment.

Results and Discussion

Tables 2 and 3 and Figs. 1, 2, 3 summarize the changes in the physical, chemical, and nutrient parameters caused by the different SLS processes.

Changes in pH, EC, and NaCl content

Different screen mesh sizes in different SLS methods create differences between the operational and removal efficiencies of SLS systems and manure characteristics (Kunz et al., 2008). pH and EC are two important characteristics of manure, especially when it is used as a liquid or compost fertilizer. pH, EC, salinity, and NaCl are indicators of the applicability of liquid manure fertilizers for plant growth and crop production (Zhao et al., 2009). In addition, plants obtain most nutrients from dissolved ions; thus, high salinity or high EC prevents efficient nutrient absorption by the plants (Abdulkareem et al., 2018).

The changes of pH and EC by SLS processes show similarities with the finding of Jørgensen and Jensen (2009), where separated liquids from the influents showed stable pH changes but variable EC changes. Our values show that the pH units remained at 6.61-8.63, which were near neutral, for 44 samples, while EC varied from 2.57 to 4.47 mS/cm. They also showed that centrifugation (+coagulation agent) resulted in the greatest reduction in EC. The near-neutral pH (6.7-7.2) and widely varied EC (4.9-17.0 mS/cm) were also reflected in studies by Kumaragamage et al. (2016) and Vanotti et al. (2018). However, the samples that used coagulation agents showed a slight increase in pH because of the chemical composition of the coagulant agents, but remained near neutral (Aguirre-Villegas et al., 2019; Jørgensen and Jensen, 2009; Vanotti et al., 2018). In this study, the pH ranges of the influents and separated liquids did not change significantly with any SLS process (Table 2). The pH changed from 6.90 ± 0.22 to 6.65 ± 0.27, 7.08 ± 0.50 to 7.23 ± 0.43, 7.20 ± 0.54 to 7.23 ± 0.75, 7.00 ± 0.94 to 6.88 ± 1.02, 7.28 ± 0.45 to 7.25 ± 0.26, 7.40 ± 0.41 to 7.53 ± 0.68, and 7.15 ± 0.63 to 7.20 ± 0.65 units for the V/S, D/S, I/S, screw press (S/P), centrifuge (Cf), Cf (+Cog), and belt press (B/P) (+Cog) processes, respectively. The (EC) reduction by Cf (+Cog) of 40.5% was the highest when the influent EC was 29.9 ± 10.2 mS/cm and the separated liquid had 17.8 ± 6.4 mS/cm EC. For the V/S, the influents had the highest EC value, 50.1 ± 7.4 mS/cm, but it was reduced by 15.0% to 42.6 ± 6.2 mS/cm after the treatment (Table 3). The lowest EC removal was observed for the Cf, where EC reduction was only 1.5%, a reduction from 28.1 ± 6.5 mS/cm to 27.7 ± 5.2 mS/cm. On the contrary, B/P (+Cog) with a coagulant agent did not show much EC reduction (2.3%). The NaCl reduction by Cf (+Cog) and B/P (+Cog) with a coagulation agent showed the highest removal efficiencies of 74.6% and 72.9%, respectively (Tables 2 and 3). Among the three screening separator processes, when V/S added up to 2.3% NaCl, I/S reduced 32.0%, and D/S reduced only 0.5%.

Table 2.

Changes in pH, electrical conductivity (EC), sodium chloride and moisture content (mean value) after treatment with different solid-liquid separation (SLS) processes (n = 3)

Items Units Stages V/S D/S I/S S/P Cf Cf (+Cog) B/P (+Cog)
pH Influents 6.90 ± 0.221) 7.08 ± 0.50 7.20 ± 0.54 7.00 ± 0.94 7.28 ± 0.45 7.40 ± 0.41 7.15 ± 0.63
Separated
liquid
6.65 ± 0.27 7.23 ± 0.43 7.23 ± 0.75 6.88 ± 1.02 7.25 ± 0.26 7.53 ± 0.68 7.20 ± 0.65
EC (mS/cm) Influents 50.10 ± 7.35 34.88 ± 14.12 22.77 ± 31.94 44.63 ± 7.12 28.08 ± 6.52 29.85 ± 10.17 32.65 ± 2.09
Separated
liquid
42.60 ± 6.21 33.70 ± 13.51 21.13 ± 29.25 41.05 ± 6.46 27.65 ± 5.19 17.75 ± 6.44 31.90 ± 1.69
NaCl (%) Influents 1.38 ± 1.46 0.68 ± 1.71 0.63 ± 3.21 2.43 ± 3.00 0.72 ± 0.76 0.75 ± 0.81 0.80 ± 0.84
Separated
liquid
1.42 ± 4.50 0.67 ± 1.77 0.43 ± 3.06 2.32 ± 2.87 0.69 ± 0.73 0.19 ± 0.09 0.22 ± 0.19
MC2) Influents - - - - - - -
Separated
solid
73.20 ± 4.53 68.60 ± 4.54 74.70 ± 3.81 65.70 ± 1.89 47.40 ± 29.45 74.00 ± 3.91 76.40 ± 0.46

1)Values are mean ± SD (n = 3)

2)MC are moisture content

Table 3.

Reduction and addition rate (%) of the physiochemical properties after operating different solid-liquid separation (SLS) processes (n = 3)

Properties V/S D/S I/S S/P Cf Cf (+Cog) B/P (+Cog)
pH 3.62 (-)2.12 (-)0.42 1.71 0.41 (-)1.76 (-)0.70
EC 14.97 3.38 7.20 8.02 1.53 40.54 2.30
NaCl (-)2.901) 1.47 31.75 4.53 4.17 74.67 72.50
TS 23.07 12.84 19.88 14.42 19.09 67.95 78.76
SS 23.99 13.78 13.91 8.07 32.12 65.42 96.89
TN 13.13 6.21 10.39 2.93 4.67 36.42 41.02
TP 9.42 8.02 27.74 11.14 29.69 94.14 91.45
K (-)2.38 (-)0.09 3.50 0.39 2.57 25.55 59.40
BOD5 14.65 7.76 13.05 3.85 4.71 53.89 66.02
CODMn 13.92 5.25 10.80 12.86 27.81 75.58 77.53
Zn 5.25 7.82 16.17 (-)4.57 12.35 ND2) 99.08
Cu 0.45 13.85 33.73 (-)1.06 9.05 98.75 98.12

1)(-) are addition rate

2)ND are not detected

Changes in TS and SS contents

One of the most important parameters of swine manure is the solid content, as it has a major impact on the performance of solid-liquid separation processes, and the solid content indicates the strength of the separated liquid (González-Fernández et al., 2008; Riaño and García-González, 2014). Fig. 1 shows the changes in TS and SS with the different SLS processes. The B/P (+Cog) and the Cf (+Cog) had 78.76% and 67.94% TS removal efficiency, respectively. Except these two-coagulation agent-supported SLS processes, the rest of the SLS processes showed 12.8-23.0% TS removal efficiency (Table 3). The coagulant supported SLS processes showed the highest SS reductions: 96.9% and 67.94% for B/P (+Cog) and Cf (+Cog), respectively. The Cf process had an SS removal efficiency of 32.2%. The rest of the SLS processes showed 8.1-24.1% TS removal efficiencies. Meanwhile, the moisture in the separated solids were 73.2%, 68.6%, 74.7%, 65.7%, 74.0%, and 76.4% for the V/S, D/S, I/S, S/P, Cf (+Cog), and B/P (+Cog) processes, respectively. The results also indicated that the process contained the lowest moisture content at 47.41% (Table 3).

https://static.apub.kr/journalsite/sites/ales/2023-035-03/N0250350306/images/ales_35_03_06_F1.jpg
Fig. 1.

Changes in solid contents (A) total solids (TS) and (b) suspended solids (SS) after treatment with different solid-liquid separation (SLS) processes.

Changes in nutrient content (TN, TP, and K), BOD5, and CODMn

By comparing the S/P with a Cf, several authors have found that the centrifuge achieves higher performance (Gooch et al., 2005; Møller et al., 2006; 2000). According to Aguirre-Villegas et al. (2019), Cf processes are more effective for the removal of TS, SS, TN, TP, K, BOD5, and CODMn than S/P processes. This finding was also reflected in this study (Table 3). Fig. 2 shows the changes in nutrient content (TN, TP, and K), BOD5, and CODMn caused by the different SLS processes. When comparing the Cf process with the V/S and D/S processes, the V/S process showed better removal of TS, TN, and BOD5. The Cf (+Cog) process exhibited higher EC, NaCl, TS, and TP removal efficiencies than the B/P process. In contrast, the B/P (+Cog) process had a comparatively better performance for TN, K, BOD5, and CODMn removal than the Cf (+Cog) process. The relatively low removal efficiencies of TN, TP, and K in liquids separated by mechanical processes without coagulation agents could be due to their more suitable or dissolved forms (Aguirre-Villegas et al., 2019; Bernet and Béline, 2009; Riaño and García-González, 2014; Saeys et al., 2005). The higher TP concentrations in the separated liquids and the removal efficiency for B/P (+Cog) were similar to those reported by Møller et al. (2002). However, the higher removal efficiencies of TN, TP, and TK by Cf (+Cog) and B/P (+Cog) were due to the chemical treatment coupled with mechanical (centrifuge and belt press) treatment, which screens out smaller-sized particles (Jørgensen and Jensen, 2009; Vanotti et al., 2002). The B/P (+Cog) showed the highest TN reduction of 41.0%, where the influents contained 7,857 ± 1,029 mg/L and the separated liquid contained 4,631 ± 342 mg/L of TN. The Cf (+Cog) had the second highest TN removal of 36.4%, where the TN decreased from 5,197 ± 1,058 to 3,304 ± 361 mg/L. However, V/S, D/S, I/S, S/P, and Cf showed 2.9-13.1% TN removal efficiency (Table 3). The TP removal was similar to that of TN. The Cf (+Cog) and B/P (+Cog) processes showed 94.2% and 91.5% TP removal efficiency, respectively, in separated liquids. However, V/S, D/S, I/S, S/P, and Cf showed 8.0-29.8% TN removal efficiencies. The B/P (+Cog) and Cf (+Cog) showed 59.4% and 25.6% K removal efficiency, respectively. The I/S, S/P, and Cf had only 0.4-3.5% removal efficiency for K. Moreover, in the case of V/S and D/S, the concentration of K somewhat increased in separated liquids. The B/P (+Cog) and Cf (+Cog) showed 59.4% and 25.6% K removal efficiency, respectively. The I/S, S/P, and Cf had only 0.4-3.5% removal efficiency for K. Moreover, in the case of V/S and D/S, the concentration of K somewhat increased in separated liquids. The concentrations of CODMn and BOD5 indicate the presence of oxygen-demanding substances in wastewater and are often used as indicators of pollution. In this study, the chemical coagulant agent-supported centrifugal and belt press SLS removed the highest amounts of BOD5 and CODMn. The B/P (+Cog) reduced 66.0% of BOD5, and the Cf (+Cog) reduced 53.9% of it; and the concentration of BOD5 in influents was 29,580 ± 1,078 mg/L and 22,825 ± 10,353 mg/L, and after treatment in separated liquid, it reduced to 10,050 ± 857 mg/L and 10,525 ± 4,948 mg/L, respectively. The removal of CODMn was similar to that of BOD5.

https://static.apub.kr/journalsite/sites/ales/2023-035-03/N0250350306/images/ales_35_03_06_F2.jpg
Fig. 2.

Changes in (A) total nitrogen (TN), (B) total phosphate (TP), (C) K, and (D) five-day biological oxygen demand (BOD5), and chemical oxygen demand (CODMn) after treatment with different solid-liquid separation (SLS) processes.

The Cf (+Cog) and B/P (+Cog) processes showed 75.6% and 77.5% of CODMn removal efficiency, respectively, in separated liquids. However, other SLS processes showed low removal efficiency for BOD5 (4.7-14.6%) and CODMn (5.3-27.8%) (Table 3). Approximately 40% of BOD5 was found in the solid fraction of manure; therefore, after performing SLS, about 60% of the BOD5 was supposed to remain in the separated liquid (Zhu et al., 2001) Therefore, the TS and BOD5 concentrations in separated liquids remained in the same sequential order of V/S, S/P, D/S, Cf, and I/S. For the coagulation agent-assisted SLS processes, the TS and BOD5 removal was 67.9% and 53.9% for Cf (+Cog) and 78.8% and 66.0% for B/P (+Cog), respectivey (Table 3). Similar properties were observed for changes in CODMn. Each sample that contained higher TS concentrations in both the influent and separated liquids also showed higher CODMn concentrations as (Chastain and Vanotti, 2003).

Changes in Zn and Cu

Separating heavy metals, such as Zn and Cu, from liquid manure before land application reduces the risk of soil contamination (Bolan et al., 2014; Riaño and García-González, 2014). Among all the analyzed heavy metals, Zn and Cu were found at the highest concentrations in the influents. The probable reason for this is that pigs receive Zn and Cu from their feeding operations (Zhang et al., 2012). Fig. 3 shows the changes in the nutrient contents of Zn and Cu caused by the different SLS processes. The coagulant assist centrifuge (Cf (+Cog)) and belt press (B/P (+Cog)) were very effective at reducing the heavy metals such as Zn (100% and 98.6%) and Cu (99.1% and 98.1%). These findings are similar to those of Vanotti et al. (2018), who found that a PAM-based mechanical pressing SLS system could remove 88% of Zn and Cu. However, the other SLS processes exhibited low Cu and Zn removal efficiencies. The V/S, D/S, I/S, and Cf showed 5.2-12.4% Zn removal efficiency and 0.4-33.7% Cu removal efficiency (Table 3), respectively. Moreover, for the I/P process, the concentrations of Zn and Cu slightly increased in the separated liquids.

https://static.apub.kr/journalsite/sites/ales/2023-035-03/N0250350306/images/ales_35_03_06_F3.jpg
Fig. 3.

Changes in (A) Zn, and (B) Cu after treatment with different solid-liquid separation (SLS) processes.

Conclusions

In this study, we assessed the separation and/or reduction efficiencies of various SLS technologies used on pig farms. The centrifugal and belt press processes that used chemical coagulation showed much greater removal of nutrients, solids, and metals such as Zn and Cu. Among all the SLS processes studied, the Cf (+Cog) process showed a 40.5% EC reduction, the highest among all SLS processes. The NaCl was reduced in the Cf (+Cog) and B/P (+Cog) by 74.6% and 72.9%, respectively. The B/P (+Cog) process exhibited the highest TS and SS reductions of 78.8% and 96.9%, respectively. The highest TN and TP removals were 41.0% and 94.2% for B/P (+Cog) and Cf (+Cog), respectively. The B/P (+Cog) removed 59.4% and 66.0% of BOD5 and CODMn, respectively. The Zn and Cu were reduced by 100% and 98.6% by Cf (+Cog), respectively. However, V/S, D/S, I/S, S/P, and Cf showed lower removal efficiencies for nutrients, solids, Zn, and Cu than the centrifugal and belt press processes that used chemical coagulation. In this study, we found that chemical coagulants made a notable difference in the SLS performance for the removal of, or changes to, different physicochemical parameters of pig manure. Although SLS is an effective pretreatment process for liquid manure treatment, and using chemical coagulants helps remove excess fine solids, nutrients, and heavy metals, further studies are needed to determine how coagulation agents react with other SLS and liquid manure treatment processes.

Acknowledgements

This work was supported by the Korea Institute of Planning and Evaluation for Technology in Food, Agriculture, and Forestry (IPET) and the Korea Smart Farm R&D Foundation (KosFarm) through the Smart Farm Innovation Technology Development Program, funded by the Ministry of Agriculture, Food, and Rural Affairs (MAFRA), Ministry of Science and ICT (MSIT), Rural Development Administration (RDA, 2022) (421046-03), and the Sangji University Graduate School.

References

1
Abdulkareem, M. A., Shaker, H. A., Muhsin, S. J. (2018) Effect of the manure levels, depth and application methods using subsoil laying machine on the soil salinity and soil pH. J Agric Res 7:1-17.
2
Aguirre-Villegas, H. A., Larson, R. A., Sharara, M. A. (2019) Anaerobic digestion, solid-liquid separation, and drying of dairy manure: Measuring constituents and modeling emission. Sci Total Environ 696:134059. 10.1016/j.scitotenv.2019.134059
3
APHA (2005) WFF. In Standard Methods for the Examination of Water and Wastewater, 21st ed.; Eaton, A. D., Clesceri, L. S., Rice, E. W., Greenberg, A. E., Eds.; American Water Work Association and Water Environment Federation: Denver, CO, USA.
4
Bernal, M. P., Roig, A., García, D. (1993) Nutrient balances in calcareous soils after application of different rates of pig slurry. Soil Use Manag 9:9-14. 10.1111/j.1475-2743.1993.tb00920.x
5
Bernal, M. P., Roig, A., Madrid, R., Navarro, A. F. (1992) Salinity risks on calcareous soils following pig slurry applications. Soil Use Manag 8:125-129. 10.1111/j.1475-2743.1992.tb00907.x
6
Bernet, N., Béline, F. (2009) Challenges and innovations on biological treatment of livestock effluents. Bioresour Technol 100:5431e5436. 10.1016/j.biortech.2009.02.00319269810
7
Bolan, N., Adriano, D., Mahimairaja, S. (2014) Distribution and bioavailability of trace elements in livestock and poultry manure by-products. Crit Rev Environ Sci Technol 34:291-338. 10.1080/10643380490434128
8
Bouwman, A. F., Booij, H. (1998) Global use and trade of foodstuffs and consequences for the nitrogen cycle. Nutr Cycl Agroecosys 52:261-267. 10.1023/A:1009763706114
9
Burton, C. H., Turner, C. (2003) Manure management: treatment strategies for sustainable agriculture, 2nd ed., Silsoe Research Institute, UK.
10
Cantrell, K. B., Ducey, T., Ro, K. S., Hunt, P. G. (2008) Livestock waste-to-bioenergy generation opportunities. Bioresour Technol 99:7941-7953. 10.1016/j.biortech.2008.02.06118485701
11
Chastain, J. P., Vanotti, M. B. (2003) Correlation equations to predict the solids and plant nutrient removal efficiencies for gravity settling of swine manure. In: R.T. Burnes (ed), Animal, Agricultural and Food Processing Wastes IX: Proceedings of the Ninth International Symposium, Research Triangle Park, NC, Oct. 12-15, ASAE, St. Joseph, MI, pp.487-495.
12
Chastain, J. P., Vanotti, M. B., Wingfield, M. M. (2001) Effectiveness of liquid-solid separation for treatment of flushed dairy manure: a case study. Appl Eng Agric 17:343-354. 10.13031/2013.6210
13
González-Fernández, C., Nieto-Diez, P. P., León-Cofreces, C., García-Encina, P. A. (2008) Solids and nutrients removals from the liquid fraction of swine slurry through screening and flocculation treatment and influence of these processes on anaerobic biodegradability. Bioresour Technol 99:6233-6239. 10.1016/j.biortech.2007.12.02218207388
14
Gooch, C. A., Inglis, S. F., Czymmek, K. (2005) Mechanical solid-liquid manure separation: performance evaluation on four New York state dairy farms - a preliminary report. Tampa, FL, July 17-20.
15
Hjorth, M., Christensen, K. V., Christensen, M. L., Sommer, S. G. (2010) Solid-liquid separation of animal slurry in theory and practice. A review. Agron Sustain Dev 30:153-180. 10.1051/agro/2009010
16
Jørgensen, K., Jensen, L. S. (2009) Chemical and biochemical variation in animal manure solids separated using different commercial separation technologies. Bioresour Technol, 100:3088-3096. 10.1016/j.biortech.2009.01.06519272772
17
Korean Ministry of Environment (KMOE) (2008) Economic analysis of waste-to-energy project. KMOE, Waste- to-Energy Division, Sejong, South Korea 18.
18
Kumaragamage, D., Akinremi, O. O., Greiger, L. (2013) Phosphorus fractions in solid and liquid separates of swine slurry separated using different technologies. J Environ Qual 42:1863-1871. 10.2134/jeq2013.03.007425602426
19
Kumaragamage, D., Akinremi, O. O., Racz, G. J. (2016) Comparison of nutrient and metal loadings with the application of swine manure slurries and their liquid separates to soils. J Environ Qual 45:1769-1775. 10.2134/jeq2016.04.013027695738
20
Kunz, A., Steinmetz, R. L. R., Ramme, M. M., Coldebella, A. (2008) Effect of storage time on swine manure solid separation efficiency by screening. Bioresour Technol 100:5485-5489. 10.1016/j.biortech.2008.10.03919128963
21
Le, H. C. (1998) Biodigester effluent versus manure, from pigs or cattle, as fertilizer for duckweed (Lemna spp.), Livest Res Rural Dev 10: 56-65.
22
Møller, H. B., Hansen, J. D., Sørensen, C. A. G. (2006) Nutrient recovery by solid-liquid separation and methane productivity of solids. American Society of Agricultural and Biological Engineers 50:193-200. 10.13031/2013.22400
23
Møller, H. B., Lund, I., Sommer, S. G. (2000) Solid-liquid separation of livestock slurry: Efficiency and cost. Bioresour Technol 74:223-229. 10.1016/S0960-8524(00)00016-X
24
Møller, H. B., Sommer, S. G., Ahring, B. K. (2002) Separation efficiency and particle size distribution in relation to manure type and storage conditions. Bioresour Technol 85:189-196. 10.1016/S0960-8524(02)00047-012227544
25
RDA (2022) Fertilizer Quality Inspection Method and Sampling Standards. Rural Development Administration, Wanju, Korea.
26
Riaño, B., García-González, M. C. (2014) On-farm treatment of swine manure based on solid-liquid separation and biological nitrification-denitrification of the liquid fraction. J Environ Manag 132:87-93. 10.1016/j.jenvman.2013.10.01424291581
27
Saeys, W., Mouazen, A. M., Ramon, H. (2005) Potential for onsite and online analysis of pig manure using visible and near infrared reflectance spectroscopy. Biosystems Eng 91:393-402. 10.1016/j.biosystemseng.2005.05.001
28
Steinfeld, H., Gerber, P., Wassenaar, T., Castel, V., Rosales, M., de-Haan, C. (2006) Livestock's long shadow: environmental issues and options, FAO, Rome. ISBN 978-92-5-105571-7.
29
Steinmetz, R. L. R., Kunz, A., Dressler, V. L., Flores, E. M. M., Martins, A. F. (2009) Study of metal distribution in raw and screened swine manure. Clean (Weinh) 37:239-244. 10.1002/clen.200800156
30
Teira-Esmatges, M. R., Flotats, X. (2003) A method for livestock waste management planning in NE Spain. Waste Manage 23:917-932. 10.1016/S0956-053X(03)00072-214614926
31
US EPA (1994) Method 200.7 and 200.8. In Determination of Trace Elements in Waters and Wastes by Inductively Coupled Plasma-Atomic Emission Spectrometry; US Environmental Protection Agency: Washington, DC, USA.
32
Vanotti, M. B., Rashash, D. M. C., Hunt, P. G. (2002) Liquid-solids separation of flushed swine manure with PAM: effect of wastewater strength. Trans. ASAE 45:1959-1969. 10.13031/2013.11422
33
Vanotti, M. B., Ro, K. S., Szogi, A. A., Loughrin, J. H., Millner, P. D. (2018) High-rate solid-liquid separation coupled with nitrogen and phosphorus treatment of swine manure: effect on water quality. Front Sust Food Syst 2:1-15. 10.3389/fsufs.2018.00049
34
Zhang, F., Li, Y., Yang, M., Li, W. (2012) Content of heavy metals in animal feeds and manures from farms of different scales in northeast China. Int. J. Environ. Res. Public Health, 9:2658-2668. 10.3390/ijerph908265823066389PMC3447579
35
Zhao, Y., Wang, P., Li, J., Chen, Y., Ying, X., Liu, S. (2009) The effect of two organic manures on soil properties and crop yields on a temperate calcareous soil under a wheat - maize cropping system. Eur J Agron 31:36-42. 10.1016/j.eja.2009.03.001
36
Zhu, J., Ndegwa, P. M., Luo, A. (2001) Effect of solid-liquid separation on BOD and VFAs in swine manure. Environ Technol 22:1237-1243. 10.1080/0959333220861820911766045
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