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Enhanced Nitrogen Removal and Distribution Distributions of Microbial Genes Associated with Nitrogen Cycling in A Vertical-flow Biofilter Treating Domestic Wastewater

Honglei Wang 1, Duntao Shu 2, Na Deng 1, Gehong Wei 2* and Tongshun Wang3

1State Key Laboratory of Soil Erosion and Dry Land Farming on the Loess Plateau, Institute of Soil and Water Conservation, Northwest A & F University, Yangling 712100, Shaanxi, China

2State Key Laboratory of Crop Stress Biology in Arid Areas, College of Life Sciences, Northwest A&F University, Yangling, Shaanxi 712100, China

3Jiangsu Hydraulic Research Institute, Nanjing 210029, Jiangsu, China

*Corresponding Author:
Honglei Wang
State Key Laboratory of Crop Stress Biology in Arid Areas, College of Life Sciences, Northwest A&F University, Yangling, Shaanxi 712100, China
Fax:
+86 29 87091175, +86 29 87091175
E-mail: wanghonglei@nwsuaf.edu.cn

Received date: 24/08/2018; Accepted date: 12/09/2018; Published date: 19/09/2018

Citation: Mbamalu ON, Antunes E, Silosini N, Samsodien H, Syce J (2016) HPLC Determination of Selected Flavonoid Glycosides and their Corresponding Aglycones in Sutherlandia frutescens Materials. Med Aromat Plants 5:246. doi: 10.4172/2167-0412.1000246

Copyright: © 2016 Mbamalu ON, et al. This is an open-access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited.

Visit for more related articles at Research & Reviews: Journal of Microbiology and Biotechnology

Abstract

Vertical-flow biofilters have been investigated as a sustainable technology for nitrogen (N) and chemical oxygen demand (COD) removal from domestic wastewater. However, the distribution contributions of microbial genes responsible for removing N remain largely unexplored, particularly along the depth gradient in vertical-flow biofilters. Here, a three-stage vertical-flow bio-filter (three stages: P1, P2, and P3) achieved large removal efficiencies for total nitrogen (TN; 87.00% and 33.69 g/m2·d), NH4 +-N (95.90% and 24.17 g/m2·d) and COD (92.00% and 558.15 g/ m2·d). The removal contributions of NH4+-N and TN in P1, P2, and P3 can be ranked as follows: P1 (45.9% and 38.4%, respectively) >P2 (39.6% and 28.2%, respectively) >P3 (10.6% and 20.5% respectively). The results revealed that amoA/bacteria, (nirK + nirS + nosZ)/bacteria, amoA/anammox and anammox/bacteria were the predominant gene groups responsible for NH4+-N and TN removal in P1, P2 and P3 and the contributions of these gene groups along the depth gradient of the bio-filter. Specifically, the NO3--N removal rate in P3 was notably enhanced and collectively governed by the (napA + narG) and nxrA gene groups. Integrated analyses confirmed that the coupling of nitrification and denitrification governed the enhanced removal of NH4+-N and TN in P1. Combining anammox and nitrification contributed to the removal of NH4+-N and TN in P2. Enhanced anammox and denitrification accounted for the robust TN reduction in P3. This study indicated that biofilters have great potential applicability for treating domestic wastewater without a sequential chain of treatments and extra aerations.

Keywords

Domestic wastewater; Vertical-flow biofilter; Functional gene; Distribution contribution; Nitrogen removal.

Abbreviations

PCR: Polymerase chain reaction; APHA: American public health association; TP: Total phosphorous; TN: Total nitrogen; COD: Chemical oxygen demand

Introduction

Biofilter systems have been designed and deeply investigated as a widely applied technology for wastewater treatment [1-3]. Given their technological, economic and ecological superiority, biofilter systems are extensively constructed and adopted for N removal from domestic wastewater, especially in developing countries [4-7]. Nevertheless, numerous active biofilter systems show attenuated and limited reductions in TN levels [4-8]. Thus, the enhanced performance of TN treatment in biofilter systems is a critical task. In addition, increasing pollution discharges in rural villages across large areas in developing countries and stricter N discharge limitations ultimately prompt urgent efforts toward ameliorated engineering designs and the application of biofilter systems.

In a biofilter, wastewater traverses multilayer devices packed with various media (i.e., lava rocks, volcanic rocks, bioceramics, natural zeolites, gravel, and polyurethane foam), and air is immediately brought into the system [2,9]. However, microorganisms immobilized in the media degrade the COD and N through several pathways, such as nitrification, denitrification, and anammox [10-13]. It is generally accepted that biofilter systems can provide suitable aerobic areas for nitrification but generally lack sufficient anaerobic areas for anaerobic microorganisms (i.e., anammox and denitrification) to function well, which leads to nitrate (NO3--N) accumulation and attenuated TN removal [5]. Previous studies have reported that single-stage biofilter systems are unable to efficiently remove TN because of their inability to synchronously provide suitable aerobic and anaerobic areas for both nitrifiers and denitrifiers [14]. Therefore, hybrid biofilter systems have been used to handle the continuous need for TN removal [5,8,15]. A denitrification biofilter was used [16] which was packed with reticulated polyurethane foam as a biofilm carrier for treating low carbon: nitrogen ratios (0.65–3.0) in wastewater and the TN removal efficiency ranged from 18.5 to 92.2%. A novel self-sustainable biofilm reactor was designed [4] with NH4+-N and TN removal efficiencies of 94% and 79% (9.84 g/m2·d), respectively. Average NH4+-N and TN removal efficiencies of 69.3% (approximately 2.9 g/m2·d) and 54% (approximately 2.2 g/m2·d) was achieved respectively [17] in a sponge-bed trickling filter. The above results indicate that achieving high and stable TN removals in biofilters remains a challenge because of the various feedbacks of microorganisms associated with N cycling to different operating parameters and ambient conditions.

Vertical-flow biofilters have been devised as a simple and useful modification to strengthen the removal of COD, NH4+- N, and TN [18,19]. These biofilters generate a rhythmic sequential cycle of aerobic zones, aerobic-anaerobic zones and anaerobic zones, which enhances nitrification and dentrification in a single reactor. However, due to the different responses of N microorganisms to aerobic and anaerobic environments, microbial communities show large heterogeneities along the depth gradient in multiple treatment units in biofilters [20]. Previous studies have revealed that the aerobic environment in biofilter systems has a negative effect on denitrifying microorganisms to function well, and the carbon substances for denitrifying microorganisms are often deficient, as the carbon sources are availably degraded which results in high NO3--N accumulation in the vertical-flow biofilters [21]. Thus, denitrification can be hypothesized as a rate-limiting TN removal process in vertical-flow biofilters. The co-occurrence of partial nitrification, denitrification, and anammox in bioreactors is known as a key factor responsible for the enhanced removal of NH4+-N and TN [22,23]. Although the effects of vertical-flow biofilters on COD and NH4+-N removal are largely explored, no further efforts have been made to enhance TN removal and investigate the underlying mechanisms of eliminating NO3--N accumulation and increasing TN removal, and the quantitative contribution of nitrogen to microbial genes in different treatment units in vertical-flow biofilters is still lacking. All of these unrevealed relationships limit our ability to improve the ability of TN removal.

In this study, we explore the feasibility of vertical-flow biofilters removing NH4+-N and TN under various organic loads and the quantitative contribution of N microbes to TN removal. The main objectives are to evaluate the removal efficiencies of COD, NH4+-N and TN in different treatment units in vertical-flow biofilters; to determine the predominant functional genes that shape NH4+-N and TN removal in different treatment units and to quantify the distributional contributions of predominant functional genes in different treatment units (along the depth gradient).

Material and Methods

Experimental

Vertical-flow biofilter: A vertical-flow biofilter, with a working volume of 72 L, was built (Supporting Information, Figure S1). The biofilter was subdivided into three parts (P1, P2, and P3). P1 (with natural ventilation) consisted of two functional layers (for each layer, L × W × H=20 × 20 × 30 cm3) which were filled with lava rocks (particle size: 5-8 mm) and bioceramics (particle size: 5-8 mm). P2 (with natural ventilation) consisted of two functional layers (for each layer, L × W × H=20 × 20 × 30 cm3) which were packed with lava rocks (particle size: 2-5 mm) and bio-ceramics (particle size: 2-5 mm). P3 (without ventilation) consisted of one functional layer (L × W × H=20 × 20 × 60 cm3)which was packed with polyurethane foaming plastic with 1 to 2 mm apertures. A bistratal sieve tray (thickness: 2 cm) was installed between the treatment layers of P1 and P2 to mix wastewater and air.

microbiology-vertical-flow-biofilter

Figure S1: Schematic diagram of the vertical-flow biofilter

According to our actual environmental quality surveys, the average COD and NH4+-N concentrations in domestic wastewaters were 342.65 ± 86.52 mg/L and 28.30 ± 12.25 mg/L respectively. The synthetic wastewater was made from tap water (NO3--N: 4.2-6.9 mg/L). In this study, the synthetic wastewater contained 200-600 mg/L of COD, 20-40 mg/L of NH4+-N, 25.49-47.91 mg/L of TN and 3-4 mg/L of TP was fed into the vertical-flow biofilter. The hydraulic loading rate was 1.0 m3/m2·d. The basic composition of the synthetic wastewater in each operation stage is organized in Table 1. The vertical-flow biofilter was installed indoors and the temperature and pH in the influents and effluents ranged from 18.5°C to 26.8°C and 7.2 to 8.1 respectively. The experiment included a start-up stage (five weeks) and operational stage (0-140 days) and the entire experiment lasted a total of 175 days.

Parameters Stage I Stage II Stage III Stage IV Stage V
COD (C6H12O6, mg/L) 200 300 400 500 600
NH4+-N (NH4Cl, mg/L) 20 25 30 35 40
C/N ratio 10.00 12.00 13.33 14.29 15.00
TP (KH2PO4, mg/L) 3.0 3.2 3.5 3.8 4.0
Time (day) 0~28 29~56 57~84 85~112 113~140

Table 1: Synthetic wastewater composition in each stage.

Samples

Water samples were extracted from P1, P2, and P3 one time each week. The water quality indexes (i.e. COD, NH4+-N, nitrite (NO2−-N), NO3−-N, TN, DO, and pH) of the influents and effluents were measured using standard techniques, and standard analytical procedures for the variables are described elsewhere [22-24]. The microbial samples (both lava rock/ bioceramic and polyurethane foaming plastic) were collected from the biofilter at the end of days 14, 28, 42, 56, 70, 84, 98, 112, 126, and 140. At every sampling time, five microorganism samples were gathered from P1, P2, and P3. Then, the samples were stored in a -20°C ice incubator and ready for DNA extraction. The OMEGA soil extraction kit (D5625-01) was used to extract genomic DNA from the samples (e.g. from the 0.5 g to 1.0 g sample) [23]. Then, the genomic DNA was stored in a -20°C ice incubator.

Quantitative PCR

The amoA and anammox genes are currently known as the markers of aerobic ammonia oxidation and anoxic ammonia oxidation, respectively [25,26]. The nxrA gene is currently known as the marker of NO2--N oxidation [30]. The periplasmic nitrate reductase (napA, NO3--N → NO2--N), membrane-bound nitrate reductase (narG, NO3--N → NO2--N), nitrite reductase (nirK/nirS, NO2--N → NO), and nitrous oxide reductase (nosZ, N2O → N2) are widely adopted as markers for denitrifying bacteria. A PCR was performed with primer pairs Eub338f/Eub518r for total bacteria [27], Ar109f/Ar344r for archaea [28], Amx809f/Amx1066r for anammox [29], amo598f/amo718r for amoA [26], F1norA/R1norA for nxrA [30], V17F/4R for napA [31], 1960 m2f/2050 m2r for narG [32], 583F/909R for nirK [33], nirScd3aF/nirSR3cd for nirS and 1527F/1773R for nosZ [34]. The qPCR was adopted to quantify the population dynamics of N microbial genes in the biofilter (P1, P2, and P3) with a 20 μL reaction mixture [16,35]. The detailed protocol and parameters for each marker are described elsewhere [16,23].

Data Processing and Statistics

Influent and effluent concentrations were adopted to quantify the removal efficiencies (%). Influent and effluent concentrations, hydraulic retention times (2.0 h) and the working volumes of functional layers (V = 0.2 × 0.2 m2) were collectively adopted to quantify the removal rates of NH4+-N, NO3--N and TN (g/m2.d). Standard deviations (SDs) in the population dynamics of the N microbial genes were analyzed using three duplicated data via the qPCR. The population dynamics of the N microbial genes and other ratios of the N microbial genes (e.g. amoA/bacteria, (nirK + nirS + nosZ)/ bacteria and nxrA/bacteria) were adopted as candidate-independent variables in the linear regression analysis, with SPSS 20 to link with the N removal rates (i.e. NH4+-N, NO3--N and TN). A pathway analysis was adopted to quantify the contributions of key functional genes (i.e. functional gene groups) to the N removal rates.

Results and Discussion

Treatment Performance of the Biofilter

During the operation, the vertical-flow biofilter achieved high COD removal efficiencies (92.15 ± 2.91%) (Figure 1a). P1, P2, and P3 accounted for 30.50 ± 9.20%, 44.22 ± 12.57% and 17.43 ± 6.79% of COD removal respectively (Figure 1b). It is hypothesized that the removal efficiencies of the COD are higher than those in other biofilter systems based on traditional methods and newly discovered methods with artificial aerations, which are currently used to treat domestic wastewater (COD=120–450 mg/L) with gross COD removal efficiencies fluctuating from 50% to 89% [7,36,37]. The average rates for COD transformation in P1, P2, and P3 were 174.14 ± 66.69 g/m2·d, 288.76 ± 163.78 g/m2·d and 95.26 ± 37.36 g/m2·d respectively. The biofilter achieved a COD removal rate of 558.15 ± 208.47 g/m2·d (Figure S2), which was higher than the treatment performances of CODs investigated in previous studies (e.g. 437.00 g/m2·d by [38] and 275.25 g/m2·d by [5]. The above results revealed the COD removal contributions of P1, P2, and P3 along the depth gradient (from top to bottom). This high COD removal performance was due to the sieve tray operation in P1 (with natural ventilation) and P2 (with natural ventilation) which allowed for wastewater/air contact. However, P3 (without ventilation, Figure S1) achieved a lower COD removal compared with P1 and P2. This was because most denitrifiers are heterotrophic bacteria which utilize organic C as a required organic source; this leads to the continued consumption and loss of COD [16,39].

microbiology-dynamic-transformation

Figure 1: Influent concentrations, effluent concentrations and removal efficiencies of COD (a, b), NH4+-N (c, d), and TN (e, f) in the vertical-flow biofilter along the depth gradient.

It is well known that vertical-flow biofilters can effectively remove COD and NH4+-N [8,38,40]. Here, we focus our discussion on the TN removal and effluent which was identified as an indicator for the simultaneous monitoring of multiple water treatment performances. As the COD increased from 200 mg/L to 600 mg/L, the NH4+-N removal efficiency stabilized at 95.88 ± 2.45% (Figure 1c). The biofilter achieved a TN removal efficiency of 87.28 ± 4.12%. According to previous study [5,41], it has been reported that a TN85.4%using a vertical-flow biofilter when integrated with a horizontal-flow multisoil-layering reactor. In other hybrid biofilters, TN removal efficiencies range from 66.5% to 83% [37,42]. In this study, the biofilter achieved even higher TN removal efficiency (maximum of 46.5 g/m2·d). TN removal rates of 27.83-30.62 g/m2·d in a vertical-flow biofilter and horizontal-flow multisoil-layering reactor was reported [5]. TN removal rates in hybrid biofilters of 2.34 and 9.84 g/m2·d was achieved respectively [4,17]. An average TN removal rate of 0.11 kg/m3·d (approximately 0.86 g/m2·d) in a partial nitrification-anammox biofilter was reported [7]. The high and stabilized removals of NH4+-N and TN in the biofilter were comparable with the values reported in the vertical-flow biofilters used for treating rural wastewater [5], multimedia biofilters used for treating for sewage treatment [20], simultaneous nitrification-denitrification biofilters [43] and anammox biofilm reactors used for the removal of nitrogen from wastewater [4,7]. In addition, the average TN effluent concentrations (4.23 ± 0.5 mg/L) were lower than those in aerobic or anaerobic biofilter systems, with a practical effluent concentration fluctuating from 5.17 mg/L to 13.1 mg/L [7,44,45].

The dynamic transformation of nitrogen in P1, P2, and P3 is shown in Figure 2 and Figure S2. P1, P2, and P3 accounted for 45.93 ± 7.70%, 39.56 ± 9.39%, and 10.65 ± 4.26% of the NH4+-N removal (Figure 1d) respectively. P1, P2, and P3 accounted for 37.72 ± 3.95%, 28.24 ± 5.49%, and 20.32 ± 4.73% of the TN removal, respectively. The residual NH4+-N in the effluent markedly decreased from 16.09 mg/L (P1) to 1.00 mg/L (P3). This distinct decline in the NH4+-N effluent was attributed to the natural ventilation in P1 and P2 (Figure S1), leading to the enhanced nitrification responsible for eliminating the accumulation of NH4+-N and NO3--N in the system (Figure 2 and Figure S2). Together, these results are consistent with those in previous studies, suggesting that biofilter systems with aeration operations enable the effective removal of COD and NH4+-N and contribute to residual NO3--N and TN in the effluent [7,21,42]. Throughout this study, apparent declines in the NO3--N and TN effluent concentrations in P3 (without air supply, Figure S1) are observed in Figure 2c, indicating that denitrification was sufficient for NO3--N and TN removal. P3 had a significantly higher rate of NO3--N transformation (3.83 g/m2·d) than those in P1 (0.29 g/m2·d) and P2 (-2.24 g/m2·d), suggesting that the functional layer without an oxygen supply plays an important role in enhancing the denitrification process to achieve effective NO3--N and TN removal.

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Figure S2: Long-term dynamic transformation rates of nitrogen in the biofilter

microbiology-depth-gradient

Figure 2: Long-term dynamic transformation of nitrogen in the vertical-flow biofilter along the depth gradient.

Nitrogen Removal Mechanisms

The experiment was divided into a startup stage (five weeks) and operational stage (0-140 days). The abundances of bacteria, archaea, and N microbial genes in P1, P2, and P3 were quantified throughout the phases of operation to estimate the changes in their numbers, which reveals the evolution of N removal pathways in P1, P2, and P3.

The results from Figure 3a indicate that the absolute abundances of bacteria in P1, P2, and P3 showed rapid increases by 12.35, 7.21, and 3.54-fold respectively over the entire period. These increases directly enhanced the continuous consumption of COD, leading to 2.03, 7.16, and 1.07-fold increases in the COD removal efficiencies of P1, P2, and P3 respectively. In this study, the COD concentrations increased from 200 mg/L to 600 mg/L, leading to an enhanced supplemental substrate for the bacteria community in the biofilter and causing rapid enrichment and growth [39]. The archaea in P1, P2, and P3 increased from 2.75 × 107 copies/g on day 14 (operational stage) to 5.67 × 108 copies/g on day 140, exhibiting low abundance and similar patterns relative to the change in COD concentration. Although archaea revealed much smaller amounts compared to bacteria Figure 3b, the archaea community may play a key role in NH4+-N removal [46,47].

microbiology-microbial-communities

Figure 3: Dynamic populations of microbial communities and functional genes in the vertical-flow biofilter along the depth gradient: bacteria (a), archaea (b), amoA (c), anammox (d), nxrA (e), narG + napA (f), nirK + nirS (g), and nosZ (h).

The NH4+ transformation communities harboring specific catabolic nitrifying-ammonium monooxygenase (amoA) and anaerobic ammonium-oxidizing (anammox) microorganisms are organized in Figure 3c and Figure 3d respectively. As the COD concentration increases, the abundance of amoA in P1, P2, and P3, with overall declining trends and similar patterns, varied between 2.13 × 104 copies/g and 7.39 × 106 copies/g. However, the abundance of anammox in P1, P2 and P3 with overall increasing trends and similar patterns, varied between 4.89 × 105 copies/g and 2.02 × 107 copies/g. The absolute abundance of amoA in P1 on day 14 was 15.10 times greater than that of anammox. These results indicate that aerobic ammonia oxidation was the controlled NH4+-N removal pathway (45.93% of NH4+-N removal, Figure 1d). Meanwhile, the ratio of amoA to anammox in P2 on day 14 was approximately 0.75, suggesting that the relationship between the nitrification and anammox processes was the predominant factor responsible for high NH4+-N removal (39.56% of NH4+-N removal, Figure 1d). The anammox in P3 on day 7 was 16.02 times greater than amoA, indicating that anaerobic ammonia oxidation was a key NH4+-N removal pathway (10.65% of NH4+-N removal, Figure 1d). After 140 days of operation, the ratios of anammox to amoA in P1, P2 and P3 were approximately 0.39, 14.19 and 947.16 respectively, suggesting that nitrification in P1 and anammox in P2 and P3 were dominant NH4+-N removal pathways responsible for the robust NH4+-N removal (96.14%, Figure 1d). The above findings suggest that the anammox process was observably enhanced and eventually superseded nitrification as the predominant NH4+-N removal pathway in the vertical-flow biofilter. As the COD concentration increased, the DO was continuously consumed during the process of organic matter oxidation (92.15% of COD removal, Figure 1b), creating intensive microdomain anaerobic environmental conditions in P1, P2 and P3, which were suitable for the growth of anaerobic oxidizing (anammox) bacteria as the governing driver of NH4+- N removal [3,4,48].

During the entire period, the nxrA gene slightly showed decreases in P1, P2, and P3, leading to attenuated nitrification activity, which accounted for the reduced production of NO3--N. Five denitrifying genes (i.e., narG, napA, nirK, nirS, and nosZ) are shown in Figures 3f-3h. All five genes showed increases in P1, P2, and P3, resulting in increased denitrification that accounted for the NO3--N removal. The synchronous growth of these five genes in the biofilter was due to their similar adaptations to anoxic environments and their associated yet distinct ecological niches [31,49,50]. Previous studies have indicated that denitrification is the dominant pathway, and the rate-limiting process is attributed to achieving a high TN removal [8,23]. In this study, the abundances of the five genes in P2 (with natural ventilation) and P3 (without natural ventilation) were 1.40 and 1.81 times greater respectively, than those in P1 (with natural ventilation), leading to higher contributions of P2 and P3 that were responsible for TN (48.56% of TN removal, Figure 1f) than those of P1 (38.72% of TN removal, Figure 1f). This might also explain the corresponding high TN removal in the biofilter compared to that in other biofilters for wastewater treatment [5,16,51].

Nitrogen Transformation Pathway

Quantitative relationships were determined to connect macroscale NH4+-N and TN removal and functional genes associate with the nitrogen cycle and improve the understanding of predominant functional genes that control the NH4+- N and TN removal processes in P1, P2, and P3. By introducing a number of specific variables into the linear stepwise regression models [23], the equations of NH4+-N, NO3--N, and TN were built with R2 > 0.819 (Table 2).

Stepwise regression models Equations R2 P F
P1 NH4+-N = 54.793amoA/bacteria + 41.906(nirK + nirS + nosZ)/bacteria – 80.831 0.966 0.034 28.803
  NO3--N = –6.387nxrA/(napA + narG) – 4.258nxrA/bacteria+9.955 0.993 0.007 135.545
  TN = 22.231(nirK + nirS + nosZ)/bacteria – 5.820nxrA/(napA + narG) – 13.337 0.996 0.004 236.885
P2 NH4+-N = –66.063amoA/anammox + 3.368nxrA+50.874 0.995 0.005 211.103
  NO3--N = 8.531(napA + narG)/nxrA – 9.724 0.819 0.035 13.599
  TN = –0.301amoA/anammox + 17.674nosZ/bacteria – 4.872 0.824 0.039 14.666
P3 NH4+-N = 5.097anammox/amoA – 4.715 0.915 0.023 32.147
  NO3--N = 1.495anammox/amoA + 1.417(napA + narG)/nxrA – 1.956 0.980 0.020 49.974
  TN = 74.686anammox/bacteria + 4.703(napA + narG +nirK + nirS + nosZ)/bacteria – 55.442 0.949 0.046 18.394

Table 2: Quantitative response relationships between the nitrogen transformation rates and functional gene groups in P1, P2, and P3.

The results showed that the NH4+-N reduction rate in P1 was significantly correlated with the ratios of amoA/bacteria and (nirK + nirS + nosZ)/bacteria. A greater direct contribution of (nirK + nirS + nosZ)/bacteria (65.8%) to the NH4+-N reduction compared with amoA/bacteria (30.8%) was observed in P1 over the entire period Figure 4a. The first variable, amoA/bacteria, shows a level of NH4+-N removed via the nitrification process (NH4+-N → NO2--N), which results in positive relations with the NH4+-N reduction rate, while the variable (nirK + nirS + nosZ)/bacteria was positively correlated with NH4+-N removal. It is generally accepted that nitrification and denitrification are adverse processes that function well under aerobic and anaerobic environmental conditions respectively [52]. Our results indicated the functional interplay between nitrifiers and denitrifiers which is in agreement with [53] who suggested that the polyphyletic distribution of denitrifying genes leads to their co-occurrence with nitrifying genes in many strains. The NO3--N accumulation rate was negatively correlated with nxrA/(napA + narG) and nxrA/bacteria (Table 1). A greater direct contribution of nxrA/(napA + narG) (-64.7%) to NO3--N accumulation compared with nxrA/bacteria (-33.8%) was observed in P1 (Figure S3a). The nxrA gene is related to NO3--N production, while the napA and narG genes are related to NO3--N consumption. Thus, the ratios of nxrA/(napA + narG) and nxrA/bacteria are defined as the NO3--N accumulation. The TN transformation in P1, related to the nitrification and denitrification processes, was jointly controlled by (nirK + nirS + nosZ)/bacteria and nxrA/(napA + narG). A greater direct contribution of (nirK + nirS + nosZ)/bacteria (90.9%) to TN reduction compared with nxrA/(napA + narG) (-21.0%) was observed in P1 over the entire period (Figure 4a). The above results indicate the close relationship between nitrification and denitrification processes was contributed to the robust NH4+-N and TN removal performances in P1 [36,54].

microbiology-Pathway-diagrams

Figure 4: Pathway diagrams estimating the direct contributions of functional gene groups to NH4+-N and TN removal in P1, P2, and P3. The arrows designate the direction of causality. The numbers adjacent to the arrows represent the degree of the direct contributions, and the positive and negative numbers represent the positive and negative contributions respectively.

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Figure S3: Pathway diagrams assessing the effects of functional gene groups on the NO3--N transformation rate (or accumulation rates if the effluent NO3--N concentration increased).

The NH4+-N reduction rate in P2 was negatively correlated with amoA/anammox. A greater direct contribution of nxrA (39.2%) to the NH4+-N reduction compared with amoA/anammox (-95.1%) was observed in P1 over the entire period (Figure 4a). This was because the ammonia-oxidizing bacteria (AOB) accounted for the production of NO2 --N (NH4+-N → NO2 --N), whereas anammox was responsible for NO2 --N consumption. However, AOB associated with the NH4+-N transformation are often restrained by the accumulation of NO2 --N [22,55,56]. The NO2 --N accumulation is known as the ratio of amoA/anammox. This is because the amoA gene is linked with NO2 --N production (NH4+-N → NO2 --N), whereas nxrA and anammox are associated with the consumption of NO2 --N [39]. This result shows the ecological association between nxrA and anammox during the removal process of NH4+-N, which is usually considered to be dominated and actuated by only the amoA gene. The NO3--N transformation is governed by the ratio of (napA + narG)/nxrA because of the two homogenous function genes (napA and narG) linked with NO3--N consumption, whereas nitrite oxidizing bacteria (nxrA) is responsible for NO3--N production. The results from Figure S3b indicate that (napA + narG)/nxrA was the predominant gene group contributing to high NO3--N reduction (90.5%) in P2. The TN reduction rate in P2 was jointly controlled by amoA/anammox and nosZ/bacteria (Table 4). A greater direct contribution of nosZ/bacteria (90.0%) to TN reduction compared with amoA/anammox (-1.0%) was observed in P2 over the entire period (Figure 4b). The amoA/ anammox variable was negatively linked with the NO2 --N accumulation rates, while the variable nosZ/bacteria were positively linked with the TN reduction rate. The nosZ gene is currently accepted as a representative for the complete degree of the denitrification process [39,57]. Thus, an increasing nosZ represents the level of TN transformation. The variable anammox/amoA, which is identified as NO2 --N consumption, exhibits a positive link with the NH4+-N and NO3--N transformations in P2 because anammox is responsible for NO2 --N consumption, whereas amoA is responsible for NO2 --N accumulation. Thus, the consumption ratio suggests the extent or level of NH4+-N transformation. More NO2 -- N consumption results in a higher NH4+-N transformation. The nxrA/bacteria variable exhibits a positive link with the NH4+-N transformation rate. The nxrA gene directly consumes NO2 --N and, thus, the consumption ratio indirectly represents the transformation of NH4+-N. The above results indicate that combined anammox/nitrification (i.e. completely autotrophic nitrogen removal over nitrite; CANON) was contributed to NH4+-N and TN removal [36,54].

The results from Figure 4c indicated that anammox/amoA was the key factor contributing to the high reduction of NH4+-N (95.6%) in P3. A higher direct effect of (napA + narG)/nxrA (53.3%) on the NO3--N reduction compared with anammox/amoA (46.6%) was observed in P3 (Figure S3c). The TN reduction rate in P3 was significantly correlated with the ratios of (napA + narG + nirK + nirS + nosZ)/bacteria and anammox/bacteria. A higher direct effect of anammox/ bacteria (49.2%) on TN reduction compared with (napA + narG + nirK + nirS + nosZ)/bacteria (39.6%) was observed in P3 (Figure 4c). The two variables were directly involved in the consumption of NH4+-N and NO3--N during the anammox and denitrification processes and were, therefore, positively linked with the TN reduction. Thus, both anammox and denitrified microorganisms contributed to the TN reduction. On the functional gene level, the results suggest that the co-occurrence of simultaneous nitrification, anammox, and denitrification (SNAD) processes can be conducive for the simultaneous and enhanced removal of N and COD in the biofilter system [22,58,59].

Environmental Implications

Biofilter systems have been largely explored and adopted as a well-known technology to remove carbon and nitrogen contaminants from wastewater. Our results indicate that the high removal potential and adaptability to remove COD, NH4+-N and TN from domestic wastewater were observed in a single vertical-flow biofilter. The maximum pollutant concentrations (COD=32.76 mg/L, NH4+-N=2.63 mg/L and TN=6.79 mg/L) in the effluent from the biofilter were lower than the most rigorously regulated Class 1 A values (COD ≤ 50 mg/L, TN ≤ 15 mg/L, and NH4+-N ≤ 5 mg/L) in the China National Standard (GB18918-2002).

To protect the surface water environment, many developing countries have established stricter statutes and restrictive standards to limit the total emission of TN [60]. Therefore, the comprehensive advantages of technical feasibility and easy operation (without the requirements of continuous aeration operations or extra running costs) offer principal benefits for the utilization of a biofilter as an advanced treatment technique to promote TN removal from domestic wastewater, especially in rural areas of developing countries. This study suggests great potential for the real application of a verticalflow biofilter for treating domestic wastewater. It may become a sustainable and affordable domestic wastewater purification method in remote or economically depressed regions of developing countries. However, the engineering applications of biofilter systems still need further study.

Conclusion

In this study, a three-stage vertical flow biofilter without extra aeration running achieved high removal efficiencies of TN (87.00 ± 2.59%, 33.69 ± 7.93 g m-2 d-1), NH4+-N (95.90 ± 2.44%, 24.17 ± 6.23 g m-2 d-1), and COD (92.00 ± 3.07%, 558.15 ± 208.47 g m-2 d-1). NH4+-N and TN removal contributions can be ranked as follows: P1 (45.9% and 38.4% respectively) > P2 (39.6% and 28.2% respectively) > P3 (10.6% and 20.5% respectively). Specifically, NO3--N removal rates in P3 was notably enhanced, resulting in apparent decline of NO3--N and TN in the effluent. The coupling of nitrification and denitrification was contributed to the robust NH4+-N and TN removal in P1. The combined anammox and nitrification was contributed to NH4+-N and TN removal in P2. The combined anammox and denitrification accounted for the robust TN reduction in P3..

Acknowledgments

This work was supported by the science and technology project of the Yangling Demonstration Zone (2016SF-05), Fundamental Research Funds for Central Universities (Z109021711), and the Start-up Funds of Northwest A & F University (for Honglei Wang; Z109021610).

References