# Removal of Nutrients from Fertilizer Plant Wastewater UsingScenedesmus sp.: Formation of Bioflocculation and Enhancement of Removal Efficiency

Authors: Thanh-Luu Pham; Manh Ha Bui
Journal: Journal of Chemistry
 (2020)

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## Abstract

Eutrophication of surface water has become an environmental concern in recent decades. High concentrations of nutrients, especially nitrogen- and phosphorus-rich species, have contributed to the process of eutrophication, highlighting a demand for effective and economical methods of removing nitrogen and phosphorus from wastewater. This study aimed to investigate the ability of a green microalga species,Scenedesmus sp., to remove nitrogen and phosphorus, as well as chemical oxygen demand (COD) and biochemical oxygen demand (BOD5), from fertilizer plant wastewater. Different microalgae concentrations from 10 mg/L to 60 mg/L were used to assess the growth rate, biomass production, and removal ability. The results indicated that Scenedesmus sp. grew well in the wastewater (with a growth rate from 0.3 to 0.38/day) and produced up to 70.2 mg/L of dry biomass. The algal species was able to remove ammonium (NH4+), nitrate (NO3−), phosphate (PO43−), total phosphorus (TP), COD, and BOD5 with removal rates up to 93%, 84%, 97%, 96%, 93%, and 84%, respectively. Autobioflocculation (AFL) was observed in all cultures with flocculation activity of up to 88.3% in the highest algal biomass treatment. The formation of bioflocculation enhanced the removal of nutrients, COD, and BOD5 from wastewater effluent. The results indicated that wastewater from a fertilizer plant could be used as a cost-effective growth medium for algal biomass. The autoflocculation of microalgae could be used as a more practical approach for wastewater treatment using microalgae to eliminate eutrophication.


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## Body

## 1. Introduction

In recent decades, the intensity of agricultural and industrial activities, together with rapid urbanization, has generated large amounts of wastewaters [1]. The continuous disposal of wastewaters without appropriate treatment to water sources has posed severe water pollution problems, especially in developing countries [2]. These effluents contain a high concentration of nutrients such as nitrogen and phosphorus, which are the leading causes of eutrophication in natural waters [3]. This condition is favorable for the development of harmful algal blooms (HABs) resulted in the degradation of water quality and impairment of freshwater ecosystems [4]. Moreover, the occurrence of HABs can result in serious problems such as anoxic conditions, toxin productions, killing of fish, and altered biodiversity [5]. HABs are considered a public health risk due to produce a variety of toxic secondary metabolisms [6]. For these reasons, many efforts have been done in order to mitigate eutrophication by reducing nitrogen and phosphorus concentration in wastewater effluents before discharging into water sources.To mitigate eutrophication, nutrient control is a fundamental process [7]. Physical and chemical methods have been developed for the removal of nutrients from wastewater, but these are costly and produce high sludge content [8]. Due to requiring large amounts of the nutrient, especially nitrogen and phosphorus for growth, many species of green microalgae such as Chlorella sp., Scenedesmus sp., and Neochloris sp. have been proposed as an alternative biological treatment to remove nitrogen and phosphorus from a different sources of wastewater for many years [2, 8, 9]. Indeed, extensive studies have been carried out on the subject of microalgae cultivation using wastewater. High removal efficiencies of nitrogen and phosphorus (more than 80%) from wastewaters of different sources have already been recorded for several microalgae species [9–12].Recent evidence indicated that the formation of microalgae-bacteria flocculation (MBF) and fungi-assisted microalgae pellets (FAMP) enhanced nutrient removal from wastewater effluent [13, 14]. While MBF is a flocculation formation of microalgae cells assisted with bacteria, FAMP is a pellet formation of microalgae cells supported with fungi [14, 15]. During bioflocculation formation, the aggregation of bacteria or fungi and microalgae cells creates large flocs or pellets which accelerate the adsorption of suspended compounds in surrounding medium to form co-bioflocculate and thus enhance the removal efficiency of nitrogen and phosphorus [14–16]. Therefore, MBF and FAMP have been used to improve nutrient removal and effluent recovery in aerobic-activated sludge technologies [13, 15, 17]. The bioflocculation of microalgae and bacteria have been intensively studied and reviewed for recent advances and perspectives [18–20]. Besides, MBF can be used as a promising low-cost method for harvesting microalga biomass [14, 21].Another flocculation can occur naturally in certain microalgae in response to some environmental stress, which is so-called autoflocculation (AFL) [14]. However, little is known about AFL of microalgae. Moreover, the driving factor for the formation of AFL is not understood yet. Therefore, it is vital to pay more attention to the technique to obtain more knowledge about AFL formation and enhance its application.The fertilizer industry is one of the most important economic sectors in Vietnam due to its economy is based on agriculture. Wastewaters from fertilizer plants contained a variety of nutrients include nitrogen and phosphorous compounds that is a significant problem of water eutrophication [22]. In the present study, wastewater effluent obtained from Phu My Fertilizer Plant (Vietnam) was used as a culture medium for microalgae production. The present study aimed to investigate the nutrient removal ability of a native microalga Scenedesmus sp. species. Furthermore, the biomass growth, flocculating activity, chemical oxygen demand (COD) and biochemical oxygen demand (BOD5) removal, dry matter and chlorophyll content of the flocs collected, and the wastewater nutrient removal were studied in order to evaluate the potential use of the microalgae for controlling eutrophication and producing renewable energy.


## 2. Materials and Methods

### 2.1. Wastewater Sample Collection and Characterization

The wastewater used in the present study was collected from equation tanks (ET) in the Phu My Fertilizer Wastewater Plant (Vietnam). Samples for wastewater characterization were immediately stored at 4°C prior to analysis. The microalgae sample was collected from a similar ET by using a phytoplankton net. Dissolved oxygen (DO), temperature, and water pH were measuredin situ with a multiparameter meter (Hach 156, USA). Before using for all the experiments throughout this study, the wastewater was filtered through 0.45 μm filters to remove the suspended grease layer.


### 2.2. Isolation of Microalgae from Wastewater

The microalgae sample was enriched separately in different flasks with COMBO medium [23] prior to isolation. Samples were screened under a microscope. Scenedesmus sp. was dominant in wastewater. Colonies of Scenedesmus sp. (Figure 1) were isolated by micropipetting and washing. All cultures were maintained under laboratory conditions at a temperature of 27°C, 12 h light photoperiods, and light intensity of 50 μmol photons/m2/s. The axenic strains were cultured in conical flasks containing a sterile liquid medium.Figure 1
Morphology of colonies ofScenedesmus sp. under a microscope. Scale bar: 20 μm.The microalgae biomass was measured using the gravimetric method. A 20 mL sample was placed in a preweighed glass tube. After centrifugation at 4000 rpm for 15 minutes, the supernatant was discarded, and then the tubes were dried at 105°C for 24 hours and reweighted. The dry biomass was calculated gravimetrically by weight difference. Samples were prepared in triplicate for calculation of the standard errors.


### 2.3. Experimental Setup

Precultures showed thatScenedesmus sp. grew well in cultured medium at room temperature (27 ± 1°C) under 12 hour photoperiods with the light intensity of 95 μmol photons/m2/s. Therefore, this condition was selected for conducting the experiments. Batch experiments were conducted in triplicate with an initial pH of 7.3 ± 0.5 (no pH control) by using 1000 mL flasks placed in a shaker at 70 rpm. Each flask with 800 mL of wastewater inoculated with a suspension of precultured cells. The initial biomass was prepared at 10, 20, 30, 40, and 60 mg dry weight (DW)/L. Illumination was provided continuously by linear fluorescent lamps using 12 hour photoperiods for 10 days. The flasks containing wastewater without microalgae cells were used as controls. The single-isolated microalga was used for the experiment. 1 mL sample was collected every day to determine optical density. Samples for measurement nutrients concentration were prepared by withdrawing 100 mL from flasks at three-day interval. And then, the samples were centrifuged at 5000 rpm for 10 min to remove the microalga cells, and the supernatant was collected for analysis of nutrients concentration in the same days. Dry microalga biomass and total lipid content were determined at the beginning and end of the bioassays.


### 2.4. Measurement of the Growth Rate and Flocculation Activity

The growth rate (GR) of the microalgae was calculated as follows:(1)GR=lnNt/N0Tt−T0,where Nt and N0 are the microalgae biomass (mg/L) at the end (Tt) and start (T0) of the growth phase, respectively.The flocculation activity (FA) was measured according to the method reported previously by Nguyen et al. [13] as follows:(2)FA%=1−OD680tOD680t0×100,where OD680t is the optical density of the sample at time t and OD680t0 is the optical density at time t0.


### 2.5. Chlorophyll Content

To determine the chlorophyll (Chl) content of microalgae, a known volume of culture samples (1 mL) was centrifuged at 5000 rpm for 10 min. After discarding the supernatant, Chl from microalgae cells was extracted with 3 mL of methanol (100%) overnight in the dark at room temperature. Then, the suspension was centrifuged at 10000 rpm for 10 min to remove the cell debris. After centrifugation, the supernatant was used to measure Chl content 652 nm (Chl-b), 665 nm (Chl-a), and 750 nm (turbidity of suspension) by using a spectrophotometer (UV-VIS, Harch, 500), and the concentration of Chl (μg/mL) was calculated as follows [24]:(3)Chl=–8.0962OD652–OD750+16.5169OD665–OD750V2V1l,where V1 and V2 are the volume of sample suspension and methanol used, respectively. And, l is the optical path, which is 1 cm.


### 2.6. Measurement of Wastewater Quality Parameters

Wastewater quality parameters including ammonium (NH4+), nitrate (NO3−) and phosphate (PO43−), total nitrogen (TN), total phosphate and total suspended solids (TSS), biochemical oxygen demand (BOD5), and chemical oxygen demand (COD) were analyzed according to the Standard Methods for Examination of Water and Wastewater [25].The efficiency of nutrient removal (Er) in wastewater was expressed in(4)Er%=Co−CfCo×100,where Co and Cf are the initial and final concentrations of nutrients concentration in wastewater effluent.


### 2.7. Statistical Analysis

The differences between mean values of the specific growth rate, dry microalga biomass, and pollutant removal rates were tested for significance using a one-way analysis of variance (ANOVA).P values ≤0.05 were considered significant differences. All results are presented in the form of mean values ± standard deviation from three samples.


## 2.1. Wastewater Sample Collection and Characterization

The wastewater used in the present study was collected from equation tanks (ET) in the Phu My Fertilizer Wastewater Plant (Vietnam). Samples for wastewater characterization were immediately stored at 4°C prior to analysis. The microalgae sample was collected from a similar ET by using a phytoplankton net. Dissolved oxygen (DO), temperature, and water pH were measuredin situ with a multiparameter meter (Hach 156, USA). Before using for all the experiments throughout this study, the wastewater was filtered through 0.45 μm filters to remove the suspended grease layer.


## 2.2. Isolation of Microalgae from Wastewater

The microalgae sample was enriched separately in different flasks with COMBO medium [23] prior to isolation. Samples were screened under a microscope. Scenedesmus sp. was dominant in wastewater. Colonies of Scenedesmus sp. (Figure 1) were isolated by micropipetting and washing. All cultures were maintained under laboratory conditions at a temperature of 27°C, 12 h light photoperiods, and light intensity of 50 μmol photons/m2/s. The axenic strains were cultured in conical flasks containing a sterile liquid medium.Figure 1
Morphology of colonies ofScenedesmus sp. under a microscope. Scale bar: 20 μm.The microalgae biomass was measured using the gravimetric method. A 20 mL sample was placed in a preweighed glass tube. After centrifugation at 4000 rpm for 15 minutes, the supernatant was discarded, and then the tubes were dried at 105°C for 24 hours and reweighted. The dry biomass was calculated gravimetrically by weight difference. Samples were prepared in triplicate for calculation of the standard errors.


## 2.3. Experimental Setup

Precultures showed thatScenedesmus sp. grew well in cultured medium at room temperature (27 ± 1°C) under 12 hour photoperiods with the light intensity of 95 μmol photons/m2/s. Therefore, this condition was selected for conducting the experiments. Batch experiments were conducted in triplicate with an initial pH of 7.3 ± 0.5 (no pH control) by using 1000 mL flasks placed in a shaker at 70 rpm. Each flask with 800 mL of wastewater inoculated with a suspension of precultured cells. The initial biomass was prepared at 10, 20, 30, 40, and 60 mg dry weight (DW)/L. Illumination was provided continuously by linear fluorescent lamps using 12 hour photoperiods for 10 days. The flasks containing wastewater without microalgae cells were used as controls. The single-isolated microalga was used for the experiment. 1 mL sample was collected every day to determine optical density. Samples for measurement nutrients concentration were prepared by withdrawing 100 mL from flasks at three-day interval. And then, the samples were centrifuged at 5000 rpm for 10 min to remove the microalga cells, and the supernatant was collected for analysis of nutrients concentration in the same days. Dry microalga biomass and total lipid content were determined at the beginning and end of the bioassays.


## 2.4. Measurement of the Growth Rate and Flocculation Activity

The growth rate (GR) of the microalgae was calculated as follows:(1)GR=lnNt/N0Tt−T0,where Nt and N0 are the microalgae biomass (mg/L) at the end (Tt) and start (T0) of the growth phase, respectively.The flocculation activity (FA) was measured according to the method reported previously by Nguyen et al. [13] as follows:(2)FA%=1−OD680tOD680t0×100,where OD680t is the optical density of the sample at time t and OD680t0 is the optical density at time t0.


## 2.5. Chlorophyll Content

To determine the chlorophyll (Chl) content of microalgae, a known volume of culture samples (1 mL) was centrifuged at 5000 rpm for 10 min. After discarding the supernatant, Chl from microalgae cells was extracted with 3 mL of methanol (100%) overnight in the dark at room temperature. Then, the suspension was centrifuged at 10000 rpm for 10 min to remove the cell debris. After centrifugation, the supernatant was used to measure Chl content 652 nm (Chl-b), 665 nm (Chl-a), and 750 nm (turbidity of suspension) by using a spectrophotometer (UV-VIS, Harch, 500), and the concentration of Chl (μg/mL) was calculated as follows [24]:(3)Chl=–8.0962OD652–OD750+16.5169OD665–OD750V2V1l,where V1 and V2 are the volume of sample suspension and methanol used, respectively. And, l is the optical path, which is 1 cm.


## 2.6. Measurement of Wastewater Quality Parameters

Wastewater quality parameters including ammonium (NH4+), nitrate (NO3−) and phosphate (PO43−), total nitrogen (TN), total phosphate and total suspended solids (TSS), biochemical oxygen demand (BOD5), and chemical oxygen demand (COD) were analyzed according to the Standard Methods for Examination of Water and Wastewater [25].The efficiency of nutrient removal (Er) in wastewater was expressed in(4)Er%=Co−CfCo×100,where Co and Cf are the initial and final concentrations of nutrients concentration in wastewater effluent.


## 2.7. Statistical Analysis

The differences between mean values of the specific growth rate, dry microalga biomass, and pollutant removal rates were tested for significance using a one-way analysis of variance (ANOVA).P values ≤0.05 were considered significant differences. All results are presented in the form of mean values ± standard deviation from three samples.


## 3. Results and Discussion

### 3.1. Characteristics of Wastewater

The wastewater used for the experiment was analyzed for evaluating physico-chemical characteristics. The physico-chemical parameters of the wastewater, including pH, temperature, main nutrient species, as well as BOD5 and COD were presented in Table 1. The wastewater effluent collected from the Phu My Fertilizer Plant contained large amounts of nitrogen (47.3 ± 5.9 mg/L) in the form of ammonium (NH4+) and nitrate (NO3−) with small amounts of phosphate (PO43−) (0.9 ± 0.28 mg/L). Besides, the initial pH of the wastewater effluent was almost constant at pH 6.8. Ammonium is among the most common chemical forms of nitrogen that can be readily absorbed by most microalga species [26]. The concentration of phosphorus was also found sufficient to support algal growth. In this respect, the effluent collected from the Phu My Fertilizer Wastewater Treatment Plant could be used as a cheap source of nutrients for microalgal cultivation. The characterized of the raw wastewater was noted to be favorable for microalgae growth. A ratio of COD/TN/TP, i.e., 180/47/2, found with this wastewater, is suitable for nutrient removal with microalgae. The BOD5/TP, BOD5/PO43−-, and PO43−/TP ratios were found to be reasonably high (Table 1). The optimal inorganic N/P ratio for freshwater algae growth was suggested to be in the range of 6.8–10 [27, 28]. In this study, the inorganic N/P ratio of the effluent was 21, much higher than the optimal ratio, indicating the wastewater as phosphorus limitation media.Table 1
The average composition of the wastewater (average ± SD of five samples).
Parameter
Unit
Value
pH
6.8 ± 0.5
Temperature
°C
29 ± 1.0
Dissolved oxygen (DO)
mg/L
4.7 ± 0.6
Ammonium (NH4+)
mg/L
26.5 ± 3.5
Nitrate (NO3−)
mg/L
11.3 ± 2.1
Phosphorus (PO43+)
mg/L
0.9 ± 0.28
Total nitrogen (TN)
mg/L
47.3 ± 5.9
Total phosphorus (TP)
mg/L
1.8 ± 0.27
Chemical oxygen demand (COD)
mg/L
180 ± 18
Biochemical oxygen demand (BOD5)
mg/L
87 ± 12
Inorganic N/P
21


### 3.2. Growth ofScenedesmus sp. in Wastewater

The green algaeScenedesmus sp. was cultivated in the wastewater for 10 days with different initial cell concentrations from 10 to 60 mg/L. The growth rate, Chl content, and flocculation activity were presented in Table 2. The microalgae grew well in the wastewater with the growth rate from 0.30 to 0.38/day. There was no significant difference in the growth rate as the initial microalgae concentration increased from 10 to 60 mg/L. In the present study, wastewater was used as a nutrient medium for the growth of microalgae, and the utilization of nutrients allows wastewater treatment. During the growth phase, microalgae consumed mineral nutrients and CO2 from wastewater to produce biomass and released O2 into the medium [29].Table 2
The growth rate, chlorophyll content, and flocculation activity.
Initial microalgae concentration (mg/L)
10 ± 0.9
20 ± 1.3
30 ± 1.6
40 ± 1.2
60 ± 1.5
Growth rate/day
0.3 ± 0.03
0.34 ± 0.02
0.36 ± 0.02
0.37 ± 0.03
0.38 ± 0.04
Chlorophyll (mg/L)
13.7 ± 1.8
14.5 ± 1.6
18.2 ± 1.9
19.4 ± 2.3
20.8 ± 2.5
Dry biomass (g/L)
30.5 ± 2.8
35.8 ± 3.3
42.1 ± 2.7
68.3 ± 3.6
70.2 ± 4.9
Flocculation activity (%)
14.2 ± 1.8
23.7 ± 4.3
41.6 ± 2.3
81.5 ± 5.7
88.3 ± 4.1Our results showed that flocculation activity increases with higher cell concentrations. Significant build up of flocculation activity (81.5 and 88.3%) was observed at the highest initial microalgae concentrations of 40 and 60 mg/L. Nguyen et al. [13] reported that the clear formation of flocculation occurred when Chlorella vulgaris in seafood wastewater with the initial concentration above 20 mg/L. Results of the present study are consistent with previous observations that higher initial biomass in the medium a better formation of flocculation because cell-cell encounters are more frequent, leading to better aggregation [30, 31]. Microalgal bioflocculation is an efficient low-cost technology for microalgal harvesting and wastewater treatment [14, 21, 32]. In general, the bioflocculation process is assisted with microorganisms (including bacteria, fungi, and yeasts) or their polymer substances [13–15]. Since no chemical is added in this process, the bio-flocculation has been considered as a sustainable and green technique for algal biomass harvesting [14, 15]. The formation of algal flocculation and its application in wastewater treatment has been reviewed in detail [14, 15, 18]. In the present study, autoflocculation occurred when cultured Scenedesmus sp. in the wastewater for 10 days. Microalgal autoflocculation was found to be associated with increase in culture pH levels, due to CO2 consumption by algal photosynthetic activity. Under these alkaline conditions, some metal ions precipitated together with the algal biomass [33]. Guo et al. [31] reported that cell wall-associated polysaccharides mediated self-flocculation of the microalga S. obliquus. Future study is needed in this area to understand the mechanism of self-flocculation of microalgal cells and increase application in wastewater treatment technology.


### 3.3. Removal of Nitrogen

Nutrient removal in different initial biomass (from 10 to 60 mg/L), including (NH4+, NO3−, PO43− and TP) during the experiment, are shown in Figure 2. The removal rate of NH4+ in the control (no microalgae) was 21.1%, and all treatment with Scenedemsus sp. achieved higher removal than in the control. The NH4+ and NO3− removal performance is shown in Figures 2(a) and 2(b) with the removal efficiencies from 71.7 to 92.8% and from 62.2 to 83.6%, respectively (Table 3). In general, the higher microalgal concentration resulted in higher removal efficiency of NH4+ and NO3−. This observation well agreed with previous studies that higher initial microalgae density enhanced nutrient uptake in different wastewater effluents [13, 34, 35]. Green algae can use a variety of nitrogen sources for growth, making it possible to use these algae for bioremediation to remove nitrogen from wastewater [26, 28]. Microalgae can convert different inorganic nitrogen forms from wastewater to organic nitrogen [15]. Previous studies have demonstrated that the major mechanisms of nitrogen removal in algae systems include nitrification or denitrification and biological uptake of nitrogen by dispersed biomass [34, 36].Figure 2
Changes of NH4+ (a), NO3− (b), PO43− (c), TP (d), COD (e), and BOD5 (f) concentrations in the treatment with different initial microalgae concentrations.
(a)
(b)
(c)
(d)
(e)
(f)Table 3
Flocculation activity and removal efficiency with different initial microalgae concentration.
Initial microalgae concentration
Flocculation activity (%)
Removal efficiency (%)
Ammonium
Nitrate
Phosphate
TP
COD
BOD5
Control
21.1 ± 1.4
−14.9 ± 3.3
17.5 ± 2.1
26.8 ± 2.7
28.1 ± 2.0
16.4 ± 1.1
10 mg/L
14.2 ± 1.8
71.7 ± 1.9
62.2 ± 2.8
94.7 ± 1.5
75.0 ± 3.6
73.5 ± 3.4
65.2 ± 1.4
20 mg/L
23.7 ± 4.3
74.1 ± 2.1
64.6 ± 3.0
94.5 ± 2.3
74.7 ± 1.9
78.4 ± 2.4
67.7 ± 1.8
30 mg/L
51.6 ± 2.3
77.9 ± 2.7
65.6 ± 3.1
96.9 ± 2.8
78.3 ± 2.2
79.5 ± 4.4
68.4 ± 3.0
40 mg/L
81.5 ± 5.7
92.3 ± 4.3
81.5 ± 3.6
94.4 ± 2.2
92.9 ± 1.9
90.4 ± 4.1
82.3 ± 4.1
60 mg/L
88.3 ± 4.1
92.8 ± 3.5
83.6 ± 4.5
97.0 ± 1.7
95.8 ± 2.8
92.6 ± 4.0
83.7 ± 2.3Nitrification was observed during the first four days of the experiment; the decrease in ammonium concentration was accompanied by nitrate formation that peaked at day fourth and then decreased (Figures2(a) and 2(b)). Although ammonium is the preferred nitrogen source for uptake, microalgae can consume nitrogen from a variety of nitrogen sources, including ammonium, nitrate, nitrite, and urea [26, 28, 36]. Since the removal efficiencies on nitrate are usually lower than those on ammonium, our results agree well with previous observations that green microalgae such as Chlorella and Scenedemus were the preference for ammonium to any other form of nitrogen present in wastewater [34, 37].


### 3.4. Removal of Phosphorus

The removal rate ofPO43− and TP were shown in Table 3 and Figures 2(c) and 2(d). The percentages of PO43− and TP removal for the control were only 17.5 and 26.8%, respectively. While in the treatment, this number ranged from 94.7% to 97.0% and from 75% to 95.8% for PO43− and TP, respectively. The removal efficiencies were not significant differences (P=0.227) as treating PO43− with different concentrations of algal biomass. However, more significant TP removal rates were found during the treatment of wastewater with higher initial algae concentration (40 and 60 mg/L), compared with lower algae concentrations (10, 20, and 30 mg/L). The removal rates of TP were a significant correlation with the flocculation activities.Removal ofPO43− up to 97% (Table 3) from wastewater treated with green algae Scenedesmus sp. was very effective. For all treatments, the concentration of PO43− decreased gradually during ten days of the experiment (Figure 2(c)). But for TP, high removal rates were only found in the treatments with 40 or 60 mg/L. The concentration of TP did not decrease significantly during the first two days of the experiment but rapidly reduced from day 2 to day 6 of the test (Figure 2(d)).Table3 shows the removal efficiency and flocculation activity at the end of the experiment. Compared with the control, the treatments with higher initial microalgae concentration had greater removal efficiencies and flocculation activities (Figure 3), showing a relationship between flocculation activity and removal efficiency. Previous studies have reported that the green algae C. vulgaris and S. obliquus could be used to remove PO43− from the difference of wastewaters [15, 34, 35, 37]. Other studies suggested that the immobilized or flocculated form of microalgae is more effective than free form for nutrient removal in wastewater treatment [13, 15, 35, 38]. Our results are consistent with Nguyen et al. [13] that bioflocculation formation of microalgae enhanced nutrient removal from wastewater effluent. Naturally, phosphate seems to be depleted from the medium through different mechanisms including adsorption onto the cells surface, assimilation by the algae biomass or chemical precipitation [17, 34]. Previous studies have demonstrated that assimilation into biomass and adsorption were the main biotic processes of elimination of phosphorus in microalgae [17, 34].Figure 3
Flocculation activities in the control (a) and treatment with different concentrations of microalgae: 10 mg/L (b), 20 mg/L (c), 30 mg/L (d), 40 mg/L (e), and 60 mg/L (f).
(a)
(b)
(c)
(d)
(e)
(f)


### 3.5. Removal of BOD5 and COD

The COD removal efficiencies varied a little among different initial microalgae concentrations (Figure2(e)). While removal rates of only 73.5%, 78.4% and 79.5% were achieved for 10 mg/L, 20 mg/L and 30 mg/L of microalgae concentration, respectively, removal rates for 40 mg/L and 60 mg/L are up to 90.4% and 92.6%, respectively (Table 3). The concentration of COD decreased gradually during the experiment course. The removal rates of BOD5 were almost the same trend with COD removal pattern and showed Figure 2(f). Higher removal rates were also found in the treatments with higher initial microalgae concentrations. There is a relationship between flocculation activity in the treatments with the removal efficiencies of COD and BOD5. Higher flocculation activity resulted in higher removal rates in all treatments. Nguyen et al. [38] investigated the ability to removal of COD and BOD5 in seafood wastewater; results indicated that the removal rates of COD and BOD5 were 88% and 81%, respectively, under sunlight mode and 81% and 74% under fluorescent illumination, respectively, as clear formation of flocculation was observed. Previous studies reported that the presence of microalgae in the cultivation medium had increased the consumption of organic as well as inorganic matters [11, 38, 39]. Besides, Wang et al. [28] reported that two different metabolic pathways, i.e., heterotrophic and autotrophic growth of algae under different culture conditions. Green algae can perform heterotrophic growth besides the common autotrophic one of using CO2 as the sole carbon source [40]. The organic substances may play as an essential organic nutrient for microalgae growth or act as an accessory growth factor. In green algae Chlorella, heterotrophic growth may occur in a much faster way by directly incorporating organic substrate in the oxidative assimilation process for storage material production [28], which is the reason why COD and BOD5 concentration decreased after algal cultivation. Our results were also in line with the observations of Shen et al. [35] that green microalgae were able to utilize organic carbon for their metabolisms and assimilate organic compounds as a carbon source [41]. These results suggested that the wastewater could be used to provide sufficient nourishment to the algal cell for the metabolism process [42].The microalgal-bacteria or fungi flocculation and its application in wastewater treatment have been investigated [13–15, 19, 20, 38], but little information is known about the autoflocculation of green algae in wastewater treatment. In this study, AFL occurred when the growth of the microalgae in the fertilizer plant wastewater. The flocculation was exceptionally high in the treatment with 40 and 60 mg/L of microalgae biomass. Nguyen et al. [38] observed that the AFL occurs when introducing the microgreen algae C. vulgaris in seafood wastewater after 8 days. AFL indicates the cell aggregation and adhesion of cells to each other in liquid culture. AFL can occur naturally in certain microalgae to response to some environmental stress such as changes in nutrients, pH, dissolved oxygen (DO), and amount of calcium and magnesium ions in the culture mediums [14]. It is reported that AFL was associated with increased pH due to the depletion of CO2 concentration due to photosynthesis compared with precipitation of phosphate, magnesium, calcium, and carbonate salts with algal cells [13, 33].In these treatments, the removal rates of nutrients, as well as COD and BOD5, were relatively higher than other treatments, indicating that the AFL enhances the removal efficiencies. At the end of treatment, the two treatments with the most senior flocculation activities produced the most top elimination of nutrients, as well as COD and BOD5. Similarly, higher removal percentages of nitrate, phosphates, and COD were reported to associate with bioflocculation process of microalgae [13, 18, 19, 38]. In general, algal cell density in flocculation forms is always higher than free forms [20, 21]. The high removal efficiency in wastewater treatment with AFL could be attributed to the availability of sufficient oxygen for further mineralization of organic carbon and nutrients because of the high concentration of microalga cells in flocculation formation. In addition, the growth and nutrient removal efficiency may depend on different mixed wavelength ratios. Zhao et al. [9] reported that S. obliquus and C. Vulgaris efficiently removed COD and TP from biogas slurry at a red : blue ratio of 5 : 5 but S. obliquus exhibited high N removal efficiency at a red : blue ratio of 7 : 3. Our results agree with reports by Tang et al. [17] who reported more nutrients, as well as COD and BOD5 were removed in the treatments with the occurrence of flocculation of C. vulgaris compared with the treatment with only free cell form, indicating the enhancement of flocculation in pollutant removal. These results are also in accordance with the study conducted by Nguyen et al. [13] who reported that TSS removal efficiencies of treatment with no flocculation occurrence (20.6 ± 10.5%) were obviously lower than those with the clear formation of flocculation (90.0–95.0%).


## 3.1. Characteristics of Wastewater

The wastewater used for the experiment was analyzed for evaluating physico-chemical characteristics. The physico-chemical parameters of the wastewater, including pH, temperature, main nutrient species, as well as BOD5 and COD were presented in Table 1. The wastewater effluent collected from the Phu My Fertilizer Plant contained large amounts of nitrogen (47.3 ± 5.9 mg/L) in the form of ammonium (NH4+) and nitrate (NO3−) with small amounts of phosphate (PO43−) (0.9 ± 0.28 mg/L). Besides, the initial pH of the wastewater effluent was almost constant at pH 6.8. Ammonium is among the most common chemical forms of nitrogen that can be readily absorbed by most microalga species [26]. The concentration of phosphorus was also found sufficient to support algal growth. In this respect, the effluent collected from the Phu My Fertilizer Wastewater Treatment Plant could be used as a cheap source of nutrients for microalgal cultivation. The characterized of the raw wastewater was noted to be favorable for microalgae growth. A ratio of COD/TN/TP, i.e., 180/47/2, found with this wastewater, is suitable for nutrient removal with microalgae. The BOD5/TP, BOD5/PO43−-, and PO43−/TP ratios were found to be reasonably high (Table 1). The optimal inorganic N/P ratio for freshwater algae growth was suggested to be in the range of 6.8–10 [27, 28]. In this study, the inorganic N/P ratio of the effluent was 21, much higher than the optimal ratio, indicating the wastewater as phosphorus limitation media.Table 1
The average composition of the wastewater (average ± SD of five samples).
Parameter
Unit
Value
pH
6.8 ± 0.5
Temperature
°C
29 ± 1.0
Dissolved oxygen (DO)
mg/L
4.7 ± 0.6
Ammonium (NH4+)
mg/L
26.5 ± 3.5
Nitrate (NO3−)
mg/L
11.3 ± 2.1
Phosphorus (PO43+)
mg/L
0.9 ± 0.28
Total nitrogen (TN)
mg/L
47.3 ± 5.9
Total phosphorus (TP)
mg/L
1.8 ± 0.27
Chemical oxygen demand (COD)
mg/L
180 ± 18
Biochemical oxygen demand (BOD5)
mg/L
87 ± 12
Inorganic N/P
21


## 3.2. Growth ofScenedesmus sp. in Wastewater

The green algaeScenedesmus sp. was cultivated in the wastewater for 10 days with different initial cell concentrations from 10 to 60 mg/L. The growth rate, Chl content, and flocculation activity were presented in Table 2. The microalgae grew well in the wastewater with the growth rate from 0.30 to 0.38/day. There was no significant difference in the growth rate as the initial microalgae concentration increased from 10 to 60 mg/L. In the present study, wastewater was used as a nutrient medium for the growth of microalgae, and the utilization of nutrients allows wastewater treatment. During the growth phase, microalgae consumed mineral nutrients and CO2 from wastewater to produce biomass and released O2 into the medium [29].Table 2
The growth rate, chlorophyll content, and flocculation activity.
Initial microalgae concentration (mg/L)
10 ± 0.9
20 ± 1.3
30 ± 1.6
40 ± 1.2
60 ± 1.5
Growth rate/day
0.3 ± 0.03
0.34 ± 0.02
0.36 ± 0.02
0.37 ± 0.03
0.38 ± 0.04
Chlorophyll (mg/L)
13.7 ± 1.8
14.5 ± 1.6
18.2 ± 1.9
19.4 ± 2.3
20.8 ± 2.5
Dry biomass (g/L)
30.5 ± 2.8
35.8 ± 3.3
42.1 ± 2.7
68.3 ± 3.6
70.2 ± 4.9
Flocculation activity (%)
14.2 ± 1.8
23.7 ± 4.3
41.6 ± 2.3
81.5 ± 5.7
88.3 ± 4.1Our results showed that flocculation activity increases with higher cell concentrations. Significant build up of flocculation activity (81.5 and 88.3%) was observed at the highest initial microalgae concentrations of 40 and 60 mg/L. Nguyen et al. [13] reported that the clear formation of flocculation occurred when Chlorella vulgaris in seafood wastewater with the initial concentration above 20 mg/L. Results of the present study are consistent with previous observations that higher initial biomass in the medium a better formation of flocculation because cell-cell encounters are more frequent, leading to better aggregation [30, 31]. Microalgal bioflocculation is an efficient low-cost technology for microalgal harvesting and wastewater treatment [14, 21, 32]. In general, the bioflocculation process is assisted with microorganisms (including bacteria, fungi, and yeasts) or their polymer substances [13–15]. Since no chemical is added in this process, the bio-flocculation has been considered as a sustainable and green technique for algal biomass harvesting [14, 15]. The formation of algal flocculation and its application in wastewater treatment has been reviewed in detail [14, 15, 18]. In the present study, autoflocculation occurred when cultured Scenedesmus sp. in the wastewater for 10 days. Microalgal autoflocculation was found to be associated with increase in culture pH levels, due to CO2 consumption by algal photosynthetic activity. Under these alkaline conditions, some metal ions precipitated together with the algal biomass [33]. Guo et al. [31] reported that cell wall-associated polysaccharides mediated self-flocculation of the microalga S. obliquus. Future study is needed in this area to understand the mechanism of self-flocculation of microalgal cells and increase application in wastewater treatment technology.


## 3.3. Removal of Nitrogen

Nutrient removal in different initial biomass (from 10 to 60 mg/L), including (NH4+, NO3−, PO43− and TP) during the experiment, are shown in Figure 2. The removal rate of NH4+ in the control (no microalgae) was 21.1%, and all treatment with Scenedemsus sp. achieved higher removal than in the control. The NH4+ and NO3− removal performance is shown in Figures 2(a) and 2(b) with the removal efficiencies from 71.7 to 92.8% and from 62.2 to 83.6%, respectively (Table 3). In general, the higher microalgal concentration resulted in higher removal efficiency of NH4+ and NO3−. This observation well agreed with previous studies that higher initial microalgae density enhanced nutrient uptake in different wastewater effluents [13, 34, 35]. Green algae can use a variety of nitrogen sources for growth, making it possible to use these algae for bioremediation to remove nitrogen from wastewater [26, 28]. Microalgae can convert different inorganic nitrogen forms from wastewater to organic nitrogen [15]. Previous studies have demonstrated that the major mechanisms of nitrogen removal in algae systems include nitrification or denitrification and biological uptake of nitrogen by dispersed biomass [34, 36].Figure 2
Changes of NH4+ (a), NO3− (b), PO43− (c), TP (d), COD (e), and BOD5 (f) concentrations in the treatment with different initial microalgae concentrations.
(a)
(b)
(c)
(d)
(e)
(f)Table 3
Flocculation activity and removal efficiency with different initial microalgae concentration.
Initial microalgae concentration
Flocculation activity (%)
Removal efficiency (%)
Ammonium
Nitrate
Phosphate
TP
COD
BOD5
Control
21.1 ± 1.4
−14.9 ± 3.3
17.5 ± 2.1
26.8 ± 2.7
28.1 ± 2.0
16.4 ± 1.1
10 mg/L
14.2 ± 1.8
71.7 ± 1.9
62.2 ± 2.8
94.7 ± 1.5
75.0 ± 3.6
73.5 ± 3.4
65.2 ± 1.4
20 mg/L
23.7 ± 4.3
74.1 ± 2.1
64.6 ± 3.0
94.5 ± 2.3
74.7 ± 1.9
78.4 ± 2.4
67.7 ± 1.8
30 mg/L
51.6 ± 2.3
77.9 ± 2.7
65.6 ± 3.1
96.9 ± 2.8
78.3 ± 2.2
79.5 ± 4.4
68.4 ± 3.0
40 mg/L
81.5 ± 5.7
92.3 ± 4.3
81.5 ± 3.6
94.4 ± 2.2
92.9 ± 1.9
90.4 ± 4.1
82.3 ± 4.1
60 mg/L
88.3 ± 4.1
92.8 ± 3.5
83.6 ± 4.5
97.0 ± 1.7
95.8 ± 2.8
92.6 ± 4.0
83.7 ± 2.3Nitrification was observed during the first four days of the experiment; the decrease in ammonium concentration was accompanied by nitrate formation that peaked at day fourth and then decreased (Figures2(a) and 2(b)). Although ammonium is the preferred nitrogen source for uptake, microalgae can consume nitrogen from a variety of nitrogen sources, including ammonium, nitrate, nitrite, and urea [26, 28, 36]. Since the removal efficiencies on nitrate are usually lower than those on ammonium, our results agree well with previous observations that green microalgae such as Chlorella and Scenedemus were the preference for ammonium to any other form of nitrogen present in wastewater [34, 37].


## 3.4. Removal of Phosphorus

The removal rate ofPO43− and TP were shown in Table 3 and Figures 2(c) and 2(d). The percentages of PO43− and TP removal for the control were only 17.5 and 26.8%, respectively. While in the treatment, this number ranged from 94.7% to 97.0% and from 75% to 95.8% for PO43− and TP, respectively. The removal efficiencies were not significant differences (P=0.227) as treating PO43− with different concentrations of algal biomass. However, more significant TP removal rates were found during the treatment of wastewater with higher initial algae concentration (40 and 60 mg/L), compared with lower algae concentrations (10, 20, and 30 mg/L). The removal rates of TP were a significant correlation with the flocculation activities.Removal ofPO43− up to 97% (Table 3) from wastewater treated with green algae Scenedesmus sp. was very effective. For all treatments, the concentration of PO43− decreased gradually during ten days of the experiment (Figure 2(c)). But for TP, high removal rates were only found in the treatments with 40 or 60 mg/L. The concentration of TP did not decrease significantly during the first two days of the experiment but rapidly reduced from day 2 to day 6 of the test (Figure 2(d)).Table3 shows the removal efficiency and flocculation activity at the end of the experiment. Compared with the control, the treatments with higher initial microalgae concentration had greater removal efficiencies and flocculation activities (Figure 3), showing a relationship between flocculation activity and removal efficiency. Previous studies have reported that the green algae C. vulgaris and S. obliquus could be used to remove PO43− from the difference of wastewaters [15, 34, 35, 37]. Other studies suggested that the immobilized or flocculated form of microalgae is more effective than free form for nutrient removal in wastewater treatment [13, 15, 35, 38]. Our results are consistent with Nguyen et al. [13] that bioflocculation formation of microalgae enhanced nutrient removal from wastewater effluent. Naturally, phosphate seems to be depleted from the medium through different mechanisms including adsorption onto the cells surface, assimilation by the algae biomass or chemical precipitation [17, 34]. Previous studies have demonstrated that assimilation into biomass and adsorption were the main biotic processes of elimination of phosphorus in microalgae [17, 34].Figure 3
Flocculation activities in the control (a) and treatment with different concentrations of microalgae: 10 mg/L (b), 20 mg/L (c), 30 mg/L (d), 40 mg/L (e), and 60 mg/L (f).
(a)
(b)
(c)
(d)
(e)
(f)


## 3.5. Removal of BOD5 and COD

The COD removal efficiencies varied a little among different initial microalgae concentrations (Figure2(e)). While removal rates of only 73.5%, 78.4% and 79.5% were achieved for 10 mg/L, 20 mg/L and 30 mg/L of microalgae concentration, respectively, removal rates for 40 mg/L and 60 mg/L are up to 90.4% and 92.6%, respectively (Table 3). The concentration of COD decreased gradually during the experiment course. The removal rates of BOD5 were almost the same trend with COD removal pattern and showed Figure 2(f). Higher removal rates were also found in the treatments with higher initial microalgae concentrations. There is a relationship between flocculation activity in the treatments with the removal efficiencies of COD and BOD5. Higher flocculation activity resulted in higher removal rates in all treatments. Nguyen et al. [38] investigated the ability to removal of COD and BOD5 in seafood wastewater; results indicated that the removal rates of COD and BOD5 were 88% and 81%, respectively, under sunlight mode and 81% and 74% under fluorescent illumination, respectively, as clear formation of flocculation was observed. Previous studies reported that the presence of microalgae in the cultivation medium had increased the consumption of organic as well as inorganic matters [11, 38, 39]. Besides, Wang et al. [28] reported that two different metabolic pathways, i.e., heterotrophic and autotrophic growth of algae under different culture conditions. Green algae can perform heterotrophic growth besides the common autotrophic one of using CO2 as the sole carbon source [40]. The organic substances may play as an essential organic nutrient for microalgae growth or act as an accessory growth factor. In green algae Chlorella, heterotrophic growth may occur in a much faster way by directly incorporating organic substrate in the oxidative assimilation process for storage material production [28], which is the reason why COD and BOD5 concentration decreased after algal cultivation. Our results were also in line with the observations of Shen et al. [35] that green microalgae were able to utilize organic carbon for their metabolisms and assimilate organic compounds as a carbon source [41]. These results suggested that the wastewater could be used to provide sufficient nourishment to the algal cell for the metabolism process [42].The microalgal-bacteria or fungi flocculation and its application in wastewater treatment have been investigated [13–15, 19, 20, 38], but little information is known about the autoflocculation of green algae in wastewater treatment. In this study, AFL occurred when the growth of the microalgae in the fertilizer plant wastewater. The flocculation was exceptionally high in the treatment with 40 and 60 mg/L of microalgae biomass. Nguyen et al. [38] observed that the AFL occurs when introducing the microgreen algae C. vulgaris in seafood wastewater after 8 days. AFL indicates the cell aggregation and adhesion of cells to each other in liquid culture. AFL can occur naturally in certain microalgae to response to some environmental stress such as changes in nutrients, pH, dissolved oxygen (DO), and amount of calcium and magnesium ions in the culture mediums [14]. It is reported that AFL was associated with increased pH due to the depletion of CO2 concentration due to photosynthesis compared with precipitation of phosphate, magnesium, calcium, and carbonate salts with algal cells [13, 33].In these treatments, the removal rates of nutrients, as well as COD and BOD5, were relatively higher than other treatments, indicating that the AFL enhances the removal efficiencies. At the end of treatment, the two treatments with the most senior flocculation activities produced the most top elimination of nutrients, as well as COD and BOD5. Similarly, higher removal percentages of nitrate, phosphates, and COD were reported to associate with bioflocculation process of microalgae [13, 18, 19, 38]. In general, algal cell density in flocculation forms is always higher than free forms [20, 21]. The high removal efficiency in wastewater treatment with AFL could be attributed to the availability of sufficient oxygen for further mineralization of organic carbon and nutrients because of the high concentration of microalga cells in flocculation formation. In addition, the growth and nutrient removal efficiency may depend on different mixed wavelength ratios. Zhao et al. [9] reported that S. obliquus and C. Vulgaris efficiently removed COD and TP from biogas slurry at a red : blue ratio of 5 : 5 but S. obliquus exhibited high N removal efficiency at a red : blue ratio of 7 : 3. Our results agree with reports by Tang et al. [17] who reported more nutrients, as well as COD and BOD5 were removed in the treatments with the occurrence of flocculation of C. vulgaris compared with the treatment with only free cell form, indicating the enhancement of flocculation in pollutant removal. These results are also in accordance with the study conducted by Nguyen et al. [13] who reported that TSS removal efficiencies of treatment with no flocculation occurrence (20.6 ± 10.5%) were obviously lower than those with the clear formation of flocculation (90.0–95.0%).


## 4. Conclusion

The present results demonstrated the use of wastewater from a fertilizer plant in the cultivation and harvesting ofScenedesmus sp. Our results indicated that wastewater from fertilizer plants could be used as a cost-effective growth medium for algal biomass. The nutrient removal efficiency by Scenedesmus sp. isolated from the wastewater evidenced that microalgae are potential in removing nitrogen and phosphorous as well as COD and BOD5 from a highly concentrated nutrient-rich such as fertilizer plant wastewater. The present study highlights the autoflocculation of microalgae could be used as a more practical alternative eco-friendly approach for wastewater treatment using microalgae to eliminate eutrophication.



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*Source: 8094272-2020-02-14.xml*