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Article

Effects of Recirculating Aquaculture System Wastewater on Anammox Performance and Community Structure

by
Jonathan A. C. Roques
1,2,†,
Federico Micolucci
1,2,†,
Suguru Hosokawa
3,
Kristina Sundell
1,2 and
Tomonori Kindaichi
3,*
1
Department of Biological and Environmental Sciences, University of Gothenburg, P.O. Box 463, SE-405 30 Gothenburg, Sweden
2
Swedish Mariculture Research Center (SWEMARC), University of Gothenburg, P.O. Box 463, SE-405 30 Gothenburg, Sweden
3
Department of Civil and Environmental Engineering, Graduate School of Advanced Science and Engineering, Hiroshima University, 1-4-1 Kagamiyama, Higashihiroshima 739-8527, Japan
*
Author to whom correspondence should be addressed.
†
Contributed equally to the study.
Processes 2021, 9(7), 1183; https://doi.org/10.3390/pr9071183
Submission received: 14 June 2021 / Revised: 2 July 2021 / Accepted: 3 July 2021 / Published: 7 July 2021
(This article belongs to the Special Issue Anammox-Based Processes for Wastewater Treatment)
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Abstract

:
Recirculating aquaculture systems (RAS) are good candidates for the sustainable development of the aquaculture sector. A current limitation of RAS is the production and accumulation of nitrogenous waste, which could affect fish health. We investigated the potential of the anaerobic ammonia oxidation (anammox) process to treat marine wastewater from a cold-water RAS. We show that the marine anammox bacteria Candidatus Scalindua is a promising candidate. However, its activity was affected by unknown compounds in the RAS wastewater and/or the sub-optimum content of essential trace elements (TEs). Anammox activity dropped to 2% and 13% in NH4+ and NO2− removal, respectively, when NO3-rich RAS wastewater was used as a medium in the absence of TE supplementation. A TE supplementation was added to the RAS wastewater in a subsequent phase, and a recovery in anammox activity was shown (25% and 24% in NH4+ and NO2− removal, respectively). Future studies need to identify the unknown factor and determine the specific needs regarding TE for optimal RAS wastewater treatment by Candidatus Scalindua.

Graphical Abstract

1. Introduction

The world population is expected to reach 9.7 billion by 2050 [1]. Therefore, there is an urgent need to increase nutritious and sustainable food production [2]. There is a global consensus about the increasing importance of aquaculture as an essential source of food. Indeed, the aquaculture sector currently accounts for almost 50% of the global fish production for human consumption and is steadily growing [3]. However, the production methods’ intensification has led to environmental concerns regarding, e.g., eutrophication, caused by the leakage of nutrients to the environment, especially in open-water systems [4]. Closed containment systems such as recirculating aquaculture systems (RAS) allow for a high degree of water reuse as well as ensuring better control of the farming environment, resulting in reduced ecological impact [5,6,7]. RAS are therefore of interest to the development of sustainable aquaculture. In RAS, ammonium (NH4+) is oxidized into nitrate (NO3–) via nitrite (NO2–) by nitrifying bacteria in aerobic biofilm reactors [8]. NO3– can accumulate over time in an RAS and can reach concentrations of up to 100–1000 mg L−1 depending on the RAS design and management [9,10]. Over time, such levels may negatively affect fish health and welfare if not appropriately managed through denitrification or regular water exchanges [11,12]. Ambient levels below 10 mg NO3−-N L−1 (freshwater) and 20 mg NO3−-N L−1 (seawater) are recommended to avoid adverse effects in fish [11]. Specific denitrification compartments, where the biological conversion of NO3– to nitrogen gas (N2) occurs, are not always present in RAS, as denitrification is an inherently unstable process that can lead to the creation and accumulation of intermediate substances (e.g., NO2–, NO and N2O) that can be toxic to fish and harmful to the environment [13,14]. Consequently, most of the current RAS are partial RAS, only using nitrification steps and requiring >10% water exchange per day in order to avoid the accumulation of NO3–. This results in a relatively high use of water and the production of nitrate-rich wastewater. New water treatment solutions for increased re-circulation of the culture water will aid in developing RAS that are more sustainable and productive.
Anaerobic ammonia oxidation (anammox) is a microbial process that converts NH4+ and NO2– directly into N2 gas [15]. This process recently attracted attention as an energy-saving and highly efficient nitrogen removal technology in wastewater treatment plants [16,17] and is, thus, a promising candidate for the nitrogen removal process in RAS [18]. The presence of anammox bacteria has been detected in many freshwater and marine environments with limited oxygen availability [19]. The presence and subsequent activity of anammox bacteria have been detected in microbial biofilm from the denitrifying compartment in both freshwater and marine RAS [20,21,22,23]. In 2009, Tal and colleagues used anammox coupled with denitrification for the first time in a pilot warm-water RAS, achieving both a recirculation rate and animal survival of 99% [24].
A marine anammox bacterium named Candidatus Scalindua sp. (hereafter Ca. Scalindua) was successfully enriched from coastal surface sediment collected from Hiroshima Bay (Japan) [25,26]. Ca. Scalindua is a promising microbial component to mitigate environmental problems of aquaculture due to its high anammox activity under high salinity and low temperature conditions [27,28]. In addition, the anammox process avoids the microbial pathways through which toxic substances (e.g., N2O) are formed in aquaculture systems.
In the present study, we investigated the behavior of Ca. Scalindua in wastewater from a commercial, cold-water marine RAS (Table 1). A newly started Ca. Scalindua reactor was exposed to artificial seawater enriched with NH4+, NO2– and essential trace elements (TEs, including B, Co, Cu, Fe, Mn, Mo, Ni, Se and Zn) (control) and RAS wastewater in the absence and presence of TEs. The anammox performance (nitrogen loading and removal rates, NH4+ and NO2– removal efficiencies) was evaluated alongside changes in the microbial community composition under the different conditions. The aim of this first pilot experiment was to show the anammox bacteria response to RAS wastewater under controlled conditions (optimal pH, salinity, temperature, NH4+ and NO2– concentrations).

2. Materials and Methods

2.1. RAS Wastewater Collection and Characteristics

RAS wastewater (20 L, Table 1) was collected from Smögenlax Aquaculture AB, Kungshamn, Sweden, a pilot-scale research and development facility for the development of land-based seawater RAS at low temperatures, in June 2019 [29]. The water samples were stored in two 5-L and ten 10-L plastic containers, immediately frozen (−80 °C) and subsequently shipped to the Department of Civil and Environmental Engineering at Hiroshima University (Japan) and kept frozen until further use. The fish species in the RAS were rainbow trout, Oncorhynchus mykiss, with an average weight of 1.3 ± 0.3 kg and were kept at a density of 40 kg m−3 ([29] and Bengt Gunnarsson, personal communication).

2.2. Reactor Operation

Ca. Scalindua granules were harvested from an up-flow column anammox stock culture that has been operating with a continuous supply of inorganic nutrient media containing NH4+ (28 mg-N L−1) and NO2− (34 mg-N L−1) [30] for more than 10 years [26,31,32]. Biomass of 1 g (wet weight) was used as inoculum in a glass column reactor (Ø 30 mm; volume, 76 cm3; KF-30, AS ONE, Tokyo, Japan) with a nonwoven fabric sheet (Japan Vilene, Tokyo, Japan) as the biofilm carrier material (Figure 1).
The reactor was operated for 150 days in 5 different phases (Table 2). During Phase 1 (days 0–65) and Phase 5 (days 104–150), the reactor was fed with synthetic marine wastewater (SEALIFE, Marinetech, Tokyo, Japan) supplemented with nitrogen (NH4+ and NO2–) and nine TEs (B, Co, Cu, Fe, Mn, Mo, Ni, Se and Zn), as described by van de Graaf and colleagues (see Supplementary Material, Table S1 and [30]). During Phases 2–4 (days 65–104), the reactor was exposed to the RAS wastewater. The RAS wastewater characteristics were adjusted to match the standard medium for the optimal functioning and growth of Ca. Scalindua in laboratory conditions in terms of temperature (20 °C), salinity (26.2 ‰), NH4+ (28 mg-N L−1), NO2– (34 mg-N L−1) and inorganic carbon (KHCO3, 1000 mg L−1) [25,26,31]. Those parameters were maintained constantly throughout the different experimental phases. The initial hydraulic retention time (HRT) was 2.3 h. During Phases 1, 3 and 5, the wastewater was supplemented with a mix of TEs in order to determine the activity of Ca. Scalindua in the presence (Phases 1, 3 and 5) or absence (Phases 2 and 4) of TEs. This TE mix was developed when the first freshwater anammox species was enriched and is currently used as a standard in anammox cultures worldwide [30]. Each time, the influent was flushed with N2 gas for at least 30 min before adding the components to achieve a concentration of dissolved oxygen below 0.1 mg L−1. The influents were continuously introduced into the reactor using a peristaltic pump (Masterflex L/S Economy Drive, Cole-Parmer Instruments, Vernon Hills, IL, USA).

2.3. Analytical Methods

The total nitrogen (TN) loading and removal rates were calculated based on the concentrations of NH4+, NO2− and NO3− as well as the HRT. Salinity was determined using a conductivity meter (LAQUAact ES-71, Horiba, Kyoto, Japan). Analyses of total suspended solids (TSS) were carried out in accordance with the Standard Methods [33]. The pH was measured using a pH meter (F-52, HORIBA, Kyoto, Japan). Total organic carbon (TOC) was measured using a TOC analyzer (Shimadzu TOC-VCSH, Kyoto, Japan, with a detection limit of 50 µg L−1) as described previously [34].
The NH4+ concentration was determined using Nessler’s method with a UV–visible spectrophotometer (DR-2800, Hach-Lange, Loveland, CO, USA) according to the manufacturer’s recommendations (Hach-Lange, Loveland, USA, Method 8038, with a detection limit of 0.02 mg-N L−1). The concentrations of NO2− and NO3– were determined using ion-exchange chromatography (HPLC 20A; Shimadzu, Kyoto, Japan) with a Shodex Asahipak NH2P-50 4D anion column (Showa Denko, Tokyo, Japan) and a UV–VIS detector (SPD-20AV, Shimadzu) after filtration of samples through 0.2-micrometer pore-size PTFE membranes (Advantec, Tokyo, Japan) [17]. The detection limit for both NO2− and NO3− was 0.5 mg-N L−1.

2.4. Microbial Community Analysis

In order to determine the potential changes in the microbial community composition during the different phases, biomass samples for amplicon sequencing were collected from the reactor at days 0, 78 and 104. DNA was extracted using a FastDNA SPIN kit for soil (MP Biomedicals, Santa Ana, USA). PCR amplification of the bacterial 16S rRNA gene was performed with a primer set for amplification of the V3-V4 region as follows: 341F (5′-CCTACGGGNGGCWGCAG-3′) and 805R (5′-GGACTACHVGGGTATCTAATCC-3′). The details of the PCR amplification were described previously [34]. PCR products were purified using the Agencourt AMPure XP system (Beckman Coulter, Brea, CA, USA) according to the manufacturer’s instructions. Purified DNA was sequenced using a MiSeq platform with a MiSeq reagent kit (v.3; Illumina, San Diego, CA, USA).
Obtained sequences were trimmed and assembled as described previously [35]. Sequence data were analyzed using QIIME 2 Core 2020.2 distribution [36]. Operational taxonomic units (OTUs) were assigned with the SILVA 132 database [37]. OTUs that accounted for more than 0.5% of the total reads were used for bar plots. The sequence data in the present study were deposited in the DNA Data Bank of Japan (DDBJ) database under the DDBJ/EMBL/GenBank accession number DRA010899.

2.5. Fluorescence In Situ Hybridization (FISH)

Biomass samples were collected from the up-flow column reactor at days 0, 78 and 104. Sample fixation and the FISH procedure were described previously [25]. The probes used in this study were as follows: a mixture of EUB338, II, III and IV probes labeled with Alexa Fluor 488 specific for all bacteria [38,39] and BS820 probes labeled with Alexa Fluor 555 specific for Ca. Scalindua [39]. Hybridized samples were observed with an Axiomager M1 epifluorescence microscope with a 100-watt HBO lamp. Images were obtained using an AxioCam MRm version 3 FireWiremonocrome camera and AxioVision software, version 4.5 (Carl Zeiss, Oberkochen, Germany).

3. Results

3.1. Reactor Performance

During Phase 1 (synthetic wastewater and TEs), the TN removal rate gradually increased while maintaining a constant TN loading rate (Figure 2). Once the reactor reached a stable state (days 45–60), the average TN loading and removal rate were 0.72 ± 0.03 and 0.61 ± 0.03 g-TN L−1 day−1, respectively (HRT 2.3 h). At the end of Phase 1, the removal efficiency had reached 93% for NH4+ and 100% for NO2−. The stoichiometry ratio of NO2−/NH4+ and NO3−/NH4+ was 1.56 and −0.16, respectively. All these parameters suggested a successful establishment of the anammox process in the reactor [31,40,41,42].
During Phase 2, the use of RAS wastewater instead of artificial seawater without TEs resulted in a drastic decrease in the TN removal rate. The average TN loading rate during this phase was higher than that in Phase 1 (1.02 ± 0.06 g-TN L−1 day−1) due to the presence of higher NO3− in RAS wastewater (Table 1). At the end of Phase 2, the removal efficiencies of NH4+ and NO2− were only 2% and 13%, respectively (HRT 2.4 h), and the TN removal rate was 0.09 g-TN L−1 day−1. These results clearly indicate that there was a negative effect of the RAS wastewater and/or the absence of TEs on the activity of anammox bacteria.
During Phase 3, RAS wastewater was used in combination with TEs, and the HRT was increased to 4.8 h (i.e., decrease in TN loading rate). The NH4+ and NO2− removal efficiencies slightly recovered during this phase, suggesting that the RAS wastewater was lacking some key TEs and/or the TN loading rate was too high for maintaining the anammox activity from Phase 2. On days 91–94, the removal efficiency of NO2− fell to almost zero due to accidental temporary oxygen contamination, which was fixed on day 94, prior to the start of the next phase. In order to investigate which factor(s) (TEs/TN loading rate) negatively affected the anammox activity during Phase 2, the TEs in the RAS wastewater were removed during Phase 4 while keeping the same TN loading rate as in Phase 3 to investigate the effect of TEs. The NH4+ and NO2− removal efficiencies were slightly improved during this phase (25.5 ± 5.4% and 24.6 ± 4.5% on average, respectively), suggesting that TE supplementation was not necessary for a short period under the Phase 4 condition. However, as TEs are strongly related to the cell biosynthesis and cell division in anammox bacteria, the impact of TE depletion and the specific TE requirements of Ca. Scalindua culture need to be investigated for at least two weeks, which is the generation time of Ca. Scalindua [25]. On the other hand, the increase in TN loading rate was due to the high NO3− concentration contained in the RAS wastewater. Since the tolerance to NO3− of Ca. Scalindua is unclear, it also needs to be investigated in the future.
During Phase 5, artificial seawater was used with TEs and 5.1 h of HRT. The decrease in TN loading rate was due to the lower NO3− concentration in the artificial seawater (0.8 mg-N L−1) compared to the RAS wastewater; the NO3− concentration in the RAS wastewater was higher (29.22 mg-N L−1, Table 1) due to the absence of a denitrification compartment in the Swedish farm. The NH4+ and NO2− removal efficiencies in Phase 5 were at similar levels as in Phase 1 within 8 days of operation. All these observations during the different phases of operation suggest that the normal anammox activity was probably affected by the presence of unknown compounds (e.g., presence of other organic and inorganic residues from feces and uneaten feed) in the RAS wastewater.

3.2. Microbial Community Analysis and FISH

A total of 27,115, 21,327 and 39,312 non-chimeric reads and 95, 131 and 138 operational taxonomic units (OTUs) were obtained on days 0, 78 and 104, respectively. In this study, OTUs that accounted for more than 0.5% of the total reads were used for the analysis, and OTUs accounting for less than 0.5% of the total reads were grouped as “Others” (Figure 3). Ca. Scalindua was identified as the most abundant species in the reactor. Interestingly, the relative abundances of Ca. Scalindua did not change over time (29.6% in the inoculum to 27.9% on day 104), even during the phase with RAS wastewater.
This stable population of Ca. Scalindua during the experiment was also supported by FISH observations (Figure 4). Therefore, the decrease in the TN removal rate was probably not caused by a decrease in anammox bacterial population abundance but rather by a decrease in the anammox activity of the Ca. Scalindua present.

4. Discussion

4.1. Reactor Performance

The observed decrease in anammox activity (Figure 2) could be due to unknown compounds present in the RAS wastewater or the imbalance of certain TEs in the wastewater. Previous and current anammox bacteria cultivations worldwide, including marine species, have been and are being performed using a synthetic feed containing nine different TEs. This cultivation protocol was developed over 25 years ago when the first freshwater anammox species was enriched [30]. Different species of anammox bacteria may have different TE requirements; in particular, marine anammox bacteria such as Ca. Scalindua may have different requirements than freshwater anammox species do [43,44]. Unfortunately, we were not able to measure TEs in the pure RAS wastewater, nor in the supplemented RAS wastewater in this study. However, it is known that some of the TEs are already present in seawater or artificial sea salt (Supplementary Material, Table S1). With the exception of B (1580 times higher), all of the other TEs were present, but at a lower (20–270 times) concentration in the synthetic salt used to supplement the RAS wastewater (SEALIFE) compared with the TE mix. Therefore, some key TEs for the normal functioning of anammox could be present in too low or too high concentrations, while others could be present in sufficient concentrations in RAS wastewater and need to be further investigated.
TEs are essential for anammox metabolism and growth. For instance, Mn is an important element for the functioning of the superoxide dismutase enzyme [45]. In addition, Mn and Fe participate in the metabolism and proliferation of anammox bacteria through the synthesis of Haem-C [46]. Nitrogen removal efficiency has been increased with Fe (0.08 mmol L−1; ca 4.47 mg L−1) and Mn (0.05 mmol L−1; ca 2.75 mg L−1) supplementation [46]. In another study, short-term exposure to Mn (2 mg L−1), Zn (2 mg L−1) and Cu (0.5 mg L−1) significantly improved the nitrogen removal rate of anammox reactors, while long-term exposure to those TE concentrations altered the microbial community structure of the anammox sludge [44]. Furthermore, too high concentrations of TEs can also negatively impact the anammox process. For instance, short-term IC50 values for Cu in freshwater anammox culture were found to be between 1.9 [47] and 12.9 mg L−1 [48]. For marine anammox species, studies on specific TE requirements are still scarce. Li and colleagues recently observed optimal ammonium removal efficiencies with 0.05 mmol L−1 (2.75 mg L−1) Mn and 0.025 mmol L−1 (1.47 mg L−1) Ni [49]. It is, therefore, paramount that future studies investigate the specific TE requirement of the marine anammox species Ca. Scalindua.
If we analyze other possible causes of the reduction in bacterial removal activity such as NO2−, we can ascertain that the NO2− concentrations in the effluent were between 0.0 and 35.4 mg-N L−1 depending on the phase. Awata and colleagues reported that the tolerance of NO2− for Ca. Scalindua was 7.5 mmol L−1 (=105 mg-N L−1) [25]. Therefore, 35.4 mg-N L−1 of NO2− accumulation can be excluded as a negative metabolic effect for the anammox activity.
Regarding the anammox stoichiometry, the ratios of NO2−/NH4+ and NO3−/NH4+ were 1.56 and −0.16, respectively, at the end of Phase 1, indicating similar anammox stoichiometry as that found in other marine anammox cultures [31]. During Phase 2, the stoichiometric ratio of NO2−/NH4+ was slightly over 2. However, these values were not stable and not reliable, as in fact, the ratio of NO2−/NH4+ depends on the NH4+ concentration, and the NH4+ removal efficiency was less than 10% during this phase.
The consumption of NO2− and NO3− is important for assessing eventual heterotrophic denitrification. As we observed no difference in the consumption of both, we concluded that there was no occurrence of heterotrophic denitrification. This was further confirmed by the low and stable population of heterotrophic denitrifying bacteria in the microbial community.

4.2. Microbial Community

FISH and the microbiological analysis testified a stable population of Ca. Scalindua during the experiment, noting that the decrease in the TN removal rate was probably not caused by a decrease in anammox bacterial population abundance but rather by a decrease in the anammox activity of the Ca. Scalindua present.
The relative abundances of bacterial phyla in the three biomass samples showed an increase in Actinomarinales (Actinobacteria), OC31 (Bacteroidetes), Balneolaceae (Bacteroidetes), Anaerolineaceae (Chloroflexi) and Rhodobacteraceae (Alphaproteobacteria), whereas OM190 (Planctomycetes) and Ulvibacter (Bacteroidetes) were decreased over the experimental period (Figure 3). Changes in the bacterial communities could be due to the presence of high protein concentrations or the presence of other organic and inorganic residues from feces and uneaten feed in the RAS wastewater (Phases 2, 3 and 4). Previous studies on organic-matter-rich synthetic wastewater and animal manure have proven to have adverse effects on anammox bacteria in favor of anaerobic denitrifying bacteria [50,51,52]. In addition to reduced anammox activity, organic-rich livestock manure can impact the microbial community structure and the spatial distribution in the outer layer of the anammox granules, with an increased density of co-existing heterotrophic bacteria [53]. Such bacteria are successful competitors and may thrive with the excess of organic matter. For example, Actinomarinales with opportunistic copiotrophic lifestyles may experience the presence of particulate organic matter as an advantageous micro-heterogeneity [54]. Chloroflexi can fermentatively utilize sugars and protein compounds [55], and Bacteroidetes are polysaccharide-degrading bacteria, highly successful competitors in gut ecosystems [56]. OM190 and Ulvibacter are both strictly aerobic [57,58]. Their presence at a relatively high proportion in the inoculum (14% and 21%, respectively) is probably due to the exposure of the biomass to aerobic conditions while setting up the reactor, while their decline in proportion with time could be attributed to the re-establishment of anaerobic conditions.

5. Conclusions

The present study demonstrates that Ca. Scalindua can potentially be used to treat wastewater from RAS. However, the activity of Ca. Scalindua rather than its relative abundance was affected by unknown compounds in the RAS wastewater and/or an imbalance in certain TEs. In this study, a much higher concentration of NO3– was present in the RAS wastewater due an efficient but sole nitrification in the RAS system. Further studies need to determine the effect of nitrate on the kinetic activity of nitrogen removal by anammox organisms. Anammox had the ability to resume its activity with high removal efficiencies once the synthetic medium was reintroduced. This leads us to understand that there is a reduction potential even with the use of RAS wastewater, but it is necessary to understand what the correct acclimatization for the organisms is and which elements cause a loss in removal efficiency in order to understand how these factors can be mitigated to improve the removal activity of these bacteria. Future studies also need to address specifically which concentrations of TEs are necessary for maintaining the anammox activity and/or growth of Ca. Scalindua to apply for RAS wastewater treatment.

Supplementary Materials

The following are available online at https://www.mdpi.com/article/10.3390/pr9071183/s1. Table S1: Comparison of TE concentrations.

Author Contributions

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

Funding

This research was conducted within the frame of the MIRAI project and was partly supported by the Helge Axelsson Johnsons foundation, Stockholm, Sweden (F19-0425 and F20-0272); the Wilhelm and Martina Lundgrens foundation, Gothenburg, Sweden (2020-3431); STINT, Stockholm, Sweden (initiation grant for international collaboration, IB2019-8110); JSPS KAKENHI Grant Number JP20KK0244, Japan; and the JSPS Bilateral Program, Grant number JPJSBP120219926.

Institutional Review Board Statement

Not applicable.

Informed Consent Statement

Not applicable.

Data Availability Statement

The sequence data in the present study were deposited in the DNA Data Bank of Japan (DDBJ) database under the DDBJ/EMBL/GenBank accession number DRA010899.

Acknowledgments

The RAS wastewater was obtained from Smögenlax Aquaculture AB, Kungshamn, Sweden. We are grateful to Miyuki Kuribara for proofreading and copy-editing this manuscript.

Conflicts of Interest

The authors declare no conflict of interest.

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Processes 09 01183 g001 550
Figure 1. Schematic drawing of the up-flow column reactor.
Figure 1. Schematic drawing of the up-flow column reactor.
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Figure 2. Anammox performance in the reactor. (A) Nitrogen loading and removal rates (filled and open circles). (B) NH4+ and NO2− removal efficiencies (filled diamonds and open triangles). Dotted lines indicate changes in the operational phase (artificial seawater or RAS wastewater, the presence of TEs). Purple arrows indicate biomass sampling on days 0, 78 and 104. RAS, recirculating aquaculture system wastewater.
Figure 2. Anammox performance in the reactor. (A) Nitrogen loading and removal rates (filled and open circles). (B) NH4+ and NO2− removal efficiencies (filled diamonds and open triangles). Dotted lines indicate changes in the operational phase (artificial seawater or RAS wastewater, the presence of TEs). Purple arrows indicate biomass sampling on days 0, 78 and 104. RAS, recirculating aquaculture system wastewater.
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Figure 3. Microbial community composition after 0, 78 and 104 days of operation, based on 16S rRNA gene amplicon sequencing. Red percentages correspond to the relative abundance of marine anammox bacteria.
Figure 3. Microbial community composition after 0, 78 and 104 days of operation, based on 16S rRNA gene amplicon sequencing. Red percentages correspond to the relative abundance of marine anammox bacteria.
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Figure 4. FISH micrographs of biomass collected from the column reactor at days 0 (A), 78 (B) and 104 (C). FISH was performed with Alexa-Fluor-488-labeled EUB338mix probes (green) for all bacteria and Alexa-Fluor-555-labeled BS820 probes (red) for Ca. Scalindua. Ca. Scalindua appears yellow and other bacteria appear green. Scale bars represent 10 μm.
Figure 4. FISH micrographs of biomass collected from the column reactor at days 0 (A), 78 (B) and 104 (C). FISH was performed with Alexa-Fluor-488-labeled EUB338mix probes (green) for all bacteria and Alexa-Fluor-555-labeled BS820 probes (red) for Ca. Scalindua. Ca. Scalindua appears yellow and other bacteria appear green. Scale bars represent 10 μm.
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Table
Table 1. Physicochemical characteristics of the RAS wastewater.
Table 1. Physicochemical characteristics of the RAS wastewater.
ParameterSalinity
(‰)		NH4+
(mg-N L−1)		NO2−
(mg-N L−1)		NO3−
(mg-N L−1)		pHTSS
(mg L−1)		TOC
(mg-C L−1)
Value14.50.250.01729.227.570.56.8
Table
Table 2. Operational conditions of the column reactor.
Table 2. Operational conditions of the column reactor.
PhasePeriodAS/RAS 1TEs 2HRTNLRpH *Salinity (‰) *
(d)(h) 3,*(g-TN L−1 day−1) 4,*InfluentEffluentInfluentEffluent
10–65AS+2.30.72 ± 0.037.62 ± 0.167.82 ± 0.1425.5 ± 2.925.6 ± 3.1
265–77RAS−2.41.02 ± 0.067.80 ± 0.247.95 ± 0.2026.6 ± 0.126.2 ± 1.0
377–96RAS+4.80.48 ± 0.037.57 ± 0.167.78 ± 0.0926.1 ± 0.626.2 ± 0.8
496–104RAS−5.10.45 ± 0.017.47 ± 0.067.67 ± 0.1526.2 ± 0.726.3 ± 0.4
5104–150AS+5.10.33 ± 0.027.66 ± 0.197.91 ± 0.1227.2 ± 0.627.2 ± 0.8
1 AS, Artificial seawater; RAS, Recirculating aquaculture system wastewater. 2 TEs, Trace element mix, reported by van de Graaf and colleagues [30]; see also Supplementary Material, Table S1. 3 HRT, Hydraulic retention time. 4 NLR, Nitrogen loading rate. * Values show the average and standard deviation during the different phases, measured 2–4 times per week (Phases 1 and 5) and 3–5 times per week (Phases 2–4).
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Roques, J.A.C.; Micolucci, F.; Hosokawa, S.; Sundell, K.; Kindaichi, T. Effects of Recirculating Aquaculture System Wastewater on Anammox Performance and Community Structure. Processes 2021, 9, 1183. https://doi.org/10.3390/pr9071183

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Roques JAC, Micolucci F, Hosokawa S, Sundell K, Kindaichi T. Effects of Recirculating Aquaculture System Wastewater on Anammox Performance and Community Structure. Processes. 2021; 9(7):1183. https://doi.org/10.3390/pr9071183

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Roques, Jonathan A. C., Federico Micolucci, Suguru Hosokawa, Kristina Sundell, and Tomonori Kindaichi. 2021. "Effects of Recirculating Aquaculture System Wastewater on Anammox Performance and Community Structure" Processes 9, no. 7: 1183. https://doi.org/10.3390/pr9071183

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