Resumen
Wastewater reuse for irrigation has become an important practice in many countries in the context of global water scarcity. However, knowledge about the potential soil impact of reusing treated fish-processing (TFP) effluents for irrigation is still limited. The aim of this study was to investigate the response of the soil prokaryotic community in general, and the nitrifying taxa in particular, to TFP-effluent irrigation. We analyzed the impacts of irrigation with two effluent dilutions (EF1 and EF2, with electrical conductivities of 2.7 and 6 mS cm−1, respectively) or water (W) as a control on soil chemical properties, dehydrogenase and nitrifying activities, amoA gene abundances of ammonia-oxidizing bacteria (AOB) and archaea (AOA), and soil prokaryotic community structure and diversity. At the end of the irrigation experiment, soil ammonium, nitrate plus nitrite, dehydrogenase and nitrifying activities, soil electrical conductivity (EC), and sodium adsorption ratio (SAR) were significantly higher in TFP-irrigated treatments than in water irrigated controls. Prokaryotic richness and diversity indices followed the pattern W > EF1 > EF2, and negatively correlated with soil EC, SAR, ammonium, nitrate plus nitrite, and total N concentrations. In particular, EF2-irrigation stimulated soil copiotrophic bacteria (e.g. Proteobacteria and Bacteroidetes) to the detriment of oligotrophic members such as Acidobacteria. TFP-effluent irrigation also influenced the relative abundance of the amoA gene of AOB but not that of AOA; and the composition of nitrifying taxa, by inducing a significant increase in OTUs whose closest cultured matches were ‘Candidatus Nitrosocosmicus franklandus’ and Nitrosospira briensis Nsp10. Overall, irrigation with the more diluted effluent (classified as slight to moderate degree of restriction by local regulations) induced a reduction of soil prokaryotic diversity, whereas the less diluted effluent (severe irrigation restriction) promoted the greatest changes in the prokaryotic community due to the increase in soil salinity and N content.
Métodos
2.1. Sampling and analysis of TFP-effluent: Effluent was collected from a fish-processing wastewater treatment plant. Aliquots of the undiluted effluent were used to determine: electrical conductivity (EC), Total Dissolved Solids (TDS), pH, Sodium Adsorption Ratio (SAR), Chemical Oxygen Demand (COD), 5-Day Biochemical Oxygen Demand (BOD5), Total Suspended Solids, oils and greases, ammonium and nitrate plus nitrite concentrations. 2.2. Microcosm study: Soil samples were collected from a field characteristic of the Patagonian Monte Shrubland. The soil samples were collected under randomly selected plant-covered patches. Samples were immediately transported to the laboratory (4 °C), pooled, homogenized, and sieved through a 2 mm mesh for further use. Soil moisture was gravimetrically determined (105 °C, 48 h) and all results were expressed on the basis of dry soil weight. Soil EC, pH, SAR, total, organic and inorganic soil carbon (C), total soil nitrogen (N), ammonium, nitrate and nitrite concentrations, and dehydrogenase activity were determined to characterize soil samples. Microcosms contained 500 g of soil and 2 g of plant litter. All the microcosm pots were randomly placed inside a dark chamber and incubated at 20 °C for 16 weeks. Soil water content was maintained at 15% (w/w) throughout the experimental period by weighing the microcosms every two days and compensating for the weight loss by the following irrigation treatments: TFP-effluent diluted to 2.7 mS cm−1 (EF1), TFP-effluent diluted to 6 mS cm−1 (EF2), and distilled water (W; control treatment). 2.3. Soil DNA extraction and microbiological analysis: Total DNA from soil samples (ca. 0.5 g) corresponding to the beginning of the experiment (time 0) and to the microcosms collected at the end of the incubation period (week 16) was extracted using the FastDNA® SPIN Kit for Soil (MP Biomedicals, USA), following the manufacturer's instructions. 2.3.1. amoA gene abundances: The number of copies of AOA and AOB amoA genes was quantified using a 7500 Real-Time PCR System (Applied Biosystems, USA), following the amplification protocol described in Marcos et al. (2021). 2.3.2. High-throughput sequencing and analysis of 16S rRNA amplicons: The universal barcoded primers 515F/806R were used for PCR amplification of the hypervariable V4 region of the bacterial and archaeal 16S rRNA genes, as described by Vallejos et al. (2020). PCR products were used for Illumina MiSeq high-throughput sequencing (Illumina, 2021). Sequences were processed using the bioinformatic software mothur v.1.39.5, following the MiSeq SOP protocol (Schloss et al., 2009). For sequence classification, SILVA SSU database v132 was employed (Quast et al., 2013). Sequences were clustered into operational taxonomic units (OTUs) at a 3% dissimilarity level. Raw sequences of bacterial and archaeal 16S rRNA genes were deposited in the NCBI Sequence Read Archive (SRA) database, under project accession PRJNA562709.