The rational utilisation of sludge as organic matter application into the soil permits enrichment in nutrients such as nitrogen and phosphorus. As dairy sewage sludge contains large amounts of organic matter and minerals, utilisation of such sludge in agriculture appears to be a noteworthy proposal. However, such waste can also be a source of toxic substances, heavy metals, inhibitors, xenobiotics and potentially pathogenic microorganisms. Therefore, it is so important to monitor its microbiological and biochemical properties in aspect of the safety for human health, natural environment preservation and a suitable level of agricultural production maintenance. The objective of study was the estimation of selected microbiological, biochemical and chemical properties of activated sludge (AS) and waste activated sludge (WAS) originating from the dairy sewage treatment plant. Nitrification and ammonification rates, respiratory, dehydrogenases, acid phosphatase, alkaline phosphatase, protease and urease activities were at significantly higher levels in the WAS than in the AS. The pH value of the AS and WAS oscillated within the range of neutral reaction.
The problem of proper utilisation of sewage sludge has been systematically growing over the recent years. It is mainly related to the high water content with the sanitary hazard that it constitutes. Steroid estrogens were found at high concentrations in untreated dairy shed effluents (Gadd et al. 2010). Also, the operating cost associated with the sludge handling is often reported to be a significant part of the overall operating cost in the wastewater treatment plant (Teh et al. 2016). Therefore, every sewage treatment plant should have a program of rational utilisation of sewage sludge based on conducting continuous monitoring of its physical, chemical and biological properties (Bieganowski et al. 2012; Singh and Agrawal 2008). The results of Tran et al. (2014) indicate that by using simple techniques, the long-term emission behaviour of residues submitted to mechanical–biological treatment can be quickly reduced to an acceptable level.
Wastes generated by the agricultural-food industry, including the dairy industry, are rich in high-protein organic matter and numerous valuable nutrients and constitute their high soil-forming and fertiliser potential. By applying composting or vermicomposting, the industrial sludge could be further improved on better quality and matured fertiliser (Lim et al. 2015, 2016). Natural utilisation of sewage sludge is proper from the ecological point of view and has a favourable effect on the reclamation of degraded soils. This approach of sludge utilisation affects positively the plant yields and reduces the use of mineral fertilisers—so it would be much more beneficial for the environment (Hussein et al. 2010; Jezierska-Tys et al. 2010; Oszust et al. 2015). An important factor that makes dairy sewage sludge applicable in agriculture is the fact that it abounds in such elements as nitrogen, magnesium, calcium and phosphorus. Also highly important is the fact that this kind of sludge has heavy metals concentration below normative standards, which makes them safe for the environment (Frąc et al. 2012; Mikosz 2015; Wyszkowska et al. 2008).
The sludge reprocessing to value-added products holds the future key to sustainable management and is one of the major areas of environmental protection. Biochar derived from waste biomass is now gaining much attention for its function as a biosorbent for environmental remediation (Xu et al. 2013). In this perspective, sludge can be also transformed, e.g., into biofertilisers. This application may change the soil microbial community composition (Mohapatra et al. 2016). However, field application of sludge-based organic fertilisers could be virtually neglected because of additional load of microorganism introduced into the soil with that kind of fertilisers. The field application of dairy sewage sludge should be expected to potentially cause epidemiological effect on plant health, while introducing harmful microorganisms. On the other hand, it may occur positively, increasing yields, since microorganisms, mainly bacteria and fungi, play an important role in making nutrients available to plants or negatively. There is a lack of information trends occurring microbial communities in the soil after application. The microbial content of the sludge from sewage treatment plants especially dairy was barley examined; therefore, it is difficult to clearly identify threats that result from the presence of microorganisms in that kind of material (Frąc 2012). Sewage sludge formed through mechanical, biological and chemical treatment of sewage, meeting specific requirements concerning the microbiological status and chemical composition are an excellent alternative for other sources of organic matter and help to maintain the required level of humus in soil. That is why continuous monitoring of sewage sludge, as well as raw and digested dairy manure is necessary to preserve the high quality of sludge in order to safe agricultural application (Saunders et al. 2012).
The aim of the study was a multifaceted evaluation of microbiological and biochemical properties of sewage sludge from a dairy wastewater treatment plant from the District Dairy Cooperative in Krasnystaw (Eastern Poland, Europe). The study is related to environmental protection, especially with agricultural utilisation of the sludge and is of particular importance in the aspect of control of the quality of soils, especially those subjected to human activity.
Materials and methods
The experiment description
Dairy sewage is a result of washing off technological lines on which various dairy products are being produced. The sewage is purified in mechanical–biological treatment plants with the activated sludge system. First, crude sewage is supplied by gravity to a grating for preliminary mechanical purification. Then the sewage flows to a horizontal sand bed where sedimentation of small organic and mineral pollutants takes place. For the purpose of averaging the pollution load and pH, the sewage then flows under gravity to the preliminary aeration tank. After about 5 h, the sewage flows by gravity along a canal to the separation tank and then to two stirring tanks with AS. The process flow diagram summarising the production of dairy sewage sludge is presented as Fig. 1.
The study was performed on AS and WAS from the District Dairy Cooperative in Krasnystaw (Eastern Poland, Europe). Microbiological, biochemical and chemical analyses were conducted on 5 terms, and samples for the tests were taken over a period of 5 months at monthly intervals (from April to August 2011). AS was taken from aerated reactors, whereas WAS was collected from the prism immediately after dehydration by centrifugation. In each sampling term, 20 samples were collected from each object, as mean sample. All the parameters were assayed in three replications. The results were processed statistically using the analysis of variance (ANOVA). LSD values were calculated using the Tukey test at significance level of α = 0.05. All the analyses were performed using the STATISTICA 7.1 software.
The microbiological characterisation of the sludge under study comprised determinations of the total numbers of culturable bacteria and filamentous fungi by the plate method, numbers of nitrifying bacteria by the dilutions method and respiratory activity of both types of sludge. The total number of bacteria was determined on plate count agar (PCA, Biocorp, Poland) and the total numbers of fungi on Bengal rose agar (Biocorp, Poland). The determination of the nitrifiers was carried out in mineral liquid medium. Respiratory activity of the sludge was assayed with the method of respiration induction through the addition of glucose and application of 0.2 M NaOH as the acceptor of CO2 after 24 h of incubation according to the method of Rühling and Tyler (1973). Ten-milligram glucose g−1 dry soil was added to obtain maximum initial respiratory response. The identification of the dominant fungi was performed in waste activated dairy sewage sludge. Identification of fungi was performed on the basis of macroscopic and microscopic observation of strains in micro-cultures, using the systematic works of Watanabe (2010).
Genetic diversity evaluation of nitrifiers’ community
The dynamics of populations of nitrifying bacteria based on amoA gene was analysed with the use of the molecular technique polymerase chain reaction–denaturing gradient gel electrophoresis (PCR-DGGE). The analyses included the extraction of nucleic acids from the AS and WAS, and then PCR amplification of the amoA gene encoding the ammonium monooxygenase, with the use of primers GC-1F CGC CCG GGG CGC GCC CCG GGC GGG GCG GGG GCAC GGG GGT TTC TAC TGG TGGT and 2R CCC CTC KGS AAA GCC TTC TTC (Avrahami and Conrad 2003; Rotthauwe et al. 1997). Amplification of sludge DNA was conducted under the following conditions: preliminary denaturation at 94 °C 5 min, denaturation 94 °C 45 s, connection of starters 50 °C 30 s and elongation 72 °C 1 min, 30 cycles, and then the final elongation of DNA strands at 72 °C for 7 min, using fast thermal cycler (Applied Biosystem, Life Technologies, Waltham, Massachusetts, USA). PCR products were controlled on the agarose gel to evaluate quality and quantity of DNA. The electrophoretic separation of amplicons (80 ng) was conducted in the 6% polyacrylamide gel in denaturing agent gradient (DGGE) in the form of urea and formamide in the range of 30–60% for 18 h, at temperature of 60 °C and under voltage of 70 V, with the use of electrophoresis apparatus DCode System (Universal Mutation Detection System, BioRad) (Ceccherini et al. 2007). The gel was stained with a solution of SybrGreenI-1 × TAE (Sigma-Aldrich), and product visualisation was made in UV light with the use of a transilluminator (BioRad). The stripe patterns of the genetic profiles obtained were archivised using the GelDoc (BioRad) system. DNA from Nitrosomonas europea (ATCC 25978) and Nitrosolobus multiformis (ATCC 25196) was used as reference control. Based on the stripe patters obtained, a diagram was plotted illustrating the genetic distance between the analysed samples.
Dendrogram presenting similarity, between WAS and AS in different terms of analyses samples was set on scaled axis bond distances (Ward’s method), with marked boundaries Sneath’s criteria (33 and 66%). The diagram was created using Quantity One 2000 (BioRad, Hercules, California, USA).
Biochemical and chemical analyses
Dehydrogenase activity was assayed using the Thalmann method (1968) by the reduction of colourless, water soluble substrate (TTC) by dehydrogenases present in the soil environment; an insoluble product with red colour (triphenylformazan-TPF) is formed. Protease activity was evaluated according to Ladd and Butler method (1972), urease was assayed following Zantua and Bremner (1975), acid and alkaline phosphatase Alef et al. (1995), the rate of ammonification Nessler method and the rate of nitrification with the brucine method, and the concentration of ions NH4 + and NO3 − was measured spectrophotometrically using asparagine and ammonium phosphate, respectively, as substrates.
The heavy metals and macro-elements content in the AS and WAS were determined by inductively coupled plasma mass spectrometry after microwave digestion method with a HNO3 and H2O2, pH potentiometrically and total solid by weight method. Chemical analyses were performed in The Institute of Soil Science and Plant Cultivation—State Research Institute in Pulawy, Poland.
Results and discussion
The results of total number of culturable bacteria, fungi and nitrifiers are presented in Fig. 2. Both the total numbers of bacteria and those of fungi were greater in the WAS in relation to the AS (in the AS the total numbers of bacteria and fungi remained at a fairly constant level throughout the experiment). On the second term of analyses (in May), a significant drop in the numbers of bacteria in the WAS compared to the other times of analyses was observed. During the same period, also an inhibition of the growth of fungi was noted in the WAS (Fig. 2). The study showed that the range of variation in the total number of bacteria in 1 kg of WAS ranged between 87.6 × 10−9 and 131.3 × 10−9 cfu, while the number of bacteria in 1 kg of AS varied within a narrower range from 21.0 × 10−9 to 31.3 × 10−9 cfu. The total numbers of fungi during the period of the study varied within the range of 26.0–41.6 × 10−7 cfu per kg of WAS and 1.3 to 6.6 × 10−7 cfu per kg of AS. Significantly higher number of microorganisms was found in WAS than in AS. The highest numbers of first- and second-phase nitrifiers in the WAS were assayed on the third term of analyses (in June), while in the AS on the second term of analyses (in May) (Fig. 2). The experiment revealed that the populations of that microbial group were varied and depended significantly on the term of analyses. At all the terms of analyses (in each months from April to August), the content of second phase of nitrifiers was at a higher level in the AS than in the WAS. On the second term of analyses (in May) in the AS, a significant increase in the numbers of first phase of nitrifying bacteria was observed, but towards the end of the experiment the number of those nitrifiers decreased notably. The group of nitrifying microorganisms intensively participates in wastewater treatment. Therefore, the significant increase of nitrifiers in AS in II term of analyses (May) could be caused by higher pollution load of wastewater flowing into the treatment plant. However, the significant the decrease of nitrifiers number in WAS compared to AS was probably connected with pH of the sludge. The optimum pH for the growth of nitrifying bacteria is about 7.00; then, they are very sensitive on pH changes. The pH of WAS ranged from 8.11 to 8.81 (Table 1); therefore, the growth of this bacteria group was decreased (Fig. 2).
The waste activated dairy sewage sludge can be used as organic fertiliser, however, is regarded as a source of potentially phytopathogenic fungi. Therefore, it is important to monitor its mycological status before land application. Moulds from genera Actinomucor, Alternaria, Aspergillus, Chrysosporium, Cladosporium, Geotrichum, Mucor, Penicillium are reported in greater amounts in wastewater; therefore, they should be regarded as sludge-related microorganisms (Gotkowska-Płachta et al. 2013; Korzeniewska 2011). The dominant fungi isolated from the WAS included genera as Aspergillus sp., Penicillium sp., Candida sp. and Trichophyton sp. (Fig. 3). The presence of the above-mentioned fungi, also was found in municipal sewage sludge or in the air samples of wastewater treatment plant area and surroundings (Gotkowska-Płachta et al. 2013; Romdhana et al. 2009). Analyses of fungal diversity in wastes of this type were also conducted by Awad and Kraume (2011), Kacprzak and Stańczyk-Mazanek (2003). Those authors demonstrated that sewage sludge can be a habitat for potentially pathogenic and toxigenic fungi. Häuslerová (2006) recognised in her experiments that numerous micromycetes are a recognised part of the biocoenosis of growth in receiving waters strongly polluted by organically rich waste waters and of the growth on biofilter surfaces. The principal representatives are some Deuteromycetes, Mucorales and Saccharomycetaceae, whereas the so-called true aquatic fungi (Oomycetes) with the exception of Leptomitus lacteus, that they were not found. Generally, the filaments in the AS are ascribed to filamentous bacteria and as long as fungi were isolated from AS. The growths of micromycetes in AS remain still an unanswered question (Häuslerová 2006).
The determination of respiratory activity in sewage sludge reflects the intensity of respiratory metabolism of microorganisms and can be used as an indicator for the determination of microbiological activity of sewage sludge (Ren 2004). The increase of the organic matter content in soil after AS or WAS application can stimulate the growth of microorganisms, which in turn causes an increase in the respiratory activity of microorganisms. The weakening respiratory activity of the WAS in the last term of analyses (August) probably could have been caused by the increase of toxic heavy metals in the sludge (Table 1), inhibiting the respiratory metabolism of microorganisms (Ren 2004). The respiratory activity of the WAS attained the highest level on the third term of analyses (in June), and on the other terms of analyses (in April, in May, in July, in August) it remained at a fairly constant level (Fig. 4). The microbial respiration is dependent on pH, which strongly influences abiotic factors and may control biotic factors, such as the biomass composition of fungi and bacteria in environmental samples, including sewage sludge. Respiration, a measurement of the total activity of the microbial community, was probably not as strongly affected by pH between 7.00 and 8.81 as by heavy metals concentration, macro-element and total solid content (Fig. 4; Table 1).
Genetic diversity evaluation of nitrifiers’ community
The isolation and identification of microorganisms inhabiting the AS are of key importance for the understanding of the process of the biological treatment of sewage and for enhancing its effectiveness (Hesham et al. 2011). Studies on the genetic diversity of microorganisms inhabiting sewage sludge with the use of the molecular technique of the Denaturant Gel Gradient Electrophoresis (DGGE) were conducted by numerous researchers, e.g., Hesham et al. (2011), Er-ming and Wei (2011), Ding et al. (2011), Liu et al. (2007) and Forney et al. (2001). Diversity analysis of nitrifiers community occurring WAS and AS was conducted on five terms (I-V) (Fig. 5). Taking into account the less restrictive Sneath criterion (66%), there were five groups distinguishable (A–E). In cluster A, there was WAS II, WAS V grouped. In cluster B–AS IV. Clusters C and D contain WAS III and AS I, respectively. Moreover, cluster described as E grouped AS II, AS III, AS V, WAS I and WAS IV. The genetic diversity of treatments grouped in cluster E displayed fairly high similarity to each other (63–84%). Similar results were obtained by Hesham et al. (2011), who observed notable variability of microorganisms in sewage supplied to a treatment plant over a 6-month period from February to July. Also Forney et al. (2001) noted seasonal changes in microbial populations isolated from sewage sludge from the same treatment plant over the period of 1 year. Er-ming and Wei (2011), Liu et al. (2007) compared the genetic composition of nitrifiers community in sewage sludge from treatment plants utilising two different systems of sewage treatment and observed greater species diversity in that plant which was characterised by more effective elimination of ammonia. Ding et al. (2011) observed that various environmental conditions in the course of the process of sewage treatment may cause the selection of various microbial groups. Those results were also confirmed by Rowan et al. (2003), who observed that the profiles of nitrifiers were different in each of the sewage treatment plants studied.
The study showed that the activity of all enzymes under analysis was at a significantly higher level in the WAS than in the AS (Figs. 4, 6). In the AS, no significant differences were observed in the activity of the microbiological and biochemical parameters studied throughout the whole period of the experiment. WAS, on the other hand, was characterised by a certain dynamics of changes in the parameters under analysis in the course of the study. In the case of alkaline phosphatase, acid phosphatase, dehydrogenases, protease and urease, the highest activity of the WAS was observed on the third term of analyses (in June). With the exception of alkaline phosphatase, significant differences were observed in the activity of the enzymes (different months).
The greatest intensity of ammonification and nitrification in the WAS was also assayed on the third term of analyses (in June) (Fig. 7). After an initial increase, a significant decrease in the rate of those processes was also observed on the final term of analyses (in August). The obtained results indicate greater stability of microbial populations in the AS as compared to the WAS, which was visible in the lack of the significant differences in microbiological and biochemical parameters throughout the whole period of the experiment. Dehydrogenases activity, as well as the respiratory activity reflected the intensity of the respiratory metabolism of microorganisms and can be used for the determination of the microbiological activity of sewage sludge as those enzymes appear only in alive cells (Kumar and Tarafdar 2003). The lower dehydrogenase activity in the final stage of the study could have been caused by the depletion of organic matter after the initial intensive mineralisation of easily available biodegradable substrates.
Simultaneous measurement of the activity of various kinds of enzymes appears to be useful approach for the estimation of the biochemical activity of sewage sludge. Urease is an extracellular enzyme, and its activity increased proportionally to the concentration of the substrate, up to the point of attaining a maximum with a specific concentration of urea, following which it decreased. Acid and alkaline phosphatases play an important role in the mineralisation of organic phosphorus compounds, and dairy sewage sludge is a rich source of substrates for those enzymes. The decrease in acid and alkaline phosphatase activity after an initial increase can be attributed to the depletion of that group of substrates and also to the appearance of sewage contaminated with, e.g., heavy metals, as those enzymes are particularly sensitive to all kinds of toxic substances (Frąc and Jezierska-Tys 2011).
The WAS was characterised by a fairly high proteolytic activity on the third (in June) and fifth (in August) terms of analyses, which could have been caused by a high level of organic matter in the sludge formed in the course of treatment of dairy sewage. Janczukowicz et al. (2007) also confirm that dairy sewage sludge is a rich source of various kinds of organic substances, mineral compounds and total nitrogen. The least pronounced effect of dairy sewage sludge on the growth of microorganisms displaying proteolytic activity on the remaining terms of analyses can be attributed to the depletion of nutrients available for that microbial group.
Ammonium ions evolved in the course of the process of ammonification and as a result of urease activity caused the greatest intensification of the process of nitrification and thus an increase in the production of nitrate ions in the middle of the period of the study. Additionally, nitrate ions can inhibit the activity of dehydrogenases. The process of ammonification and nitrification is closely related to microorganisms involved in the nitrogen cycle and therefore depends on the presence of ammonia, nitrates and other nitrogen compounds in a given environment (Frąc and Jezierska-Tys 2011). The intensity of the process of nitrification may be reduced in a situation where the activity of nitrifying bacteria is inhibited by heavy metals.
The work fulfils the lack of knowledge about fungi occurrence in dairy sewage sludge which is rather poorly investigated comparing to other kinds of sludge. Aspergillus sp., Penicillium sp., Candida sp. and Trichophyton sp. were the most dominant fungi isolated from the waste activated dairy sewage sludge. Molecular analysis of nitrifying bacteria revealed their notable diversity in the sludge studied, related to the term of analyses. The intensity of nitrification, ammonification, and also respiratory activity and the activity of dehydrogenase, acid phosphatase, alkaline phosphatase, protease and urease were at significantly higher levels in the WAS than in the AS. Our results proved that microbial activity and fungal diversity can be used as quality indicators of waste such as dairy sewage sludge.
The results can be used by the management of wastewater treatment plants, including those located at the agro-food industry, farmers using sludge as fertiliser and organisations concerned with the protection of the natural environment.
Alef K, Nannipieri P, Trasar-Cepeda C (1995) Methods in applied soil microbiology and biochemistry. Academic Press, London, pp 335–344
Avrahami S, Conrad R (2003) Patterns of community change among ammonia oxidizers in meadow soils upon long-term incubation at different temperatures. Appl Environ Microbiol 69:6152–6164. doi:10.1128/AEM.69.10.6152-6164.2003
Awad MF, Kraume M (2011) Fungal diversity in activated sludge from membrane bioreactors in Berlin. Can J Microbiol 57:693–698. doi:10.1139/w11-056
Bieganowski A, Łagód G, Ryżak M, Montusiewicz A, Chomczyńska M, Sochan A (2012) Measurement of activated sludge particle diameters using laser diffraction method. Ecol Chem Eng S 19:597–608. doi:10.2478/v10216-011-0042-7
Ceccherini MT, Ascher J, Pietramellara G, Mocali S, Viti C, Nannipieri P (2007) The effect of pharmaceutical waste-fungal biomass, treated to degrade DNA on the composition of eubacterial and ammonia oxidizing populations of soil. Biol Fertil Soil 44:299–306. doi:10.1007/s00374-007-0204-z
Ding L, Zhou Q, Wang L, Zhang Q (2011) Dynamics of bacterial community structure in a full-scale wastewater treatment plant with anoxic-oxic configuration using 16S rDNA PCR-DGGE fingerprints. Afr J Biotechnol 10:589–600. doi:10.5897/AJB10.386
Er-ming O, Wei W (2011) Effects of elevated temperature on performance and microbial community structure in ASBR treating thermal-hydrolyzed sewage sludge. Energy Proced 11:3294–3303. doi:10.1016/j.egypro.2011.10.686
Forney LJ, Liu WT, Guckert JB, Kumagai Y, Namkung E, Nishihara T, Larson RJ (2001) Structure of microbial communities in activated sludge: potential implications for assessing the biodegradability of chemicals. Ecotoxicol Environ Saf 49:40–53. doi:10.1006/eesa.2001.2034
Frąc M (2012) Ocena mikologiczna osadu z oczyszczalni ścieków mleczarskich oraz jego wpływu na różnorodność funkcjonalną mikroorganizmów glebowych. Acta Agrophs Monogr 1:1–142
Frąc M, Jezierska-Tys S (2011) Agricultural utilisation of dairy sewage sludge: its effect on enzymatic activity and microorganisms of the soil environment. AJMR 5:1755–1762. doi:10.5897/AJMR10.707
Frąc M, Oszust K, Lipiec J (2012) Community level physiological profiles (CLPP), characterization and microbial activity of soil amended with dairy sewage sludge. Sensors 12:3253–3268. doi:10.3390/s120303253
Gadd JB, Northcott GL, Tremblay LA (2010) Passive secondary biological treatment systems reduce estrogens in dairy shed effluent. Environ Sci Technol 44:7601–7606. doi:10.1021/es1008054
Gotkowska-Płachta A, Filipkowska Z, Korzeniewska E, Janczukowicz W, Dixon B, Gołas I, Szwalgin D (2013) Airborne microorganisms emitted from wastewater treatment plant treating domestic wastewater and meat processing industry wastes. CLEAN Soil Air Water 41:429–436. doi:10.1002/clen.201100466
Häuslerová J (2006) The growth of micromycetes in activated sludge media. CLEAN Soil Air Water 4:137–152. doi:10.1002/aheh.3470040204
Hesham EA, Rong Q, Yang M (2011) Comparison of bacterial community structures in two systems of a sewage treatment plant using PCR-DGGE analysis. J Environ Sci 23:2049–2054. doi:10.1016/S1001-0742(10)60647-X
Hussein KA, Hassan AF, Abdel-Hady ES (2010) Study of sewage sludge use in agriculture and its effect on plant and soil. ABJNA 1:1044–1049
Janczukowicz W, Zieliński M, Dębowski M (2007) Biodegradability evaluation of dairy effluents originated in selected sections of dairy production. Bioresour Technol 99:4199–4205. doi:10.1016/j.biortech.2007.08.077
Jezierska-Tys S, Frąc M, Tys J (2010) Microbiological hazards resulting from application of dairy sewage sludge: effects on occurrence of pathogenic microorganisms in soil. J Toxicol Environ Health A 73:1194–1201. doi:10.1080/15287394.2010.491777
Kacprzak M, Stańczyk-Mazanek E (2003) Changes in the structure of fungal communities of soil treated with sewage sludge. Biol Fertil Soil 38:89–95. doi:10.1007/s00374-003-0633-2
Korzeniewska E (2011) Emission of bacteria and fungi in the air from wastewater treatment plants—a review. Front Biosci 1:393–407
Kumar P, Tarafdar JC (2003) 2,3,5-Triphenyltetrazolium chloride (TTC) as an electron acceptor of culturable soil bacteria, fungi and actinomycetes. Biol Fertil Soil 38:186–189. doi:10.1007/s00374-003-0600-y
Ladd JN, Butler JH (1972) Short-term assay of soil proteolytic enzyme activities using proteins and dipeptide derivatives as substrates. Soil Biol Biochem 4:19–30
Lim SL, Wu TY, Lim PN, Shak KP (2015) The use of vermicompost in organic farming: overview, effects on soil and economics. J Sci Food Agric 95:1143–1156. doi:10.1002/jsfa.6849
Lim SL, Lee LH, Wu TY (2016) Sustainability of using composting and vermicomposting technologies for organic solid waste biotransformation: recent overview, greenhouse gases emissions and economic analysis. J Clean Prod 111:262–278. doi:10.1016/j.jclepro.2015.08.083
Liu C, Zhang Y, Yang M, Wang Z, Lv W (2007) Analysis of bacterial community structures in two sewage treatment plants with different sludge properties and treatment performance by nested PCR-DGGE method. J Environ Sci 19:60–66
Mikosz J (2015) Determination of permissible industrial pollution load at a municipal wastewater treatment plant. Int J Environ Sci Technol 12:827–836. doi:10.1007/s13762-013-0472-0
Mohapatra DP, Cledón MS, Brar K, Surampalli RY (2016) Application of wastewater and biosolids in soil: occurrence and fate of emerging contaminants. Water Air Soil Pollut 227:77. doi:10.1007/s11270-016-2768-4
Oszust K, Frąc M, Lipiec J (2015) Soil microbial functionality in response to dairy sewage sludge and mineral fertilisers application under winter rape. Int J Environ Sci Technol 12:3675–3684. doi:10.1007/s13762-015-0807-0
Ren S (2004) Assessing wastewater toxicity to activated sludge: recent research and developments. Environ Int 30:1151–1164. doi:10.1016/j.envint.2004.06.003
Romdhana MH, Lecomte D, Ladevie B, Sablayrolles C (2009) Monitoring of pathogenic microorganisms contamination during heat drying process of sewage sludge. Process Saf Environ 8:377–386. doi:10.1016/j.psep.2009.08.003
Rotthauwe JH, Witzel KP, Liesack W (1997) The ammonia monooxygenase structural gene amoA as a functional marker: molecular fine-scale analysis of natural ammonia-oxidizing populations. Appl Environ Microbiol 6:4704–4712
Rowan AK, Snape JR, Fearnside D, Barer MR, Curtis TP, Head IM (2003) Composition and diversity of ammonia-oxidizing bacterial communities in wastewater treatment reactors of different design treating identical wastewater. FEMS Microbiol Ecol 43:195–206. doi:10.1111/j.1574-6941.2003.tb01059.x
Rühling A, Tyler G (1973) Heavy metal pollution and decomposition of spruce needly litter. Oikos 24:402–415
Saunders OE, Fortuna AM, Harrison JH, Cogger CG, Whitefield E, Green T (2012) Gaseous nitrogen and bacterial responses to raw and digested dairy manure applications in incubated soil. Environ Sci Technol 46:11684–11692. doi:10.1021/es301754s
Singh RP, Agrawal M (2008) Potential benefits and risks of land application of sewage sludge. Waste Manag 28:347–358. doi:10.1016/j.wasman.2006.12.010
Teh CY, Budiman PM, Shak KP, Wu TY (2016) Recent advancement of coagulation–flocculation and its application in wastewater treatment. Ind Eng Chem Res 55:4363–4389. doi:10.1021/acs.iecr.5b04703
Thalmann A (1968) Zur methodik der bestimmung der dehydrogenaseactivität im boden mittels triphenyltetrazoliumchlorid (TTC). Landwirtsh Forsch 21:249–258
Tran NH, Münnich K, Fricke K, Harborth P (2014) Removal of nitrogen from MBT residues by leachate recirculation in combination with intermittent aeration. Waste Manage Res 32:56–63. doi:10.1177/0734242X9801600106
Watanabe T (2010) Pictorial atlas of soil and seed fungi: morphologies of cultured fungi and key to species. CRC Press Taylor and Francis Group, Boca Raton, pp 1–404
Wyszkowska J, Kucharski J, Borowik A, Boros E (2008) Response of bacteria to soil contamination with heavy metals. J Elementol 13:443–453
Xu X, Cao X, Zhao L, Wang W, Yu H, Gao B (2013) Removal of Cu, Zn, and Cd from aqueous solutions by the dairy manure-derived biochar. Environ Sci Pollut Res Int 1:358–368. doi:10.1007/s11356-012-0873-5
Zantua MJ, Bremner JM (1975) Comparison of methods of assaying urease activity in soils. Soil Biol Biochem 7:291–295. doi:10.1016/0038-0717(75)90069-3
The research was partially funded by funds from the Ministry of Science and Higher Education in Poland in the years 2010–2013 as a research project (N N310 307439) and partially from The National Centre for Research and Development (NCBiR) in Poland—LIDER PROGRAMME 2011–2014 (LIDER/24/48/l2/10/NCBiR/2011).
Conflict of interest
The authors have declared no conflict of interest.
Editorial responsibility: M. Abbaspour.
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Frąc, M., Jezierska-Tys, S., Oszust, K. et al. Assessment of microbiological and biochemical properties of dairy sewage sludge. Int. J. Environ. Sci. Technol. 14, 679–688 (2017). https://doi.org/10.1007/s13762-016-1179-9
- Enzymatic activity
- Fungal composition
- Nitrifiers genetic diversity