Como citar este trabajo
Torri S.I., Corrêa R.S., Renella G. 2017. Biosolids application to agricultural land: a contribution to global phosphorus recycle, Pedosphere 27(1): 1–16, doi:10.1016/S1002-0160(15)60106-0, ISSN 1002-0160/CN 32-1315/P
Biosolids application to agricultural land: a contribution to global phosphor...Silvana Torri
Torri S.I., Corrêa R.S., Renella G. 2017. Biosolids application to agricultural land: a contribution to global phosphorus recycle, Pedosphere 27(1): 1–16, doi:10.1016/S1002-0160(15)60106-0, ISSN 1002-0160/CN 32-1315/P
soil organic carbon- a key for sustainable soil quality under scenario of cli...Bornali Borah
The global soil resource is already showing a sign of serious degradation (Banwart et al. 2014) which has ultimately negative impact on sustained crop yield and environmental quality. Due to intense rainfall and concurrent rise in temperature with changing climate, the fertile top soil is prone to severe degradation with depletion of SOC. Most soils in agricultural ecosystems have lost soil C ranging from 30 to 60 t C ha-1 with the magnitude of 50 to 75% loss (Lal, 2004). Hence, restoration of soil quality through different carbon management options will enhance soil health, mitigate climate change and provide sustained agricultural production.
Fate of cadmium, copper, lead and zinc on soils after the application of dif...Silvana Torri
Como citar este trabajo
Torri S, Lavado R. 2009. Fate of cadmium, copper, lead and zinc on soils after the application of different treated sewage sludge in soils of the Pampas region. In: Sewage Treatment: Uses, Processes and Impact. Editors: Anna Stephens and Mark Fuller, Nova Science Publishers, Inc., Hauppauge, NY 11788. ISBN: 978-1-60692-959-9. 95-123. 394p.
This presentation was presented during the Plenary 1, Opening Ceremony of the Global Symposium on Soil Organic Carbon that took place in Rome 21-23 March 2017. The presentation was made by Mr. Luca Montanarella from EU Commission’s Joint Research Centre, in FAO Hq, Rome
Environmental impact of biosolids land applicationSilvana Torri
Como citar este trabajo
Torri S, Cabrera M. 2017 Environmental impact of biosolids land application. In: Organic Waste: Management Strategies, Environmental Impact and Emerging Regulations, Editor: M Collins, Nova Science Publishers, Inc., Hauppauge, NY 11788, ISBN: 978-1-53610-936-8, 185-208, 226 pp
Biosolids application to agricultural land: a contribution to global phosphor...Silvana Torri
Torri S.I., Corrêa R.S., Renella G. 2017. Biosolids application to agricultural land: a contribution to global phosphorus recycle, Pedosphere 27(1): 1–16, doi:10.1016/S1002-0160(15)60106-0, ISSN 1002-0160/CN 32-1315/P
soil organic carbon- a key for sustainable soil quality under scenario of cli...Bornali Borah
The global soil resource is already showing a sign of serious degradation (Banwart et al. 2014) which has ultimately negative impact on sustained crop yield and environmental quality. Due to intense rainfall and concurrent rise in temperature with changing climate, the fertile top soil is prone to severe degradation with depletion of SOC. Most soils in agricultural ecosystems have lost soil C ranging from 30 to 60 t C ha-1 with the magnitude of 50 to 75% loss (Lal, 2004). Hence, restoration of soil quality through different carbon management options will enhance soil health, mitigate climate change and provide sustained agricultural production.
Fate of cadmium, copper, lead and zinc on soils after the application of dif...Silvana Torri
Como citar este trabajo
Torri S, Lavado R. 2009. Fate of cadmium, copper, lead and zinc on soils after the application of different treated sewage sludge in soils of the Pampas region. In: Sewage Treatment: Uses, Processes and Impact. Editors: Anna Stephens and Mark Fuller, Nova Science Publishers, Inc., Hauppauge, NY 11788. ISBN: 978-1-60692-959-9. 95-123. 394p.
This presentation was presented during the Plenary 1, Opening Ceremony of the Global Symposium on Soil Organic Carbon that took place in Rome 21-23 March 2017. The presentation was made by Mr. Luca Montanarella from EU Commission’s Joint Research Centre, in FAO Hq, Rome
Environmental impact of biosolids land applicationSilvana Torri
Como citar este trabajo
Torri S, Cabrera M. 2017 Environmental impact of biosolids land application. In: Organic Waste: Management Strategies, Environmental Impact and Emerging Regulations, Editor: M Collins, Nova Science Publishers, Inc., Hauppauge, NY 11788, ISBN: 978-1-53610-936-8, 185-208, 226 pp
Soil Organic Carbon stabilization in compost amended soilsExternalEvents
This presentation was presented during the 2 Parallel session on Theme 2, Maintaining and/or increasing SOC stocks for climate change mitigation and adaptation and Land Degradation Neutrality, of the Global Symposium on Soil Organic Carbon that took place in Rome 21-23 March 2017. The presentation was made by Mr. Riccardo Spaccini, from Universitá di Napoli Federico II - Italy, in FAO Hq, Rome
Assessing the potential of soil organic carbon sequestration in African soilsExternalEvents
This presentation was presented during the 2 Parallel session on Theme 2, Maintaining and/or increasing SOC stocks for climate change mitigation and adaptation and Land Degradation Neutrality, of the Global Symposium on Soil Organic Carbon that took place in Rome 21-23 March 2017. The presentation was made by Ms. Tantely Razafimbelo, from University of Antananarivo and CASA - Madagascar, in FAO Hq, Rome
Carbon sequestration through the use of biosolids in soils of the Pampas reg...Silvana Torri
Como citar este trabajo
Torri S, Lavado R. 2011. Carbon sequestration through the use of biosolids in soils of the Pampas region, Argentina. In: Environmental Management: Systems, Sustainability and Current Issues.Editor: H. C. Dupont, Nova Science Publishers, Inc., Hauppauge, NY 11788,ISBN: 978-1-61324-733-4.pag. 221-236, 336 p
Impact of soil properties on carbon sequestrationyoginimahadule
Carbon sequestration is an important global phenomenon that plays a significant role in maintaining a balanced global carbon cycle and sustainable crop production. Carbon Sequestration is the placement of CO2 into a depository in such way that it remains safely and not released back to the atmosphere.
Among the soil factors, texture plays an important role in C sequestration. The observation that the decrease in clay- and silt associated C and N upon cultivation of soils was generally less than the decrease in C and N in the particle size fraction > 20 µm confirms that clay and sift particles protect C against microbial degradation (Hassink, 1997).
Increase in SOC concentration with conservation tillage was partly responsible for the increased macroaggregation near the soil surface.( Zhang et al. 2013)
Electrical conductivity in soils affects the organic carbon content by reducing the uptake of minerals and water by the plant which ultimately results in less plant growth. A higher electrical conductivity causes less decomposition in soils which consequently reduces the accumulation of humus meanwhile, the values of acidity; percentage of organic matter, organic carbon and the sequestration of carbon in soils containing T. kotschyiwas more than the values observed in soils containing T. aphylla and the soil of the control which contained no plants.
Nitrogen applicaton at optimum rate help to sequester carbon in soil.(Jiang et al. 2019). Integrated nutrient application in long-term rice-wheat cropping system would be a suitable option with respect to its potentiality of increasing yield, nutrient availability, and sequestering soil organic carbon for sustainable soil health management in partially reclaimed sodic soils of the north Indian subcontinent. He concluded that FYM application increase passive pool of soil while green manure increase active and labile pool. (Choudhury et al. 2018)
Six et al. (2006) by various observation of different sites concludes changes in the relative abundance and activity of bacteria and fungi may significantly affect C cycling and storage, due to the unique physiologies and differential interactions with soil physical properties of these two microbial groups. It has been hypothesized that C turnover is slower in fungal-dominated communities in part because fungi in corporate more soil C into biomass than bacteria and because fungal cell walls are more recalcitrant than bacterial cell walls. Same result by Aliasgharzad et al. 2016).
Tsai et al. (2013) showed positive correlation of soil organic carbon with elevation
Feasibility of using a mixture of sewage sludge and incinerated sewage sludge...Silvana Torri
Como citar este trabajo:
Torri S. 2009. Feasibility of using a mixture of sewage sludge and incinerated sewage sludge as a soil amendment. In: Sludge: Types, Treatment Processes and Disposal. Editor: Richard E. Baily, Nova Science Publishers, Inc., Hauppauge, NY 11788. ISBN: 978-1-60741-842-9. pp. 187-208, 317p.
Determination of the Soil Organic Carbon (SOC) and Measurement of the Biodive...Shariful Islam
Soil organic carbon is one of the important elements and the major component of the soil. A complex biogeochemical cycle in the soil mostly dependent on the soil organic carbon (SOC). However, this experimental method measure the soil organic carbon in the Chandpai range, Sundarbans. The research has been found the soil organic carbon at very low portion in the study area and the different diversity index of different study plots of the forest. The sampling area contaminated with oil spill and affected by different human activities. Most of the studied focused on the different parameters of the forest soil such as soil pH, soil water holdings capacity, soil moisture etc. However, this study analyzes the soil to measure the soil organic carbon and calculate the biodiversity index in the Sundarbans
Soil Organic Carbon: A Key Factor of Sustainable Agriculture in IranExternalEvents
This presentation was presented during the 3 Parallel session on Theme 3.3, Managing SOC in: Dryland soils, of the Global Symposium on Soil Organic Carbon that took place in Rome 21-23 March 2017. The presentation was made by Mr. Fahrad Moshiri, from Agricultural Research, Education, and Extensio Organization – Iran, in FAO Hq, Rome
Zn distribution in soils amended with different kinds of sewage sludgeSilvana Torri
Como citar este trabajo
Torri S, Lavado R. 2008 b. Zn distribution in soils amended with different kinds of sewage sludge. Journal of Environmental Management (Elsevier, Amsterdam, The Netherlands), 88: 1571-1579. doi:10.1016/j.jenvman.2007.07.026 ISSN: 0301-4797.
Cadmium and lead hazards as occurring with their speciations in periurbain ag...Premier Publishers
Environment pollution hazard awareness is required for less industrialized countries which are faced with increasing periurban agriculture practice however. Lead (Pb) and Cadmium (Cd) were characterized around Abidjan city (Bingerville, Port-Bouët and Yopougon) in soil, perched ground water and vegetable crops (Hibiscus and sweet potato). Total amounts and speciations of metals were determined respectively. The sites were mainly differing with pH observed at Yopougon characterized by highest soil content of Pb (40 mg kg-1). In contrast with the low soil contents of metals, plant contaminations were observed in the root for Cd and Pb at Yopougon and Port-Bouët sites respectively with variance involving above and below ground organs as specific contamination of Hibiscus or sweet potato. Skeleton fractions as exchangeable (F1) and carbonate bound (F2) were characterizing these contaminations although additional fraction as oxide bound (F3) Cd and organic (F4) Pb were required respectively for effectiveness. The non-polluted perched groundwater pH, Eh, temperature and O2 concentration were likely concerned by these fractions availability beside that of residual fraction (F5) of Cd. Enhance isomorphic substitution of anionic Pb forms transforming F2 into F5 and the cationic substitutions between Cd and Pb were suggested for pollution management.
Quantifying Global Soil Carbon Losses in Response to WarmingExternalEvents
This presentation was presented during the Plenary 1, GSOC17 – Setting the scientific scene for GSOC17 of the Global Symposium on Soil Organic Carbon that took place in Rome 21-23 March 2017. The presentation was made by Mr. Thomas Crowther from Netherlands Institute of Ecology , in FAO Hq, Rome
Soil Organic Carbon stabilization in compost amended soilsExternalEvents
This presentation was presented during the 2 Parallel session on Theme 2, Maintaining and/or increasing SOC stocks for climate change mitigation and adaptation and Land Degradation Neutrality, of the Global Symposium on Soil Organic Carbon that took place in Rome 21-23 March 2017. The presentation was made by Mr. Riccardo Spaccini, from Universitá di Napoli Federico II - Italy, in FAO Hq, Rome
Assessing the potential of soil organic carbon sequestration in African soilsExternalEvents
This presentation was presented during the 2 Parallel session on Theme 2, Maintaining and/or increasing SOC stocks for climate change mitigation and adaptation and Land Degradation Neutrality, of the Global Symposium on Soil Organic Carbon that took place in Rome 21-23 March 2017. The presentation was made by Ms. Tantely Razafimbelo, from University of Antananarivo and CASA - Madagascar, in FAO Hq, Rome
Carbon sequestration through the use of biosolids in soils of the Pampas reg...Silvana Torri
Como citar este trabajo
Torri S, Lavado R. 2011. Carbon sequestration through the use of biosolids in soils of the Pampas region, Argentina. In: Environmental Management: Systems, Sustainability and Current Issues.Editor: H. C. Dupont, Nova Science Publishers, Inc., Hauppauge, NY 11788,ISBN: 978-1-61324-733-4.pag. 221-236, 336 p
Impact of soil properties on carbon sequestrationyoginimahadule
Carbon sequestration is an important global phenomenon that plays a significant role in maintaining a balanced global carbon cycle and sustainable crop production. Carbon Sequestration is the placement of CO2 into a depository in such way that it remains safely and not released back to the atmosphere.
Among the soil factors, texture plays an important role in C sequestration. The observation that the decrease in clay- and silt associated C and N upon cultivation of soils was generally less than the decrease in C and N in the particle size fraction > 20 µm confirms that clay and sift particles protect C against microbial degradation (Hassink, 1997).
Increase in SOC concentration with conservation tillage was partly responsible for the increased macroaggregation near the soil surface.( Zhang et al. 2013)
Electrical conductivity in soils affects the organic carbon content by reducing the uptake of minerals and water by the plant which ultimately results in less plant growth. A higher electrical conductivity causes less decomposition in soils which consequently reduces the accumulation of humus meanwhile, the values of acidity; percentage of organic matter, organic carbon and the sequestration of carbon in soils containing T. kotschyiwas more than the values observed in soils containing T. aphylla and the soil of the control which contained no plants.
Nitrogen applicaton at optimum rate help to sequester carbon in soil.(Jiang et al. 2019). Integrated nutrient application in long-term rice-wheat cropping system would be a suitable option with respect to its potentiality of increasing yield, nutrient availability, and sequestering soil organic carbon for sustainable soil health management in partially reclaimed sodic soils of the north Indian subcontinent. He concluded that FYM application increase passive pool of soil while green manure increase active and labile pool. (Choudhury et al. 2018)
Six et al. (2006) by various observation of different sites concludes changes in the relative abundance and activity of bacteria and fungi may significantly affect C cycling and storage, due to the unique physiologies and differential interactions with soil physical properties of these two microbial groups. It has been hypothesized that C turnover is slower in fungal-dominated communities in part because fungi in corporate more soil C into biomass than bacteria and because fungal cell walls are more recalcitrant than bacterial cell walls. Same result by Aliasgharzad et al. 2016).
Tsai et al. (2013) showed positive correlation of soil organic carbon with elevation
Feasibility of using a mixture of sewage sludge and incinerated sewage sludge...Silvana Torri
Como citar este trabajo:
Torri S. 2009. Feasibility of using a mixture of sewage sludge and incinerated sewage sludge as a soil amendment. In: Sludge: Types, Treatment Processes and Disposal. Editor: Richard E. Baily, Nova Science Publishers, Inc., Hauppauge, NY 11788. ISBN: 978-1-60741-842-9. pp. 187-208, 317p.
Determination of the Soil Organic Carbon (SOC) and Measurement of the Biodive...Shariful Islam
Soil organic carbon is one of the important elements and the major component of the soil. A complex biogeochemical cycle in the soil mostly dependent on the soil organic carbon (SOC). However, this experimental method measure the soil organic carbon in the Chandpai range, Sundarbans. The research has been found the soil organic carbon at very low portion in the study area and the different diversity index of different study plots of the forest. The sampling area contaminated with oil spill and affected by different human activities. Most of the studied focused on the different parameters of the forest soil such as soil pH, soil water holdings capacity, soil moisture etc. However, this study analyzes the soil to measure the soil organic carbon and calculate the biodiversity index in the Sundarbans
Soil Organic Carbon: A Key Factor of Sustainable Agriculture in IranExternalEvents
This presentation was presented during the 3 Parallel session on Theme 3.3, Managing SOC in: Dryland soils, of the Global Symposium on Soil Organic Carbon that took place in Rome 21-23 March 2017. The presentation was made by Mr. Fahrad Moshiri, from Agricultural Research, Education, and Extensio Organization – Iran, in FAO Hq, Rome
Zn distribution in soils amended with different kinds of sewage sludgeSilvana Torri
Como citar este trabajo
Torri S, Lavado R. 2008 b. Zn distribution in soils amended with different kinds of sewage sludge. Journal of Environmental Management (Elsevier, Amsterdam, The Netherlands), 88: 1571-1579. doi:10.1016/j.jenvman.2007.07.026 ISSN: 0301-4797.
Cadmium and lead hazards as occurring with their speciations in periurbain ag...Premier Publishers
Environment pollution hazard awareness is required for less industrialized countries which are faced with increasing periurban agriculture practice however. Lead (Pb) and Cadmium (Cd) were characterized around Abidjan city (Bingerville, Port-Bouët and Yopougon) in soil, perched ground water and vegetable crops (Hibiscus and sweet potato). Total amounts and speciations of metals were determined respectively. The sites were mainly differing with pH observed at Yopougon characterized by highest soil content of Pb (40 mg kg-1). In contrast with the low soil contents of metals, plant contaminations were observed in the root for Cd and Pb at Yopougon and Port-Bouët sites respectively with variance involving above and below ground organs as specific contamination of Hibiscus or sweet potato. Skeleton fractions as exchangeable (F1) and carbonate bound (F2) were characterizing these contaminations although additional fraction as oxide bound (F3) Cd and organic (F4) Pb were required respectively for effectiveness. The non-polluted perched groundwater pH, Eh, temperature and O2 concentration were likely concerned by these fractions availability beside that of residual fraction (F5) of Cd. Enhance isomorphic substitution of anionic Pb forms transforming F2 into F5 and the cationic substitutions between Cd and Pb were suggested for pollution management.
Quantifying Global Soil Carbon Losses in Response to WarmingExternalEvents
This presentation was presented during the Plenary 1, GSOC17 – Setting the scientific scene for GSOC17 of the Global Symposium on Soil Organic Carbon that took place in Rome 21-23 March 2017. The presentation was made by Mr. Thomas Crowther from Netherlands Institute of Ecology , in FAO Hq, Rome
Phosphorus recycling is a emerging problem in organic farming due to deterioration of rock phosphate sources from earth. There is a need for usage of alternative sources for P requirement by knowing their environmental impacts.
Soybean and Corn crop response to enhanced efficiency phosphate fertilizerAI Publications
Many agricultural soils worldwide in their natural state are deficient in phosphorous (P). As P is vital for all living beings, as P fertilizers are manufactured from non-renewable resources and as P fertilizer efficiency is generally low, we need to improve the P use efficiency and minimize P fertilizers usage to ensure the future sustainability of our cropping systems. Enhanced-efficiency fertilizers use is one of the strategies to increase P fertilizer efficiency, but there is no consensus on the effectiveness of this type of technology. The need to increase the efficiency of P fertilization and the lack of information about enhanced efficiency P fertilizer justifies studies to evaluate the performance of this kind of fertilizer. Experiments were carried out in greenhouse and field conditions to investigate the effect of P fertilizer coated with anionic polymers (Policote) on corn and soybean crop development and yield, and agronomic P use efficiency. Greenhouse experiments were conducted with corn crop, while field trials were carried out with soybean crop. Greater increases in plant growth parameters, crop yield, soil P content, and fertilizer efficiency use were observed with Policote coated fertilizer than with conventional P fertilizer. The observed changes in P use efficiency among P fertilizers increased our understanding of enhanced efficiency fertilizers. The obtained results demonstrated that Policote coated fertilizer can be used as an enhanced efficiency fertilizer. Results show that Policote coated fertilizer is a more efficient way to deliver required phosphorous to plants than conventional ones.
Enhancement of phosphorus utilization and availability in the mountainous reg...Open Access Research Paper
The soil has a large reserve of phosphorus. However, phosphorus availability for plant nutrition is limited, and mostly in ferralitic tropical soils, determined by the geochemical distribution of elements. In the mountainous region of Man, West Côte d’Ivoire, the geology and geomorphology constitute a particular characteristic which, more or less, could significantly influence soil phosphorus distribution and availability. A study was thus setup to assess soil oxides and mineralogy, and their influence on soil phosphorous content in Man. Four different rice producing sites were selected for soil sampling; Krikouma, Dompleu, Blolé and Petit-Gbêpleu (PG). Within each site, three composite samples were taken at 0 – 20cm depth from 3 plot of 25m2, each. The results of the X-ray fluorescence analysis showed the presence of large quantities of iron and aluminium oxides in the soil. In addition, these soils were rich in SiO2. The mineralogical matrix had two dominant mineral species Berlinite and Quartz, dividing the soils into two categories. This study provides scientific base for developing strategies for a sustainable phosphorous fertilization of rice cropping soils.
Enhanced efficiency phosphorous fertilizers on the coffee crop in sandy soilAI Publications
Crops are generally cultivated in deficient phosphorus soils in the tropics. Phosphorus (P) is essential to crop development and has a low efficient use in fertilizer management. The need to increase P fertilization efficiency justify studies evaluating the performance of enhanced efficiency P fertilizers. A greenhouse experiment was carried out to evaluate coffee growth, plant P contents, and agronomic P fertilization efficiency. The treatments, randomly designed with three replicates, were arranged in a 2x5 factorial scheme: two P sources (Triple Superphosphate – TSP and Policote coated TSP – TSP+Policote) and five P rates (0; 5; 10; 15 and 20 g P2O5.plot-1). The experimental plot was formed by a pot with 14 kg of sandy soil. All treatments were homogenized with the plot's soil. Then, coffee seedlings were transplanted. Coffee growth, plant P content and accumulation, and agronomic P fertilization efficiency were affected by phosphorus fertilization. TSP+Policote promoted higher leaf and plant dry matter yield and P accumulation in coffee than conventional P fertilizer. The higher agronomic efficiency and apparent P recovery efficiency index, observed with TSP+Policote, explain the higher coffee plant growth observed with Policote coated P fertilizer. The obtained results demonstrated that Policote coated P fertilizer can be used as an enhanced efficiency fertilizer. Results show that Policote coated P fertilizer is a more efficient way to deliver the required P to plants.
Utilization of Marginal Soils with Application of Phosphorus and Ethephon for...Agriculture Journal IJOEAR
— Abundance of marginal soils is among the major constraint to achieve high yield for crop production due to unsuitable physical and chemical properties of the soils. Commonly, farmers would manage the marginal soil by adding soil amendment, compost and fertilizer which increase the cost of production. Alternatively, application of fertilizer together with plant growth regulator (PGR) during crop management can be practiced to utilize the marginal soil effectively. The aim of this experiment was to determine effects of phosphorus (P) fertilizer and PGR namely ethephon on growth performance of sweet corn grown in three marginal soils namely Rasau, Kuah and Dampar. The treatments were arranged as factorial randomized complete block design with four rates of P fertilizer and standard rate of ethephon replicated four times. The results indicated that the physical properties of the marginal soils vary which Rasau dan Kuah series have low content of silt (10.30% and 36.10%), respectively and clay (9.40% and 11.86%) while Dampar series has low sand content (21%). Consequently, Dampar series depicted highest soil moisture content (18.80%) compared to Rasau and Kuah with high content of silt and clay at 42.43% and 36.43%, respectively. At tasseling stage, where application of P fertilizer with combination of ethephon at 0 and 15 kg P 2 O 5 ha-1 there were significant difference between soil series on root length, total biomass wet and dry weight but exception for total biomass dry weight at 0 kg P 2 O 5 ha-1. Moreover, at 45 kg P 2 O 5 ha-1 there were significant difference among soil series on leaf number and total biomass dry weight whereas at highest P rate of 60 kg P 2 O 5 ha-1 only root length and root volume were affected. Most of the results were observed highest on Rasau soil series which contain highest sand particle instead of silt and clay compared to Kuah and Dampar series. However, the addition of ethephon and several P rates did not affect plant height among soil series. The results suggest that, the marginal soil can be utilized for sweet corn production by addition of combined P fertilizer at low rate and PGR.
Biosolids application to agricultural land: a contribution to global phosphor...Silvana Torri
Como citar este trabajo
Torri S.I., Corrêa R.S., Renella G. 2017. Biosolids application to agricultural land: a contribution to global phosphorus recycle, Pedosphere 27(1): 1–16, doi:10.1016/S1002-0160(15)60106-0, ISSN 1002-0160/CN 32-1315/P
Soil carbon sequestration resulting from biosolids application, Silvana Torri
Como citar este trabajo
Torri S.I., Corrêa R.S., Renella G. 2014. Soil carbon sequestration resulting from biosolids application, Applied and Environmental Soil Science (ISSN: 1687-7667), Volume 2014 (2014), Article ID 821768, 9 pages. doi:10.1155/2014/821768.
Characterization of organic compounds from biosolids of Buenos Aires City, Silvana Torri
Como citar este trabajo
Torri S.I., C. Alberti. 2012. Characterization of organic compounds from biosolids of Buenos Aires City, Journal of Soil Science and Plant Nutrition, 12 (1), 143-152
Downward movement of potentially toxic elements in biosolids amended soils,Silvana Torri
Como citar este trabajo
Torri S.I., Corrêa R.S. 2012. Downward movement of potentially toxic elements in biosolids amended soils, Special issue: Biosolids Soil Application: Agronomic and Environmental Implications, Applied and Environmental Soil Science (ISSN: 1687-7667), Volume 2012, Article ID 145724, 7 pages, doi:10.1155/2012/145724.
Use of vermiculture technology for waste management and environmental remedia...Silvana Torri
Como citar este trabajo
Torri S, Puelles M. 2010. Use of vermiculture technology for waste management and environmental remediation in Argentina, International Journal of Environmental Engineering (IJEE), Sp. Issue on Vermiculture Technology, Vol. 10, No.3/4 pp. 239 –254. doi:10.1504/IJGENVI.2010.037269. ISSN (Online): 1756-8471, ISSN (Print): 1756-8463.
Potential of Discaria Americana for metal immobilization on soils amended wit...Silvana Torri
Como citar este trabajo
Torri S, Zubillaga M, Cusato M. 2009. Potential of Discaria Americana for metal immobilization on soils amended with biosolid and ash-spiked biosolids. International Journal of Phytoremediation (Taylor & Francis, Inc., 325 Chestnut Street, Suite 800, Philadelphia, PA 19106), 11:1–13, (Print ISSN: 1522-6514; Online ISSN: 1549-7879).
Plant absorption of trace elements in sludge amended soils and correlation wi...Silvana Torri
Como citar este trabajo
Torri S, Lavado R. 2009. Plant absorption of trace elements in sludge amended soils and correlation with soil chemical speciation. Journal of Hazardous Materials, 166: 1459–1465. ISSN: 0304-3894 doi: 10.1016/ j.jhazmat.2008.12.075.
Estimation of leaf area in pecan cultivars (Carya illinoinensis), Silvana Torri
Como citar este trabajo
Torri S, Descalzi C, Frusso E. 2009. Estimation of leaf area in pecan cultivars (Carya illinoinensis), Cien. Inv. Agr. 36:53-58, ISSN 0718-1620. Editorial: Facultad de Agronomía e Ingeniería Forestal, Pontificia Universidad Católica de Chile, Santiago, Chile.
Dynamics of Cd, Cu and Pb added to soil through different kinds of sewage sludgeSilvana Torri
Como citar este trabajo
Torri S, Lavado R. 2008 a. Dynamics of Cd, Cu and Pb added to soil through different kinds of sewage sludge. Waste Management (Elsevier, Amsterdam, The Netherlands), 28: 821-832. ISSN: 0956-053X. doi:10.1016/j.wasman.2007.01.020.
Remediación de suelos contaminados con elementos traza mediante el uso de bio...Silvana Torri
Torri S, Zubillaga M, Lavado RS. 2006. Remediación de suelos contaminados con elementos traza mediante el uso de biosólidos compostados y enmienda calcárea. II) efecto sobre las fracciones de menor biodisponibilidad de Zn. Revista Facultad de Agronomía, UBA. Editorial Facultad de Agronomía (EFA) UBA. Buenos Aires, Argentina. 26: 93-97. ISSN: 0325-9250.
Mineralization of Carbon from Sewage sludge in three soils of the Argentine p...Silvana Torri
Como citar este trabajo
Torri S, Alvarez R, Lavado R. 2003. Mineralization of Carbon from Sewage sludge in three soils of the Argentine pampas. Commun. Soil Sci. and Plant Anal. (Taylor & Francis, Inc., 325 Chestnut Street, Suite 800, Philadelphia, PA 19106) 34 (13-14): 2035-2043. ISSN (impresa): 0010-3624. ISSN (electronica): 1532-2416.
Distribución y disponibilidad de elementos potencialmente tóxicos en suelos r...Silvana Torri
Como citar este trabajo
Torri S, Lavado R. 2002. Distribución y disponibilidad de elementos potencialmente tóxicos en suelos representativos de la provincia de Buenos Aires enmendados con biosólidos. Ciencia del Suelo. 20 (2): 98-109. ISSN 0326-3169.
Micronutrientes. En: Fertilidad de suelos y fertilización de cultivosSilvana Torri
Torri S, Urricariet A.S, Lavado R. 2015. Micronutrientes. En: Fertilidad de suelos y fertilización de cultivos. García F y Echeverría H. Ediciones INTA, Balcarce, ISBN 978-987-521-565-8, 357-377. 908 p.
Micronutrientes. En: Fertilidad de suelos y fertilización de cultivos.Silvana Torri
Como citar este trabajo
Torri S, Urricariet A.S, Lavado R. 2015. Micronutrientes. En: Fertilidad de suelos y fertilización de cultivos. García F y Echeverría H. Ediciones INTA, Balcarce, ISBN 978-987-521-565-8, 357-377. 908 p.
Plants response to high soil Zn availability. Feasibility of biotechnological...Silvana Torri
Como citar este trabajo
Torri S, Cabrera M, Torres- Duggan. 2013. Plants response to high soil Zn availability. Feasibility of biotechnological improvement. En: Biotechnologic Techniques of Stress in Plants, Editor: M. Miransari, Stadium Press LLC USA, ISBN : 1-62699-031-X, 101-118.
Zinc availability to forage crops in soils of the pampas region, Argentina.Silvana Torri
Como citar este trabajo
Torri S, Perez-Carrera A, Fernández-Cirelli A. 2012. Zinc availability to forage crops in soils of the pampas region, Argentina. In: Trace Elements: Environmental Sources, Geochemistry and Human Health. Editores: D. A. De Leon y P.R. Aragon, Nova Science Publishers, Inc., Hauppauge, NY 11788.
Data Centers - Striving Within A Narrow Range - Research Report - MCG - May 2...pchutichetpong
M Capital Group (“MCG”) expects to see demand and the changing evolution of supply, facilitated through institutional investment rotation out of offices and into work from home (“WFH”), while the ever-expanding need for data storage as global internet usage expands, with experts predicting 5.3 billion users by 2023. These market factors will be underpinned by technological changes, such as progressing cloud services and edge sites, allowing the industry to see strong expected annual growth of 13% over the next 4 years.
Whilst competitive headwinds remain, represented through the recent second bankruptcy filing of Sungard, which blames “COVID-19 and other macroeconomic trends including delayed customer spending decisions, insourcing and reductions in IT spending, energy inflation and reduction in demand for certain services”, the industry has seen key adjustments, where MCG believes that engineering cost management and technological innovation will be paramount to success.
MCG reports that the more favorable market conditions expected over the next few years, helped by the winding down of pandemic restrictions and a hybrid working environment will be driving market momentum forward. The continuous injection of capital by alternative investment firms, as well as the growing infrastructural investment from cloud service providers and social media companies, whose revenues are expected to grow over 3.6x larger by value in 2026, will likely help propel center provision and innovation. These factors paint a promising picture for the industry players that offset rising input costs and adapt to new technologies.
According to M Capital Group: “Specifically, the long-term cost-saving opportunities available from the rise of remote managing will likely aid value growth for the industry. Through margin optimization and further availability of capital for reinvestment, strong players will maintain their competitive foothold, while weaker players exit the market to balance supply and demand.”
Show drafts
volume_up
Empowering the Data Analytics Ecosystem: A Laser Focus on Value
The data analytics ecosystem thrives when every component functions at its peak, unlocking the true potential of data. Here's a laser focus on key areas for an empowered ecosystem:
1. Democratize Access, Not Data:
Granular Access Controls: Provide users with self-service tools tailored to their specific needs, preventing data overload and misuse.
Data Catalogs: Implement robust data catalogs for easy discovery and understanding of available data sources.
2. Foster Collaboration with Clear Roles:
Data Mesh Architecture: Break down data silos by creating a distributed data ownership model with clear ownership and responsibilities.
Collaborative Workspaces: Utilize interactive platforms where data scientists, analysts, and domain experts can work seamlessly together.
3. Leverage Advanced Analytics Strategically:
AI-powered Automation: Automate repetitive tasks like data cleaning and feature engineering, freeing up data talent for higher-level analysis.
Right-Tool Selection: Strategically choose the most effective advanced analytics techniques (e.g., AI, ML) based on specific business problems.
4. Prioritize Data Quality with Automation:
Automated Data Validation: Implement automated data quality checks to identify and rectify errors at the source, minimizing downstream issues.
Data Lineage Tracking: Track the flow of data throughout the ecosystem, ensuring transparency and facilitating root cause analysis for errors.
5. Cultivate a Data-Driven Mindset:
Metrics-Driven Performance Management: Align KPIs and performance metrics with data-driven insights to ensure actionable decision making.
Data Storytelling Workshops: Equip stakeholders with the skills to translate complex data findings into compelling narratives that drive action.
Benefits of a Precise Ecosystem:
Sharpened Focus: Precise access and clear roles ensure everyone works with the most relevant data, maximizing efficiency.
Actionable Insights: Strategic analytics and automated quality checks lead to more reliable and actionable data insights.
Continuous Improvement: Data-driven performance management fosters a culture of learning and continuous improvement.
Sustainable Growth: Empowered by data, organizations can make informed decisions to drive sustainable growth and innovation.
By focusing on these precise actions, organizations can create an empowered data analytics ecosystem that delivers real value by driving data-driven decisions and maximizing the return on their data investment.
As Europe's leading economic powerhouse and the fourth-largest hashtag#economy globally, Germany stands at the forefront of innovation and industrial might. Renowned for its precision engineering and high-tech sectors, Germany's economic structure is heavily supported by a robust service industry, accounting for approximately 68% of its GDP. This economic clout and strategic geopolitical stance position Germany as a focal point in the global cyber threat landscape.
In the face of escalating global tensions, particularly those emanating from geopolitical disputes with nations like hashtag#Russia and hashtag#China, hashtag#Germany has witnessed a significant uptick in targeted cyber operations. Our analysis indicates a marked increase in hashtag#cyberattack sophistication aimed at critical infrastructure and key industrial sectors. These attacks range from ransomware campaigns to hashtag#AdvancedPersistentThreats (hashtag#APTs), threatening national security and business integrity.
🔑 Key findings include:
🔍 Increased frequency and complexity of cyber threats.
🔍 Escalation of state-sponsored and criminally motivated cyber operations.
🔍 Active dark web exchanges of malicious tools and tactics.
Our comprehensive report delves into these challenges, using a blend of open-source and proprietary data collection techniques. By monitoring activity on critical networks and analyzing attack patterns, our team provides a detailed overview of the threats facing German entities.
This report aims to equip stakeholders across public and private sectors with the knowledge to enhance their defensive strategies, reduce exposure to cyber risks, and reinforce Germany's resilience against cyber threats.
Adjusting primitives for graph : SHORT REPORT / NOTESSubhajit Sahu
Graph algorithms, like PageRank Compressed Sparse Row (CSR) is an adjacency-list based graph representation that is
Multiply with different modes (map)
1. Performance of sequential execution based vs OpenMP based vector multiply.
2. Comparing various launch configs for CUDA based vector multiply.
Sum with different storage types (reduce)
1. Performance of vector element sum using float vs bfloat16 as the storage type.
Sum with different modes (reduce)
1. Performance of sequential execution based vs OpenMP based vector element sum.
2. Performance of memcpy vs in-place based CUDA based vector element sum.
3. Comparing various launch configs for CUDA based vector element sum (memcpy).
4. Comparing various launch configs for CUDA based vector element sum (in-place).
Sum with in-place strategies of CUDA mode (reduce)
1. Comparing various launch configs for CUDA based vector element sum (in-place).
1. Pedosphere 27(1): 1–16, 2017
doi:10.1016/S1002-0160(15)60106-0
ISSN 1002-0160/CN 32-1315/P
c⃝ 2017 Soil Science Society of China
Published by Elsevier B.V. and Science Press
Biosolid Application to Agricultural Land—a Contribution to
Global Phosphorus Recycle: A Review
Silvana Irene TORRI1,∗
, Rodrigo Studart CORRˆEA2
and Giancarlo RENELLA3
1Department of Natural Resources and Environment, School of Agriculture, University of Buenos Aires, Avenue San Martin 4453,
Buenos Aires 1417 DSE (Argentina)
2University of Bras´ılia-UnB/PPGCA, Campus Darcy Ribeiro, Caixa Postal 04.401, 70910-970 DF (Brazil)
3Department of Agrifood Production and Environmental Sciences, University of Florence, Piazzale delle Cascine 18, Florence 50144
(Italy)
(Received June 30, 2016; revised November 10, 2016)
ABSTRACT
Phosphorus (P) is an essential nutrient required for plant development. Continuous population growth and rising global demand
for food are expected to increase the demand for phosphate fertilizers. However, high-quality phosphate rock reserves are progressively
becoming scarce. Part of the increased pressure on P resources could be alleviated by recycling P present in biosolids. Therefore, it is
crucial to understand the dynamics of P in biosolid-amended soils, the effects of residual biosolid-borne P in soils, the way in which
microorganisms may control P dynamics in biosolid-amended soils and the environmental implications of the use of biosolids as a
source of P. Further research is needed to maximize biosolid-borne P uptake by crops and minimize its loss from biosolid-amended
soils. The analysis of the microbiological control of P dynamics in biosolid-amended soils indicates interactions of biosolid P with
other nutrients such as carbon (C) and nitrogen (N), suggesting that harmonization of the current regulation on the use of biosolids
in agriculture, mainly based on total N and pollutant contents, is needed to better recycle P in agriculture.
Key Words: anthropogenic P, phosphate, P availability, P biogeocycle, P uptake, runoff P
Citation: Torri S I, Corrˆea R S, Renella G. 2017. Biosolid application to agricultural land—a contribution to global phosphorus
recycle: A review. Pedosphere. 27(1): 1–16.
INTRODUCTION
Phosphorus (P) is an essential nutrient for all forms
of life. Biomolecules containing P are present in cellu-
lar components, including membranes (phospholipids),
genetic material (DNA and RNA), and energy storage
(ATP and ADP), among others (Elser, 2012). While
humans and animals satisfy their need for P via food
intake, plants have to absorb it from soils. In spite of
its wide distribution in nature, P is one of the least
available mineral nutrients to plants (Goldstein et al.,
1988), and P uptake is usually a growth-limiting fac-
tor (Grant et al., 2005). Unlike nitrogen (N), the bio-
geochemical cycle of P does not include a significant
gaseous component, since its annual atmospheric de-
position rates are in the order of 0.25 kg P ha−1
year−1
(Liu Y et al., 2008). In natural ecosystems, P is entire-
ly supplied from the weathering of parent materials
(Schlesinger and Bernhardt, 1997), and the amount
of total P is preserved because it is released back to
the soil system through plant residues, animal excreta
or when organisms die. In agricultural systems, crop
removal represents the primary route by which P is
lost from soils. Unless P sources are artificially incor-
porated to agricultural soils, both total and available
P stocks steadily decrease with time to the point that
the soil can no longer adequately supply plant P needs
(Van Vuuren et al., 2010). In the course of time, soil P
depletion may lead to loss of soil fertility and produc-
tivity.
Mineral phosphate fertilizers are the primary so-
urce of P input to agricultural lands. Even though the
use of rock phosphate-based fertilizers was introduced
in the 1820s, it was not until the late 1940s that P
fertilizers were increasingly requested. In 2011, global
phosphate fertilizer production resulted in the deple-
tion of approximately 20 Mt of P from phosphate rock
(Jasinski, 2013). The demand for P is expected to in-
crease in the following years due to continuous popu-
lation growth and rising global demand for food, with
a predicted increase to approximately 257 Mt by 2017
(Heffer, 2013; Jasinski, 2013). Economic, high-quality
∗Corresponding author. E-mail: torri@agro.uba.ar.
2. 2 S. I. TORRI et al.
phosphate rock reserves are progressively becoming
scarce (Cordell and Neset, 2014). Although reserves of
phosphate rock are found in several countries and new
reserves have been identified (Midgley, 2012), phos-
phate rock is a finite, non-renewable resource. Accor-
ding to the U.S. Geological Survey, phosphate deposits
will last about 50 years at the current rate of extrac-
tion (Kelly and Matos, 2013). Therefore, there is an
increasing concern regarding phosphate rock reserves
to become depleted.
Part of the increased pressure on P resources could
be alleviated by recycling P present in various agricul-
tural and urban wastes (Frossard et al., 2009; Mac-
Donald et al., 2011). However, the joint effects of poor
knowledge of P status and the lack of a clear regulation
on manure or organic waste agricultural management
still limits P recycling potential in agriculture. This
paper reviews the availability and environmental fate
of P present in biosolids and envisages some possible
strategies for its sustainable management.
BIOSOLIDS AS A SOURCE OF P
Land application of organic by-products is an eco-
nomically attractive waste management strategy, lar-
gely promoted by scientists and regulating organisms.
Furthermore, it has been a socially accepted practice
for decades in many parts of the world (Tsadilas, 2011;
Larney and Angers, 2012; Lu et al., 2012).
The term biosolid was introduced in the early 1990s
to designate the solid, semi-solid or liquid materials
generated from the treatment of domestic sewage slu-
dge that has been sufficiently processed to be safely
land-applied. Biosolids contain organic carbon (C), N,
P, potassium (K), sulphur (S), calcium (Ca), magne-
sium (Mg), and microelements necessary for plants and
soil fauna to live. Nutrient contents in biosolids depend
on the untreated water source, chemicals used for pu-
rification, and types of unit operations used, and were
reported to be in the ranges of 1–210 g N kg−1
, 1–
150 g P kg−1
, 1–65 g K kg−1
, 5–170 g Ca kg−1
, and
2–94.5 g Mg kg−1
(Hansen and Chaney, 1984; Solis-
Mejia et al., 2012). Application of biosolids on agricul-
tural and degraded lands is one of the most promising
alternatives of disposal, because it offers the possibility
of recycling plant nutrients and organic matter (Gar-
c´ıa-Orenes et al., 2005; Torri and Lavado, 2009a, b;
Kowaljow et al., 2010). This practise may also con-
tribute to soil C sequestration, reducing greenhouse gas
emissions (Haynes et al., 2009; Tian et al., 2009; Torri
and Lavado, 2011; Torri et al., 2014). However, bio-
solids may contain undesirable hazardous substances
such as potentially toxic trace elements ranging from
less than 1 to over 1 000 mg kg−1
, polychlorinated
biphenyls (PCBs), polycyclic aromatic hydrocarbons
(PAHs), and dioxins (Abad et al., 2005; Mart´ınez et
al., 2007; Torri, 2009; Ahumada et al., 2014; Jord´an et
al., 2016). Consequently, biosolids have to be properly
treated and disposed to prevent health risk and en-
vironmental contamination (Kroiss, 2004). Although
to date experimental results indicate a low level of
risk for crops or pastures (Torri and Lavado, 2009a,
b; Cogger et al., 2013a), application of biosolids onto
non-agricultural land is usually preferred to avoid the
risk of hazardous substances entering the food chain
(Magesan and Wang, 2003; Athamenh et al., 2015).
In the European Union, a global regulation on
biosolid use in agriculture relies on the Water Frame-
work Directive (2000/60/EC) (EC, 2000) and the sub-
sequent Groundwater Directive (2006/118/EC) (EC,
2006), which have resumed all the previous specific
Directives on bathing waters, sewages sludge, urban
wastes and nitrates, and limit the potential recycle of
any biosolids in agriculture to their impacts on surface
water, groundwater, and atmosphere caused by exces-
sive nutrient, organic and inorganic pollutants. While
most organic pollutants can be degraded and excessive
N may be volatilized during sludge treatment, trace
elements are generally concentrated and may exceed
the mandatory limits for sludge application to agri-
cultural soils (CEC, 1986). Elevated contents of trace
elements prevent the use of sludge as a soil amendment
because of their negative impacts on soil microbial di-
versity and microbial activity (Renella et al., 2007a;
Gomes et al., 2010).
In wastewater, P is mainly found as orthophos-
phates, usually linked to small amounts of organic P
(Tran et al., 2012). Phosphorus removal is performed
by biological treatment or physiochemical precipita-
tion. In both cases, the soluble forms of P are con-
verted into a solid fraction, which can be an insolu-
ble salt or microbial biomass (De-Bashan and Bashan,
2004). Physiochemical precipitation removes dissolved
P phosphates by the addition of aluminium (Al),
iron (Fe), or calcium (Ca) compounds (Lee and Lin,
2007). The reaction is probably a combination of sur-
face adsorption onto metal hydroxides with chemi-
cal precipitation of the metal phosphate, producing
low P concentrations in the liquid phase (Elliott and
O’Connor, 2007). Biological P removal (BPR) pro-
cess relies on the use of a specific group of bacteria
that take up P in excess for their growth requirements
(Chen et al., 2013; Keating et al., 2016). The excess of
P is stored as intracellular granules of polyphosphate
(Grady et al., 2011), concentrating diluted P in waste-
3. BIOSOLID APPLICATION AND GLOBAL P RECYCLE 3
water by 10–50 times in bacterial aggregates (Yuan et
al., 2012).
Depending on the pre- or post-treatment used,
mean total P in biosolids was reported to be in the
range of 3.7–72.6 g P kg−1
on a dry weight base (Bar-
barick and Ippolito, 2007; Cordell, 2010). The addition
of some type of liming agent to stabilize biosolids may
result in lower total P (Christie et al., 2001). Since
more stringent N and P discharge limits have been im-
plemented on wastewater treatment plants (WWTP)
in environmentally sensitive areas, total P in biosolids
is expected to increase from current values (Clark et
al., 2010; Qin et al., 2015).
In biosolids, P exists in both soluble and insolu-
ble organic and inorganic P compounds (Tian et al.,
2012). Inorganic P is the predominant form, represen-
ting 70%–90% of total P (O’Connor et al., 2004; He
et al., 2010). Most P in biosolids is commonly in the
forms of aluminium phosphate (Shannon and Verghese,
1976), adsorbed onto ferric hydroxo-phosphate surfaces
(Jenkins et al., 1971), and hydroxyapatite or tricalcium
phosphate (Stumm and Morgan, 1970), with relatively
low water-soluble P as compared to total P (Brandt
et al., 2004). Organic P is mainly found as orthophos-
phate monoesters, orthophosphate diesters, phospho-
nates, phytates, and phospholipids (Hinedi et al., 1989;
He et al., 2010; Torri and Alberti, 2012).
It is well known that availability of P to plants
depends on the replenishment of labile P in the soil
solution from diverse soil fractions (Beck and Sanchez,
1994). In a general sense, P availability is defined as
those P compounds that are present in the correct
chemical forms to be taken up by plants during their
life cycle or taken up and used by living biological
organisms. The most significant P compound in terms
of availability is the orthophosphate anion, which is
associated with readily accessible short-term availabi-
lity for plants (Montalvo et al., 2015; Anand et al.,
2016). Phosphorus precipitation and dissolution reac-
tions greatly influence its concentration in the soil so-
lution, whereas organic P has to be hydrolyzed and
mineralized by microbial biomass to release orthophos-
phate anions. Hence, the importance of insoluble P
compounds rests entirely on their ability to buffer P
solution concentration or to become soluble in the soil
environment (McLaughlin, 1984).
Phosphorus availability in biosolids is strongly in-
fluenced by the wastewater treatment (WWT) proces-
ses (O’Connor et al., 2004; Elliott et al., 2005; White
et al., 2010). Sludge treatment with high Al and/or Fe
doses results in biosolids having low available P con-
centrations, with Fe and Al phosphates as dominant
P forms (Shober and Sims, 2007). Taking into account
that the solubility kinetics of these phosphate mine-
rals is extremely slow, it is unlikely that such mine-
rals, once formed, would readily release P into the
soil solution (Strawn et al., 2015). In fact, P in bio-
solids treated with Al and Fe was found to be less
soluble than P in untreated biosolids or commercial
fertilizers (Kyle and McClintock, 1995). Addition of
lime was reported to increase biosolid pH and decrease
the solubility of P by the formation of recalcitrant Ca-
phosphate minerals (Maguire et al., 2006; Shober et
al., 2006; Islas-Espinoza et al., 2014). Conversely, bio-
solids obtained by BPR exhibit both elevated total P
and water-extractable P when exposed to anaerobic
conditions (Stratful et al., 1999; Penn and Sim, 2002;
Ebeling et al., 2003). As the latter achieves effluent P
standards without the use of metal salts, the resultant
biosolids are typically low in Al and Fe contents and
their water-soluble P is higher than that of the other
treatments (Penn and Sims 2002; Brandt et al., 2004).
Heat-dried biosolids (non-BPR) were reported to
have the lowest P availability of all WWT processes.
Heat drying has been seen to reduce P extractability
by an average of 75% compared to dewatered proces-
ses (Smith et al., 2002a). Sarkar and O’Connor (2004)
found that heat-dried biosolids containing high levels
of Al and Fe have less than 10% water-soluble P. Ot-
her researchers reported that water-soluble P in heat-
dried biosolids was relatively low, in the range of 0.2%–
38%, as compared to total P (Frossard et al., 1996a;
Brandt et al., 2004). Smith et al. (2002b) indicated
that heat drying changes available P forms into low
soluble crystalline P minerals such as hydroxyapatite
and iron pyrophosphate. It was hypothesized that
the relatively low P bioavailability may be partly
attributed to slow physical breakdown of the pellets
(O’Connor and Sarkar, 1999; Smith et al., 2002b). In
the light of all these, O’Connor et al. (2004) suggested
grouping biosolids into three categories according to
biosolid-borne P availability relative to the inorganic
fertilizer triple superphosphate (TSP): low (< 25% of
TSP), moderate (25%–75% of TSP), and high (> 75%
of TSP). Their study identified biosolids produced with
conventional WWT processes as being in the moderate
category, BPR biosolids as being in the high category,
and biosolids with high total Fe and Al as being in the
low category. Current potential techniques for direct
speciation of P in soil and organic matrices have been
reviewed by Kruse et al. (2015).
DYNAMICS OF P IN BIOSOLID-AMENDED SOILS
The dynamics of biosolid-borne P differs from that
4. 4 S. I. TORRI et al.
of mineral fertilizer P because not all the P in bio-
solids is phytoavailable in soil (Penn and Sims, 2002;
Codling, 2014). As mentioned above, biosolid P phy-
toavailability is closely related to its chemical forms in
the solid phase (Akhtar et al., 2005), which depends on
the composition of the wastewater entering the treat-
ment plant and the type of treatment process used (Sa-
blayrolles et al., 2010). Biosolid-borne P is often less
soluble and less plant available compared to soluble
phosphate fertilizer P (Tian et al., 2009). Jenkins et
al. (2000) estimated that almost 50% of phosphate in
most biosolid products is available for plant uptake du-
ring the first year.
When biosolids are land applied, different processes
occur, such as P sorption/desorption, microbial decom-
position of organic P, and dissolution/precipitation of
mineral P phases. Thus, changes in the forms and con-
centrations of biosolid-borne P occur upon biosolid in-
corporation. Depending on the biological and physico-
chemical properties of a soil, the rate of one of these
processes may be higher than the other one.
Several studies have reported an increase in bio-
available P levels in biosolid-amended soils in line with
biosolid application rates (Akhtar et al., 2012; Alleoni
et al., 2012; Hosseinpur and Pashamokhtari, 2013; Sha-
heen and Tsadilas, 2013). This increase may be at-
tributed to the high concentration of inorganic P in
the biosolids. However, these differences seem to be
less pronounced in P-enriched soils or soils that have
high affinity to retain P, such as those derived from cal-
careous parent material (Sarkar and O’Connor, 2004;
Ippolito et al., 2007). Other researchers reported that
the shift of biosolid-borne P from less labile to more
labile forms may also contribute to increases in soil P
availability to plants (Sui et al., 1999; Haney et al.,
2015).
Calcium-dominated biosolids result in higher con-
centrations of water-soluble P in biosolid-amended
soils (Brandt et al., 2004). Moreover, alkaline-stabi-
lized biosolids exhibit mean percentages of water-
extractable P statistically higher than conventionally
stabilized biosolids, which may be attributed to the
mineralization of organic P in biosolids. Many studies
have found that lime amendments increase soil orga-
nic C mineralization (Wong and Su, 1997; Torri et al.,
2003). Jokinen (1990) studied the influence of treat-
ment process on available soil P in biosolid-amended
soils and concluded that Al treatment reduces soil P
availability, whereas Ca treatment increases soil P ava-
ilability. Recently, Withers et al. (2015) observed that
Fe-treated and thermally dried biosolids give the lowest
increases (3%–6%), whereas lime-treated biosolids pro-
duce the largest increases in available P (11%–12%).
Past research has shown that P availability in soils
amended with chemically treated, anaerobically diges-
ted biosolids followed the order: Ca treatment > Fe
treatment > Al treatment (Soon and Bates, 1982). An
explanation to this is that P is bound to soil Ca sur-
faces with lower binding energy compared with Fe or
Al surfaces which bind P more strongly (Delgado and
Torrent, 1997; Elliot et al., 2002b). Therefore, chemi-
cal addition of Al, Fe, and Ca during wastewater and
biosolid processing is of main importance in determi-
ning P dynamics in biosolid-amended soils. Moreover,
if biosolids had undergone thermal treatment, the re-
activity of Fe-bound P minerals in biosolids is consi-
derably reduced and, consequently, the release of avai-
lable P is restricted (Hogan et al., 2001).
Biosolid soil application may also enhance P mi-
neralization, which would contribute to releases of or-
ganic biosolid-borne P and thus lead to an increase
in extractable P levels in the soil (O’Connor et al.,
2004). The positive correlations between soil respira-
tion and labile organic C and N in biosolid-amended
soils suggest that the stimulation of the activity of both
soil and biosolid-borne microbial communities can e-
xert a general solubilizing effect towards biosolid nutri-
ents (S´anchez-Monedero et al., 2004; Jin et al., 2011),
including P (Haney et al., 2015). However, the inte-
raction between biosolid degradation and P availability
may be more complex. For instance, in a leaching ex-
periment, Silveira and O’Connor (2013) reported that
dissolved organic C (DOC) released through biosolid
mineralization does not follow the same pattern as P
in leachates. Their results suggest that part of the mi-
neralized P is sorbed onto Al and Fe oxides present in
the soil, masking any relationship between DOC and
water-extractable P concentrations.
Land application of biosolids also incorporates non-
crystalline, colloidal amorphous forms of Fe and Al
oxides with a large specific surface area (Shober et
al., 2006). These amorphous complexes of Fe and Al
oxides can effectively adsorb or bind native soil phos-
phates (Nanzyo, 1986). Most research results have
shown that land application of biosolids modifies not
only soil P adsorption capacity (Maguire et al., 2000;
Lu and O’Connor, 2001), but also certain soil proper-
ties, such as dissolved organic matter, electrical con-
ductivity, pH and biological properties (Silveira et al.,
2003; Gilmour et al., 2003; Torri, 2009; Scharenbroch
et al., 2013). Biosolid organic matter was found to have
an indirect effect on phosphate adsorption, through in-
5. BIOSOLID APPLICATION AND GLOBAL P RECYCLE 5
hibiting Al oxide crystallization and even through in-
creasing the amorphous nature of Al (Bøen et al.,
2013; Maguire et al., 2000). This effect was similar,
but less pronounced, for Fe compounds (Borggaard
et al., 1990). In addition, P availability in biosolid-
amended soils may be also modified by environmental
conditions, such as temperature and moisture content.
Specific reactions between biosolid-borne P and the
soil matrix increase with time and, thus, P extractabi-
lity may be considerably reduced. For example, Silve-
ira and O’Connor (2013) observed that P becomes
less bioavailable with time due to increased P sorp-
tion. Consequently, it is very complicated to predict
the dynamics and availability of biosolid-borne P in
biosolid-amended soils.
EFFECT OF RESIDUAL BIOSOLID P IN SOILS
Phosphorus from biosolids has been applied in ex-
cess to soils at N-based rates because sewage materials
have a much higher P:N ratio (0.5–1.1) than required
by plants (0.07–0.14) (Mitchell et al., 2000). Even
though the fate of P after biosolid N exhaustion is
still an unsolved matter in the management of sewage
materials in soils (Corrˆea, 2004). Nutrients from bio-
solids and chemical fertilizers may continue to act in
soils beyond the period they are supposed to promote
plant growth (Weatherley et al., 1988). Such a linge-
ring effect to nourish plants decreases with time (Cor-
rˆea and Silva, 2016) to a negligible level considered
as residual effect (Barrow and Campbell, 1972). Seve-
ral studies have measured residual effects of fertilizers,
but only few have done it for biosolids (Michael et al.,
1991). Residual effects of biosolid P left in soils can
be measured in various ways including by means of
plant yield, providing that all other nutrients for plant
growth are sufficiently supplied (Barrow and Camp-
bell, 1972). In this case, biosolid P remaining in soils
after N depletion may further enhance plant yields if
N fertilizer is again supplied to plants (Pascual et al.,
1999).
Nutrient availability for plant uptake depends on
soil chemical, biological, and physical conditions. Or-
ganic matter, organisms, and nutrients that remain in
biosolid-amended soils after N depletion may improve
soil conditions (Corrˆea and Bento, 2010) and further
increase plant absorption of nutrients if N is applied on
the top of residual biosolids (Corrˆea et al., 2005). Posi-
tive effects of residual biosolid P and organic matter in
a Spodosol have been indirectly measured through di-
fferences in plant production between chemically ferti-
lized soils (control) and soils containing residual ter-
tiary domestic sewage sludge that were applied with
urea N (Fig. 1) (Corrˆea, 2002). Plant yields were 2–3
times higher in the Spodosol containing residual bio-
solids than in the control (Fig. 1). The application of
chemical P to the Spodosol containing residual bioso-
lids did not enhance plant yields, since P was not in
shortage in this soil after N exhaustion (Barrow and
Bolland, 1990; Corrˆea, 2004).
Differently from the Spodosol, an Oxisol contai-
ning the same residual tertiary domestic sewage sludge
showed detrimental effect on plant yields after recei-
ving urea N (Fig. 2) (Corrˆea, 2002). Such an effect sug-
gests shortage of available P because the Oxisol chemi-
cally fertilized at 20 mg P kg−1
(control) responded
well to increasing rates of urea N. Oxisols have a high
P-fixing capacity due to their high contents of Fe and
Al oxides (Smyth and Sanchez, 1980), which decrease
P availability to plants by means of phosphate adsorp-
tion onto soil particles (Barrow and Campbell, 1972).
As previously mentioned, tertiary sewage sludge is con-
Fig. 1 Plant yields (dry weight) at different rates of urea N applied to a Spodosol chemically fertilized at 20 mg P kg−1 (control)
and to the same Spodosol containing residual tertiary sewage sludge previously applied at rates of 1, 3, and 5 t ha−1 (Corrˆea, 2002).
6. 6 S. I. TORRI et al.
Fig. 2 Plant yields (dry weight) at different rates of urea N applied to an Oxisol chemically fertilized at 20 mg P kg−1 (control) and
to the same Oxisol containing residual tertiary sewage sludge previously applied at rates of 1, 3, and 5 t ha−1 (Corrˆea, 2002).
ditioned with Al and Fe salts that can further increase
phosphate-retention capacity of soils (Whitehead et al.,
2001). Scharer et al. (2001) reported that the applica-
tion of Al and Fe oxides to a soil at 10 mg kg−1
in-
creased its P-sorption capacity by 1.6 times, with pro-
portional decrease in P availability in soil solution. As
a result, up to 90% of P in biosolids conditioned with
Al and Fe salts can not be taken up by plants (Corrˆea,
2004; Sarkar and O’Connor, 2004). The incorporation
of tertiary sewage sludge into soils naturally rich in Fe
and Al like the Oxisol may turn the edaphic environ-
ment into a P sink. When it happens, P sources applied
at rates high enough to exceed P sorption capacity of
biosolid-amended soil can overcome shortage of avai-
lable P for plant growth (Maguire et al., 2000). A-
gricultural lime (CaCO3 or CaMg(CO3)2) amendment
can decrease soil P-sorption capacity for a while, but
P application is more effective in increasing P availabi-
lity in soils than lime amendment (Smyth and Sanchez,
1980).
Contrary to the Spodosol, plant yields respon-
ded well to the application of P fertilizer to the Oxi-
sol containing residual tertiary sewage sludge (Corrˆea,
2002), which confirms the hypothesis of shortage of
available P in the last soil. Studies have generally re-
ported decreases in plant P uptake from soils amen-
ded with biosolids conditioned with Al and Fe salts
(Saarela, 1998; Esteller et al., 2009). Investigation on
P sorption revealed that both P isotherm slopes and
equilibrium P concentrations have unfavorably been al-
tered in the Oxisol containing residual tertiary sewage
sludge in comparison to the control Oxisol, which was
not amended with sewage sludge (Corrˆea, 2002). Par-
ticular behaviors of biosolid P in different soils make it
difficult to generalize an optimal biosolid use for a self-
sustained positive residual effect. A specific aspect of
P dynamics in biosolid-amended soils is that the flexi-
bility of soil microorganisms influence P uptake and
immobilization rates, in particular in relation to C and
N availability by altering the C:N:P ratio (Frossard
et al., 1996b; Maguire et al., 2000). There are several
mechanisms of nutrient interactions in soils, and plant
responses to N are often dependent upon the availabi-
lity of P (Walworth and Summer, 1988).
The magnitude of P adsorption to soil particles is
also related to timing after a soil receiving phosphate
application (Burkitt et al., 2001; Whitehead et al.,
2001). Thus, biosolid P left in some soil types after N
exhaustion may not be useful for plant production after
a certain time due to soil P fixation. In other soils like
the Spodosol, plant yields were significantly enhanced
when chemical N was applied on the top of residual
biosolid P (Corrˆea, 2002), which continues to be valu-
able for plant production. Among various minerals and
substances present in soils, Fe and Al oxides lead to the
highest P-fixing capacity due to the increasing number
of sorption sites (Celi et al., 2001; Scharer et al., 2001;
Liu Z et al., 2008). In this regard, a promising alter-
native to the use of Al and Fe salts in WWT process
is recovering N and P as struvite (MgNH4PO4·6H2O),
a slow-release fertilizer that precipitates when Mg and
lime (CaO or Ca(OH)2) are added to wastewater or
sewage sludge (Liu Z et al., 2008). This can increase
the efficiency of biosolid P use by plants (Corrˆea, 2004)
and enhance the recycling of P from wastes in soils.
MICROBIOLOGICAL CONTROL OF P DYNAMICS
IN BIOSOLID-AMENDED SOILS
The existence of a microbial P turnover in soils is
long known and its relation with C and N cycles has
7. BIOSOLID APPLICATION AND GLOBAL P RECYCLE 7
been proven in the past (Johnson and Broadbent,
1952). There is a general consensus that biosolid-borne
P undergoes a slower turnover rate than P from chemi-
cal fertilizers. This is mainly due to the complexity of
biosolid matrix that becomes more recalcitrant during
decomposition. Moreover, biosolid particle allocation
within the soil aggregates also contributes to different
partition among the different biotic and abiotic pools
(Fig. 3), as hypothesized by Hens and Merckx (2001).
Soil microorganisms as well as plant roots actively
or passively release extracellular enzymes to mineralize
C, N, P, and S from complex substrates to make them
bioavailable (Nannipieri et al., 2012). Biochemical hy-
drolysis of organic phosphate esters in soils is main-
ly catalyzed by phosphomonoesterase and phospho-
diesterase, which release orthophosphate anions, the
preferentially assimilated P form by plants and soil
microorganisms. It has been reported that phosphomo-
noesterase activity in the rhizosphere is the main me-
chanism for P acquisition by plants (Gilbert et al.,
1999), catalyzing P released by a wide range of or-
thophosphate esters and anhydrides (Gellatly et al.,
1994). More complex P solubilization mechanisms, me-
diated by the release of specific secondary metabo-
lites such as polyphenols in legume plants, have al-
so been reported (Tomasi et al., 2008). In forest
soils phosphatase activity responds mainly to seaso-
nal changes of soil temperature and moisture, whereas
in arable soils, phosphatase activity mainly responds
to agricultural practices (Dick and Tabatabai, 1992)
and to the release of root exudates by crops (Renel-
la et al., 2007b). Phosphatase activity can be inhibi-
ted in soils fertilized with N, P, and K, whereas in
biosolid-amended soils, P is added together with ot-
her nutrients (e.g., C, N, and S), used as energy
sources by soil microorganisms for the synthesis of
several hydrolytic enzymes according to the economic
theory (Allison and Vitousek, 2005; Renella et al.,
2007c). This makes the major difference in P dynamics
between biosolid amendment and inorganic P fertiliza-
tion. In any case, high phosphatase activity genera-
lly observed in biosolid-amended soils does not neces-
sarily imply high P availability, as variable values of
phosphatase:microbial biomass ratio have been found
in different agro-ecosystems (Carpenter-Boggs et al.,
2003).
Increasing acid phosphomonoesterase activity has
been previously reported in agricultural soils amended
with biosolids (Dodor and Tabatabai 2003), and it is
likely related to the increases of soil microbial biomass
and activity in response to higher nutrient contents.
Different production and persistence rates of various
soil enzyme activities in different soils have also been
previously reported (Renella et al., 2007c). Biosolid-
amended soils may also undergo changes in pH-bu-
ffering capacity, which may change phosphatase acti-
vity (Renella et al., 2006). Phosphomonoesterase and
phosphodiesterase activities in biosolid-amended soils
Fig. 3 Phosphorus cycle in agricultural soils amended with chemical P fertilizers or biosolids. The thickness of the arrows and of the
boxes represent the relative importance of the pools and processes in the P cycle, respectively.
8. 8 S. I. TORRI et al.
can be considered as indicators of potential P release
from sewage sludge because these biosolids genera-
lly contain various P forms, with a predominant pro-
portion of phospholipids (Stott and Tabatabai, 1985).
Competition between plants and microorganisms for
P in the rhizosphere mainly depends on P demand by
crops, which in turn depends on plant development
stage. Previous studies have shown that the higher the
P demand by crops, the higher the acid phosphomo-
noesterase activity, either of plant or microbial origin
(Moorhead and Sinsabaugh, 2000). Bioavailability is
the potential for a substance or molecule to be trans-
ported across the cell layer. In complex natural bodies
like soil, this pool can be determined by the use of
whole cell biosensors. Whole cell biosensors are soil-
borne bacterial strains inserted with genes producing
a detectable signal (e.g., lux for bioluminescence and
gfp for autofluorescent proteins) upon assimilation of
specific molecules (van der Meer et al., 2004). Micro-
bial biosensors responding to C, N, and P in soil have
been constructed and used to monitor the bioavaila-
ble C, N, and P pools in plant rhizosphere and bulk
soil (Kragelund et al., 1997; Darwent et al., 2003). The
use of whole cell biosensor, although not routine and
standardized methods, hold the potential to finely as-
sess P dynamics in biosolid-amended soils, where more
chemical P forms are present compared to soils ferti-
lized with inorganic P. Moreover, the development of
whole cell biosensors with multiple gene insertions and
of signaling availability for different nutrients (Koch
et al., 2001) or the use of simultaneous biosensors re-
sponding to C, N, and P (Standing et al., 2003) allows
the study of P bioavailability in function of C and N
bioavailability, which may reveal how P dynamics is
interactively influenced by C and N bioavailability. In
particular, their use may be useful to better under-
stand how C and N bioavailability influences biosolid
P mineralization/immobilization dynamics, taking in-
to account that different biosolids may widely vary in
their C:N:P ratios both at the time of application or
during decomposition (Cleveland and Liptzin, 2007).
ENVIRONMENTAL IMPLICATIONS OF BIOSO-
LID USE
In most legislation, annual application rates of bio-
solids are determined by crop N requirements. The rea-
son for this is to prevent N leaching to groundwater
(Corrˆea et al., 2012; Al-Dhumri et al., 2013). Howe-
ver, the relatively low N/P ratio of biosolids has led
to a significant over application of P at the N-based
rate. As the amounts of P applied often exceed crop
removal (Shober and Sims, 2003; Schroder et al., 2008;
Cogger et al., 2013b), more than 95% of biosolid-borne
P remains in soils (Corrˆea, 2004). Surplus soil P from
biosolids is not detrimental to plants. Many soils in
developed nations nowadays contain adequate to ex-
cessive P due to years of application of P fertilizers or
organic materials containing P (O’Connor and China-
ult, 2006), but soil P sorption capacity may become
saturated with time (Smith et al., 2006; Withers et al.,
2009). Maguire et al. (2000) reported increased soil P
and increased P saturation in soils receiving long-term
biosolid amendment relative to unamended soils. Past
research has shown that soils that are more saturated
with P have less capacity to retain added P, which may
increase the more labile forms of soil P, with the risk
of P loss in runoff or by leaching (Hooda et al., 2000;
Pautler and Sims, 2000). The problem arises when ru-
noff waters or subsurface flows contain environmen-
tally unacceptable contents of dissolved P forms, or
when highly P-enriched soil particles are eroded in-
to water bodies (Maguire et al., 2005). Diffuse P pol-
lution is directly associated with the development of
water body eutrophication in agricultural ecosystems
(Withers and Jarvie, 2008; Quinton et al., 2010). Al-
though both P and N contribute to eutrophication, P
is the primary agent in freshwater eutrophication be-
cause many algae are able to obtain N from the at-
mosphere (Schindler, 1977). Soluble P as low as 0.02
mg L−1
is sufficient to induce water body eutrophica-
tion (Sharpley and Rekolainen, 1997). Eutrophication
brings a series of adverse ecological and water quality
problems such as fish death, shifts in species compo-
sition, blooms of harmful algae, and hypoxia in water
body, together with the presence of toxins, taste and
odour in drinking water (Hilton et al., 2006; Lowe et
al., 2008).
Research has shown that not all biosolids have the
same potential to affect the environment when land
applied. The solubility of P in biosolids exerts a ma-
jor influence on the potential for off-site P migration
at land application sites. As mentioned above, WWT
processes govern soil P solubility because of several
factors, including biosolid treatment (especially heat
drying) and biosolid chemical composition (especially
contents of Fe, Al, and Ca). Several studies have re-
ported a relationship between low P solubility in bioso-
lids and a high content of total or amorphous Fe and Al
(Maguire et al., 2001; O’Connor et al., 2004; Krogstad
et al., 2005). Biosolid treatments that produce rela-
tively dry biosolids, like heat drying, tend to reduce
water-extractable P (WEP) (Brandt et al., 2004). Si-
nce only a small fraction of P from most conventionally
9. BIOSOLID APPLICATION AND GLOBAL P RECYCLE 9
produced biosolids is soluble, biosolid P should be less
likely to negatively affect the environment compared
with soluble P sources like mineral fertilizers or ma-
nures.
Even though the solubility of P in the soil increa-
ses with biosolid application rates, off-site P migration
may not necessarily increase, since a number of bin-
ding compounds incorporated through biosolids coun-
teract the leaching process. For example, Withers et
al. (2001) measured runoff P from field plots that had
previously received P from different sources, and con-
cluded that there was a lower risk of P runoff follo-
wing application of biosolid compared with other agri-
cultural P amendments at similar P application rates.
Al- and Fe-rich biosolids have been found to increase
the amorphous soil fraction, which is considered to be
a measure of the P sorption capacity of acidic soils
(Pote et al., 1996; Maguire et al., 2000). In calcareous
soils, P solubility is also influenced by Ca precipita-
tion (Pierzynski et al., 2005). Therefore, biosolids can
increase not only total P content of the soil but also
its P sorption capacity. Addition of wastes rich in Fe
and Al was also found to dramatically reduce biosolid
P leaching and runoff from high-P soils (Haustein et
al., 2000; Elliott et al., 2002b).
Different studies showed that WEP is highly cor-
related to runoff P and leachate P in manures and
manure-amended soils, and has been proposed as a
useful indicator of environmental P loss from waste-
amended soils (Kleinman et al., 2002; Brandt and
Elliott, 2003; Brandt et al., 2004). As total P varies
among organic amendments, percent WEP (PWEP
= WEP × 100/total P) is used to compare the en-
vironmentally relevant P in relation to total P. For
most biosolids, PWEP is found to be less than 5%
(Brandt et al., 2004), while Fe or Al-produced bioso-
lids have PWEP values of less than 0.5% (Brandt et al.,
2004). Conversely, BPR biosolids typically have greater
soluble P and PWEP (≥ 14%) than conventionally
produced biosolids (Brandt et al., 2004). O’Connor
and Chinault (2008) concluded that biosolid PWEP
is a very good indicator of the way that biosolid P
may affect the environment when land applied, and
proposed that biosolids with PWEP values higher
than 14% should be assumed to have a larger poten-
tial negative environmental impact than biosolids with
PWEP values less than 14%.
Until recently, P has been thought to be so strong-
ly bound to the soil matrix that its vertical movement
through the soil profile is insignificant (Kostyanovsky
et al., 2011; Oladeji et al., 2013). Since most soils have
an appreciable P-sorbing capacity, P that may move
down the soil profile generally becomes fixed in the
subsoil. Hence, P leaching is not considered an im-
portant P loss mechanism (Miller, 2008). Therefore,
numerous studies concluded that P vertical movement
through the soil profile in biosolid-amended soils was
negligible, despite the high rates of P applied or soil
texture. However, over application of P to soils with
low P sorption capacity may significantly increase P
vertical movement and leaching. Leaching of P from
organic amendments may occur in both organic and
inorganic forms (Eghball et al., 1996). Complexation
of P with mobile organic compounds may favour the
deep transport of organic forms of P, even through lay-
ers with a great P adsorption capacity. In a column
experiment using a fine sandy soil amended with six
conventional treated biosolids at N-based rates, P lea-
ching was less than 1% of P applied, and not statistical-
ly different from unamended soils. In contrast, 21% of
the P applied was found to leach in columns amended
with TSP (Elliott et al., 2002a). Rydin and Otabbong
(1997) leached 35 mm of water through soils amended
with either Fe- or Al-treated biosolids and found that
less P was released from Fe-treated biosolids compared
with Al-treated biosolids. When only biological treat-
ment processes are involved, biosolids are usually re-
ported to have a relatively high risk of P leaching than
soils amended with biosolids stabilized with high levels
of Fe or Al (Kyle and McClintock, 1995). This varia-
tion is most likely due to differences in solubility in the
forms of inorganic P resulting from different WWTPs.
Thermal treatment of biosolids was also found to sig-
nificantly reduce P leaching in sandy soils (O’Connor
et al., 2002), because heating increases the rate of reac-
tion of simple, readily dissolvable phosphate minerals
to more complex, less soluble forms.
Runoff losses of P may occur in particulate and
soluble P forms. Particulate P is associated with soil
particles, such as minerals or organic matter. Runoff
of particulate P may be decreased through different
management practices (Kleinman et al., 2011; Dodd
and Sharpley, 2015), but soluble inorganic P loss is of
concern, especially in low P-retaining soils (McDowell
et al., 2004; Shober and Sims, 2007). Penn and Sims
(2002) noted that runoff P is very high (0.064 mg L−1
)
from soils amended with BPR biosolids, followed by Fe
and lime-treated biosolids (0.039 mg L−1
), no-Fe and
no-lime biosolids (0.014 9 mg L−1
), and Fe-treated and
no-lime biosolids (0.002 mg L−1
) at equal rates of to-
tal P (200 kg ha−1
). The reason for this situation is
that P amendments which do not add P-binding ele-
ments (e.g., BPR) can be expected to increase P sa-
turation, reduce P-binding strength, and release more
10. 10 S. I. TORRI et al.
P to runoff (Holford et al., 1997; Siddique and Robin-
son, 2003). When only biological treatment processes
are involved, biosolids are usually reported to have a
relatively high risk of off-site P migration than those
stabilized with high levels of Fe or Al (Kyle and Mc-
Clintock, 1995). Field studies of White et al. (2010)
have shown that runoff P for the soils amended with
Fe-treated biosolids is not significantly different from
that for the unamended control soil despite biosolid
application rates. The soils amended with lime-treated
biosolids produce the largest runoff P, the soils amen-
ded with Fe and lime-treated biosolid are intermediate,
and those amended with Fe-treated biosolids are the
lowest. These have been attributed to the dissolution
of calcium-bound P (Ca-P) species in acidic soils af-
ter land application of biosolids (Leytem et al., 2004;
White et al., 2010). Most research has shown that the
addition of metal salts at the WWTP reduces solu-
ble P losses by runoff (Penn and Sims, 2002; Agyin-
Birikorang et al., 2008; Alleoni et al., 2008). Elliott et
al. (2005) reported that with additions of Fe and/or Al
during WWT processes, like heat drying, runoff P los-
ses produced are not statistically different between the
amended and unamended soils. Other researchers re-
ported that some biosolid-amended soils produced less
runoff P losses than the unamended soils (Brandt and
Elliott, 2003; O’Connor and Elliott, 2006).
A peculiar environmental behaviour of soil P dy-
namics is the so-called P leaching breakpoint, first
observed in the long-term Broadbalk Experiment at
Rothamsted, UK (Heckrath et al., 1995). The P lea-
ching breakpoint indicates an abrupt change occurring
in the Olsen P fraction when it is in the range of 21–104
mg P kg−1
. The occurrence of a P leaching breakpoint
has been confirmed for other soils under various mana-
gement practices (Brookes and Hesketh, 1998; Jordan
et al., 2000). To our knowledge, the existence of a P
leaching breakpoint in biosolid-amended soils has not
been studied. This aspect may be important from the
perspective of utilizing biosolid P, as the higher or-
ganic matter content of biosolid-amended soils should
theoretically saturate P sorption sites, leading to po-
tentially greater P losses compared to those of the soils
amended with chemical fertilizers.
CONCLUSIONS AND PERSPECTIVES
Phosphate rock is a finite, non-renewable resource,
and its reserves are progressively becoming scarce. Re-
cycling P from biosolids is a valuable feedstock for
agronomic purposes to enhance and sustain society,
and represents the best environmental option so far.
However, land application of biosolids is becoming in-
creasingly constrained by the amounts of P addition in
sensitive agronomic scenarios. It is generally accepted
that leaching of P from biosolid-amended soils is mini-
mal. However, the risk of soluble inorganic P transport
in surface runoff after land application of biosolids is
of major concern. The WWT processes clearly influ-
ence differences in soil P solubility and soil P speci-
ation after land application of biosolids. In sensitive
scenarios, Fe- or Al-treated biosolids reduce the risk
of P transport. However, if runoff P is not a major
concern and biosolids are primarily applied to provide
available P to crops, the standard BPR process or a
process that involves the addition of lime instead of
Fe and Al oxides may be adequate. In all cases, it is
critical to control sources of nonpoint P pollution of
surface- and groundwater. While in natural soils, the
phosphatase activity likely plays an important role in
P mineralization and phytoavailability, other microbio-
logical and biochemical activities likely play predomi-
nant roles in P mineralization and fate. The use of
whole cell biosensors specifically signalling to P up-
take by soil microorganisms is a promising biotech-
nology for the assessment of the P bioavailability in
soil which can improve understanding of P released by
biosolid application. Further research on P forms in
the various biosolids, the use of biotechnologies for the
assessment of the P bioavailable fractions such as the
whole cell biosensors, and the analysis of genetic plant
responses to soil biosolid amendment can improve the
understanding of potential P uptake by crops and opti-
mal use of P-rich biosolids for sustainable agriculture.
Harmonization of the regulation on the use of bioso-
lids in agriculture, currently mainly based on N and
pollutant contents, may also contribute to a better P
balance in agriculture.
REFERENCES
Abad E, Mart´ınez K, Planas C, Palacios O, Caixach J, Rivera
J. 2005. Priority organic pollutant assessment of sludges for
agricultural purposes. Chemosphere. 61: 1358–1369.
Agyin-Birikorang S, O’Connor G A, Brinton S R. 2008. Evalu-
ating phosphorus losses from a Florida spodosol as affected
by phosphorus-source application methods. J Environ Qual.
37: 1180–1189.
Ahumada I, Sep´ulveda K, Fern´andez P, Ascar L, Pedraza C,
Richter P, Brown S. 2014. Effect of biosolid application to
Mollisol Chilean soils on the bioavailability of heavy metals
(Cu, Cr, Ni, and Zn) as assessed by bioassays with sunflower
(Helianthus annuus) and DGT measurements. J Soil Sedi-
ment. 14: 886–896.
Akhtar M, McCallister D L, Francis D D, Schepers J S. 2005.
Manure source effect on soil phosphorus fractions and their
distribution. Soil Sci. 170: 183–190.
Akhtar N, Inam A, Khan N A. 2012. Effects of city wastewater
11. BIOSOLID APPLICATION AND GLOBAL P RECYCLE 11
on the characteristics of wheat with varying doses of nitro-
gen, phosphorus, and potassium. Recent Res Sci Technol. 4:
18–29.
Al-Dhumri S, Beshah F H, Porter N A, Meehan B, Wrigley R.
2013. An assessment of the guidelines in Victoria, Austra-
lia, for land application of biosolids based on plant-available
nitrogen. Soil Res. 51: 529–538.
Alleoni L R F, Brinton S R, O’Connor G A. 2008. Runoff and
leachate losses of phosphorus in a sandy Spodosol amended
with biosolids. J Environ Qual. 37: 259–265.
Alleoni L R F, Fernandes A R, Jord˜ao C B. 2012. Phosphorus
availability in an Oxisol amended with biosolids in a long-
term field experiment. Soil Sci Soc Am J. 76: 1678–1684.
Allison S D, Vitousek P M. 2005. Responses of extracellular
enzymes to simple and complex nutrient inputs. Soil Biol
Biochem. 37: 937–944.
Anand K, Kumari B, Mallick M A. 2016. Phosphate solubilizing
microbes: An effective and alternative approach as biofertili-
zers. J Pharm Pharm Sci. 8: 37–40.
Athamenh B M, Salem N M, El-Zuraiqi S M, Suleiman W, Rusan
M J. 2015. Combined land application of treated wastewa-
ter and biosolids enhances crop production and soil fertility.
Desalin Water Treat. 53: 3283–3294.
Barbarick K A, Ippolito J A. 2007. Nutrient assessment of a
dryland wheat agroecosystem after 12 years of biosolids ap-
plications. Agron J. 99: 715–722.
Barrow N J, Bolland M D A. 1990. A comparison of methods
for measuring the effect of level of application on the relative
effectiveness of two fertilizers. Fert Res. 26: 1–10.
Barrow N J, Campbell N A. 1972. Methods of measuring resi-
dual value of fertilisers. Aust J Exp Agr. 12: 502–510.
Beck M A, Sanchez P A. 1994. Soil phosphorus fractions dyna-
mics during 18 years of cultivation on a Typic Paleudult. Soil
Sci Soc Am J. 58: 1424–1431.
Bøen A, Haraldsen T K, Krogstad T. 2013. Large differences in
soil phosphorus solubility after the application of compost
and biosolids at high rates. Acta Agr Scand B. 63: 473–482.
Borggaard O K, Jørgensen S S, Moberg J P, Raben-Lange B.
1990. Influence of organic matter on phosphate adsorption
by aluminium and iron oxides in sandy soils. J Soil Sci. 41:
443–449.
Brandt R C, Elliott H A, O’Connor G A. 2004. Water-extra-
ctable phosphorus in biosolids: Implications for land-based
recycling. Water Environ Res. 76: 121–129.
Brandt R C, Elliott H A. 2003. Phosphorus runoff losses from
surface-applied biosolids and dairy manure. In Water Envi-
ronment Federation (ed.) Proc. 17th Annual Residuals and
Biosolids Manage. Conf., Baltimore. Water Environment Fe-
deration, Alexandria. pp. 19–22.
Brookes P C, Hesketh N. 1998. Developing an indicator to pre-
dict the risk of soil phosphorus movement in drainage water.
In Foy R H, Dils R (eds.) Practical and innovative Measures
for the Control of Agricultural Phosphorus Losses to Water.
OECD Workshop, 16–19 June 1998. OECD, Antrim. pp. 16–
21.
Burkitt L, Gourley C, Sale P. 2001. Temporal changes in Olsen
phosphorus (P) concentrations when P fertiliser rates were
applied to nine different soil types of varying P buffering ca-
pacity. In Haygarth P M, Condron L M, Butler P J, Chisholm
J S (eds.) Connecting Phosphorus Transfer from Agriculture
to Impacts in Surface Waters. Proceedings of the Interna-
tional Phosphorus Transfer Workshop (IPTW 2001). Insti-
tute of Grassland and Environmental Research, Plymouth
University, Devon. pp. 30–31.
Carpenter-Boggs L, Stahl P D, Lindstrom M J, Schumacher T E.
2003. Soil microbial properties under permanent grass, con-
ventional tillage, and no-till management in South Dakota.
Soil Till Res. 71: 15–23.
Celi L, Marsan A, Barberis E. 2001. Some molecular aspects
of organic phosphorus dynamics in soil. In Haygarth P M,
Condron L M, Butler P J, Chisholm, J S (eds.) Connecting
Phosphorus Transfer from Agriculture to Impacts in Surface
Waters. Proceedings of the International Phosphorus Trans-
fer Workshop (IPTW 2001). Institute of Grassland and En-
vironmental Research, Plymouth University, Devon. pp. 33–
34.
Chen H, Wang D, Li X, Yang Q, Luo K, Zeng G. 2013. Biolo-
gical phosphorus removal from real wastewater in a sequen-
cing batch reactor operated as aerobic/extended-idle regime.
Biochem Eng J. 77: 147–153.
Christie P, Easson D L, Picton J R, Love S C P. 2001. Agro-
nomic value of alkaline-stabilized biosolids for spring barley.
Agron J. 93: 144–151.
Clark D L, Hunt G, Kasch M S, Lemonds P J, Moen G M, Neeth-
ling J. 2010. Nutrient Management: Regulatory Approach-
es to Protect Water Quality. Volume 1. Review of Existing
Practices. Water Environment & Reuse Foundation (WER-
F), Alexandria. pp. 5830–5835.
Cleveland C C, Liptzin D. 2007. C:N:P stoichiometry in soil: is
there a “Redfield ratio” for the microbial biomass? Biogeo-
chemistry. 85: 235–252.
Codling E E. 2014. Long-term effects of biosolid-amended soils
on phosphorus, copper, manganese and zinc uptake by wheat.
Soil Sci. 179: 21–27.
Cogger C G, Bary A I, Kennedy A C, Fortuna A M. 2013a.
Long-term crop and soil response to biosolids applications in
dryland wheat. J Environ Qual. 42: 1872–1880.
Cogger C G, Bary A I, Myhre E A, Fortuna A M. 2013b. Bio-
solids applications to tall fescue have long-term influence on
soil nitrogen, carbon, and phosphorus. J Environ Qual. 42:
516–522.
Cordell D, Neset T S. 2014. Phosphorus vulnerability: a quali-
tative framework for assessing the vulnerability of national
and regional food systems to the multi-dimensional stressors
of phosphorus scarcity. Global Environ Chang. 24: 108–122.
Cordell D. 2010. The Story of Phosphorus: Sustainability im-
plications of Global Phosphorus Scarcity for Food Security.
Doctoral Thesis. Collaborative Ph.D. between the Institute
for Sustainable Futures, University of Technology, Sydney
(UTS) and Department of Water and Environmental Studies,
Link¨oping University, Sweden. Link¨oping University Press,
Link¨oping.
Corrˆea R S. 2002. Beneficial use of biosolids based on their N and
P fertilising value. Ph.D. Thesis, University of Melbourne.
Corrˆea R S. 2004. Efficiency of five biosolids to supply nitro-
gen and phosphorus to ryegrass. Pesqui Agropecu Bras. 39:
1133–1139.
Corrˆea R S, Bento M A B. 2010. Quality of a revegetated mine
spoil in the Federal District of Brazil. Rev Bras Cien Solo.
34: 1435–1443.
Corrˆea R S, Silva D J. 2016. Effectiveness of five biosolids as
nitrogen sources to produce single and cumulative ryegrass
harvests in two Australian soils. Rev Bras Cien Solo. 40:
e0150216.
Corrˆea R S, White R E, Weatherley A J. 2005. Biosolids effec-
tiveness to yield ryegrass based on their nitrogen content.
Sci Agr. 62: 274–280.
Corrˆea R S, White R E, Weatherley A J. 2012. Effects of sewage
sludge stabilization on organic-N mineralization in two soils.
12. 12 S. I. TORRI et al.
Soil Use Manage. 28: 12–18.
Commission of the European Communities (CEC). 1986. Coun-
cil Directive of 12 June 1986 on the Protection of the Envi-
ronment, and in Particular of the Soil, when Sewage Sludge
is Used in Agriculture (86/278/EEC). Official Journal of the
European Communities No. L 181. Office for Official Publi-
cations of the European Communities, Luxembourg.
Darwent M J, Paterson E, McDonald A J S, Tomos A D. 2003.
Biosensor reporting of root exudation from Hordeum vulgare
in relation to shoot nitrate concentration. J Exp Bot. 54:
325–334.
De-Bashan L E, Bashan Y. 2004. Recent advanced in removing
phosphorus from wastewater and its future use as fertilizer
(1997–2003). Water Res. 38: 4222–4246.
Delgado A, Torrent J. 1997. Phosphate-rich soils in the European
Union: estimating total plant-available phosphorus. Eur J
Agron. 6: 205–214.
Dick W A, Tabatabai M A. 1992. Significance and potential u-
ses of soil enzymes. In Metting F B Jr (ed.) Soil Microbial
Ecology. Marcel Dekker, New York. pp. 95–127.
Dodd R J, Sharpley A N. 2015. Conservation practice effective-
ness and adoption: unintended consequences and implica-
tions for sustainable phosphorus management. Nutr Cycl A-
groecosys. 104: 1–20.
Dodor D E, Tabatabai M A. 2003. Effect of cropping systems on
phosphatases in soils. J Plant Nutr Soil Sci. 66: 7–13.
Ebeling A M, Cooperband L R, Bundy L G. 2003. Phosphorus
availability to wheat from manures, biosolids, and an inor-
ganic fertilizer. Commun Soil Sci Plant Anal. 34: 1347–1365.
European Communities (EC). 2000. Directive 2000/60/EC of
the European Parliament and of the Council of 23 October
2000 Establishing a Framework for Community Action in
the Field of Water Policy. Official Journal of the European
Communities No. L 327. Office for Official Publications of
the European Communities, Luxembourg.
European Communities (EC). 2006. Directive 2006/118/EC of
the European Parliament and the Council of 12th of Decem-
ber 2006 on the Protection of Ground Water against Pol-
lution and Deterioration. Official Journal of the European
Communities No. L 372/19. Office for Official Publications
of the European Communities, Luxembourg.
Eghball, B, Binford G D, Baltensperger D D. 1996. Phospho-
rus movement and adsorption in a soil receiving long-term
manure and fertilizer application. J Environ Qual. 25: 1339–
1343.
Elliott H A, O’Connor G A, Brinton S. 2002a. Phosphorus lea-
ching from biosolids-amended sandy soils. J Environ Qual.
31: 681–689.
Elliot H A, O’Connor G A, Lu P, Brinton S. 2002b. Influence
of water treatment residuals on phosphorus solubility and
leaching. J Environ Qual. 31: 1362–1369.
Elliott H A, Brandt R C, O’Connor G A. 2005. Runoff phospho-
rus losses from surface-applied biosolids. J Environ Qual. 34:
1632–1639.
Elliott H A, O’Connor G. 2007. Phosphorus management for
sustainable biosolids recycling in the United States. Soil Bi-
ol Biochem. 39: 1318-1327.
Elser J J. 2012. Phosphorus: A limiting nutrient for humanity?
Curr Opin Biotechnol. 23: 833–838.
Esteller M V, Mart´ınez-Vald´es H, Garrido S, Uribe Q. 2009.
Nitrate and phosphate leaching in a Phaeozem soil treated
with biosolids, composted biosolids and inorganic fertilizers.
Waste Manage. 29: 1936–1944.
Frossard E, B¨unemann E, Jansa J, Oberson A, Feller C. 2009.
Concepts and practices of nutrient management in agro-
ecosystems: can we draw lessons from history to design fu-
ture sustainable agricultural production systems? Die Bo-
denkultur. 60: 43–60.
Frossard E, Sinaj S, Dufour P. 1996a. Phosphorus in urban
sewage sludges as assessed by isotopic exchange. Soil Sci Soc
Am J. 60: 179–182.
Frossard E, Sinaj S, Zhang L M, Morel J L. 1996b. The fate of
sludge phosphorus in soil-plant systems. Soil Sci Soc Am J.
60: 1248–1253.
Garc´ıa-Orenes F, Guerrero C, Mataix-Solera J, Navarro-Pedre˜no
J, G´omez I, Mataix-Beneyto J. 2005. Factors controlling the
aggregate stability and bulk density in two different degraded
soils amended with biosolids. Soil Till Res. 82: 65–76.
Gellatly K S, Moorhead G B G, Duff S M G, Lefebvre D D,
Plaxton W C. 1994. Purification and characterization of a
potato tuber acid phosphatase having significant phosphoty-
rosine phosphatase activity. Plant Physiol. 106: 223–232.
Gilbert G A, Knight J D, Vance C P, Allan D L. 1999. Acid phos-
phatase activity in phosphorus-deficient white lupin roots.
Plant Cell Environ. 22: 801–810.
Gilmour J T, Cogger C G, Jacobs L W, Evanylo G K, Sullivan
D M. 2003. Decomposition and plant-available nitrogen in
biosolids. J Environ Qual. 32: 1498–1507.
Goldstein A H, Baertlein D A, McDaniel R G. 1988. Phosphate
starvation inducible metabolism in Lycopersicon esculentum.
Plant Physiol. 87: 711–715.
Gomes N C M, Landi L, Smalla K, Nannipieri P, Brookes P
C, Renella G. 2010. Effects of Cd and Zn enriched sewage
sludge on soil bacterial and fungal com-munities. Ecotox En-
viron Safe. 73: 1255–1263.
Grady C P L Jr, Daigger G T, Love N G, Filipe C D M. 2011. Bi-
ological Wastewater Treatment. 3rd Edn. CRC Press, New
York.
Grant C, Bittman S, Montreal M, Plenchette C, Morel C. 2005.
Soil and fertilizer phosphorus: effects on plant P supply and
mycorrhizal development. Can J Plant Sci. 85: 3–14.
Haney C H, Samuel B S, Bush J, Ausubel F M. 2015. Asso-
ciations with rhizosphere bacteria can confer an adaptive ad-
vantage to plants. Nat Plants. 1: 15051.
Hansen L G, Chaney R L. 1984. Environmental and food chain
effects of the agricultural use of sewage sludges. In Hodges R
D (ed.) Reviews in Environmental Toxicology. Elsevier Sci.
Publ., Amsterdam. pp. 103–172.
Haustein G K, Daniel T C, Miller D M, Moore P A Jr, McNew
R W. 2000. Aluminum-containing residuals influence high-
phosphorus soils and runoff water quality. J Environ Qual.
29: 1954–1959.
Haynes R J, Murtaza G, Naidu R. 2009. Inorganic and organic
constituents and contaminants of biosolids: implications for
land application. Adv Agron. 104: 165–267.
He Z, Zhang H, Toor G S, Dou Z, Honeycutt C W, Haggard B
E, Reiter M S. 2010. Phosphorus distribution in sequentially
extracted fractions of biosolids, poultry litter, and granulated
products. Soil Sci. 175: 154–161.
Heckrath G., Brookes P C, Poulton P R, Goulding K W T. 1995.
Phosphorus leaching from soils containing different phospho-
rus concentrations in the Broadbalk experiment. J Environ
Qual. 4: 904–910.
Heffer P. 2013. Phosphate Policy Issues from the Industry’s Per-
spective. The 1st Global TraPs Conference, Beijing.
Hens M, Merckx R. 2001. Funcional charatcertization of collo-
idal phosphorus species in the soil solution of sandy soils.
Environ Sci Technol. 35: 493–500.
Hilton J, O’Hare M, Bowes M J, Jones J I. 2006. How green is
my river? A new paradigm of eutrophication in rivers. Sci
13. BIOSOLID APPLICATION AND GLOBAL P RECYCLE 13
Total Environ. 365: 66–83.
Hinedi Z R, Chang A C, Lee R W K. 1989. Characterization of
phosphorus in sludge extracts using phosphorus-31 nuclear
magnetic resonance spectroscopy. J Environ Qual. 18: 323–
329.
Hogan F, McHugh M, Morton S. 2001. Phosphorus availability
for beneficial use in biosolids products. Environ Technol. 22:
1347–1353.
Holford I C R, Hird C, Lawrie R. 1997. Effects of animal efflu-
ents on the phosphorus sorption characteristics of soils. Aust
J Soil Res. 35: 365–373.
Hooda P S, Rendell A R, Edwards A C, Withers P J A, Aitken
M N, Truesdale V W. 2000. Relating soil phosphorus indices
to potential phosphorus release to water. J Enviro Qual. 29:
1166–1171.
Hosseinpur A, Pashamokhtari H. 2013. The effects of incubation
on phosphorus desorption properties, phosphorus availabi-
lity, and salinity of biosolids-amended soils. Environ Earth
Sci. 69: 899–908.
Ippolito J A, Barbarick K A, Norvell K L. 2007. Biosolids impact
soil phosphorus accountability, fractionation, and potential
environmental risk. J Environ Qual. 36: 764–772.
Islas-Espinoza M, Sol´ıs-Mej´ıa L, Esteller M V. 2014. Phosphorus
release kinetics in a soil amended with biosolids and vermi-
compost. Environ Earth Sci. 71: 1441–1451.
Jasinski S M. 2013. Phosphate rock. In U.S. Geological Survey
(ed.) Mineral. Yearbook. U.S. Government Publishing Of-
fice, Washington, D.C. pp. 56.1–56.11.
Jenkins D, Ferguson J F, Menar A B. 1971. Chemical processes
for phosphorus removal. Water Res. 5: 369–387.
Jenkins D, Horwath W R, Stutz-McDonald S. 2000. Phosphate
leaching from biosolids/soils mixtures. In Water Environ-
ment Federation (ed.) Proceedings of the Water Environment
Federation, Anaheim, CA., 14–18 Oct. 2000. Water Environ-
ment Federation, Alexandria. pp. 56–70.
Jin V L, Johnson M V V, Haney R L, Arnold J G. 2011. Po-
tential carbon and nitrogen mineralization in soils from a
perennial forage production system amended with class B
biosolids. Agr Ecosyst Environ. 141: 461–465.
Johnson D D, Broadbent F E. 1952. Microbial turnover of phos-
phorus in soil. Soil Sci Soc Am J. 16: 56–59.
Jokinen R. 1990. Effect of phosphorus precipitation chemicals
on characteristics and agricultural value of municipal sewage
sludges. Acta Agr Scand. 40: 141–147.
Jordan C, McGuckin S O, Smith R V. 2000. Increased predicted
losses of phosphorus to surface waters from soils with high
Olsen-P concentrations. Soil Use Manage. 16: 27–35.
Jord´an M M, Rinc´on-Mora B, Almendro-Candel M B. 2016.
Heavy metal distribution and electrical conductivity mea-
surements in biosolid pellets. J Soil Sediment. 16: 1176–
1182.
Keating C, Chin J P, Hughes D, Manesiotis P, Cysneiros
D, Mahony T, Smith C J, McGrath J W, O’Flaherty V.
2016. Biological phosphorus removal during high-rate, low-
temperature, anaerobic digestion of wastewater. Front Mi-
crobiol. 7: 226–239.
Kelly T D, Matos G R. 2013. Historical statistics for mineral and
material commodities in the United States. U.S. Geological
Survey Data Series 140. Available online at http://pubs.
usgs.gov/ds/2005/140/ (verified on November 10, 2016).
Kleinman P J A, Sharpley A N, Moyer B G, Elwinger G F. 2002.
Effect of mineral and manure phosphorus sources on runoff
phosphorus. J Environ Manage. 31: 2026–2033.
Kleinman P J A, Sharpley A N, Buda A R, McDowell R W, Allen
A L. 2011. Soil controls of phosphorus in runoff: Management
barriers and opportunities. Can J Soil Sci. 91: 329–338.
Koch B, Worm J, Jensen L E, Højberg O, Nybroe O. 2001.
Carbon limitation induces S-dependent gene expression in
Pseudomonas fluorescens in soil. Appl Environ Microb. 67:
3363–3370.
Kostyanovsky K I, Evanylo G K, Lasley K K, Daniels W L,
Shang C. 2011. Leaching potential and forms of phosphorus
in deep row applied biosolids underlying hybrid poplar. Ecol
Eng. 37: 1765–1771.
Kowaljow E, Mazzarino M J, Satti P, Jim´enez-Rodr´ıguez C.
2010. Organic and inorganic fertilizer effects on a degraded
Patagonian rangeland. Plant Soil. 332: 135–145.
Kragelund L, Hosbond C, Nybroe O. 1997. Distribution of
metabolic activity and phosphate starvation response of lux-
tagged Pseudomonas fluorescens reporter bacteria in the bar-
ley rhizosphere. Appl Environ Microb. 63: 4920–4928.
Krogstad T, Sogn T A, Asdal A, Sæbø A. 2005. Influence of
chemically and biologically stabilized sewage sludge on plant-
available phosphorus in soil. Ecol Eng. 25: 51–60.
Kroiss H. 2004. What is the potential for using the resources in
sludge? Water Sci Technol. 49: 1–10.
Kruse J, Abraham M, Amelung W, Baum C, Bol R, K¨uhn O,
Lewandowski H, Niederberger J, Oelmann Y, R¨uger C, Sant-
ner J, Siebers M, Siebers N, Spohn M, Vestergren J, Vogts
A, Leinweber P. 2015. Innovative methods in soil phosphorus
research: A review. J Plant Nutr Soil Sci. 178: 43–88.
Kyle M A, McClintock S A. 1995. The availability of phosphorus
in municipal wastewater sludge as a function of the phospho-
rus removal process and the sludge treatment method. Water
Environ Res. 67: 282–299.
Larney F J, Angers D A. 2012. The role of organic amendments
in soil reclamation: a review. Can J Soil Sci. 92: 19–38.
Lee C C, Lin S D. 2007. Handbook of Environmental Enginee-
ring Calculations. McGraw-Hill Professional, New York.
Leytem A B, Sims J T, Coale F J. 2004. Determination of phos-
phorus source coefficients for organic phosphorus sources:
Laboratory studies. J Environ Qual. 33: 380–388.
Liu Y, Villalba G, Ayres R U, Schroder H. 2008. Global phos-
phorus flows and environmental impacts from a consumption
perspective. J Ind Ecol. 12: 229–247.
Liu Z, Zhao Q, Lee D J, Yang N. 2008. Enhancing phospho-
rus recovery by a new internal recycle seeding MAP reactor.
Bioresource Technol. 99: 6488–6493.
Lowe J J, Rasmussen S O, Bjorck S, Hoek W Z, Steffensen J
P, Walker M J C, Yu Z C, Grp I. 2008. Synchronisation of
palaeoenvironmental events in the North Atlantic region du-
ring the Last Termination: A revised protocol recommended
by the INTIMATE group. Quaternary Sci Rev. 27: 6–17.
Lu P, O’Connor G A. 2001. Biosolids effects on phosphorus re-
tention and release in some sandy soils. J Environ Qual. 30:
1059–1063.
Lu Q, He Z L, Stoffella P J. 2012. Land application of biosolids
in the USA: a review. Appl Environ Soil Sci. 1: 1–11.
MacDonald G K, Bennett E M, Potter P A, Ramankutty N.
2011. Agronomic phosphorus imbalances across the world’s
croplands. Proc Natl Acad Sci USA. 108: 3086–3091.
Magesan G N, Wang H. 2003. Application of municipal and in-
dustrial residuals in New Zealand forests: an overview. Aust
J Soil Res. 41: 557–569.
Maguire R O, Chardon W J, Simard R R. 2005. Assessing po-
tential environmental impacts of soil phosphorus by soil tes-
ting. In Sims J T, Sharpley A N (eds.) Phosphorus: Agricul-
ture and the Environment. American Society of Agronomy
(ASA), Crop Science Society of America (CSSA) and Soil
Science Society of America (SSSA), Madison. pp. 145–180.
14. 14 S. I. TORRI et al.
Maguire R O, Hesterberg D L, Gernat A, Anderson K, Wineland
M, Grimes J. 2006. Liming poultry litter manures to decrease
soluble phosphorus and suppress the bacteria population. J
Environ Qual. 35: 849–857.
Maguire R O, Sims J T, Coale F J. 2000. Phosphorus solubility
in biosolids-amended farm soils in the mid-Atlantic region of
the USA. J Environ Qual. 29: 1225–1233.
Maguire R O, Sims J T, Dentel S K, Coale F J, Mah J T. 2001.
Relationships between biosolids treatment process and soil
phosphorus availability. J Environ Qual. 30: 1023–1033.
Mart´ınez K, Abad E, Palacios O, Caixach J, Rivera J. 2007.
Assessment of polychlorinated dibenzo-p-dioxins and diben-
zofurans in sludges according to the European environmental
policy. Environ Int. 33: 1040–1047.
McDowell R W, Biggs B J F, Sharpley A N, Nguyen L. 2004.
Connecting phosphorus loss from agricultural landscapes to
surface water quality. Chem Ecol. 20: 1–40.
McLaughlin M J. 1984. Land application of sewage sludge: Phos-
phorus considerations. S Afr J Plant Soil. 1: 21–29.
Michael N, Bradshaw A D, Hall J E. 1991. The value of fertili-
zer, surface applied and injected sewage sludge to vegetation
established on reclaimed colliery spoil suffering from regres-
sion. Soil Use Manage. 7: 233–239.
Midgley J F. 2012. Proposed Recovery of Phosphate Enriched
Sediments from the Marine Mining Licence Area no. 170
off Walvis Bay Namibia. Sandpiper Project. Appendix 5.
Namibian Marine Phosphate (PTY) Ltd. J Midgley & Asso-
ciates, Whindoek.
Miller M. 2008. Characterizing the long-term lability of biosolids-
phosphorus. M.S. Thesis, University of Florida.
Mitchell D S, Edwards A C, Ferrier R C. 2000. Changes in fluxes
of N and P in water draining a stand of Scots pine treated
with sewage sludge. Forest Ecol Manag. 139: 203–213.
Montalvo D, Degryse F, McLaughlin M J. 2015. Natural col-
loidal P and its contribution to plant P uptake. Environ Sci
Technol. 49: 3427–3434.
Moorhead D L, Sinsabaugh R L. 2000. Simulated patterns of lit-
ter decay predict patterns of extracellular enzyme activities.
Appl Soil Ecol. 14: 71–79.
Nannipieri P, Giagnoni L, Renella G, Puglisi E, Ceccanti B, Mas-
ciandaro G, Fornasier F, Marinari S. 2012. Soil enzymology:
Classical and molecular approaches. Biol Fert Soils. 48: 743–
762.
Nanzyo M. 1986. Infrared spectra of phosphate sorbed on iron
hydroxide gel and the sorption products. Soil Sci Plant Nutr.
32: 51–58.
O’Connor G A, Chinault S L. 2006. Environmental impacts of
land applying biosolids. Fla Wat Res J. 5: 50–54.
O’Connor G A, Elliott H A, Sarkar D, Graetz D R. 2002. Chara-
cterizing Forms, Solubilities, Bioavailabilities, and Minera-
lization Rates of Phosphorus in Biosolids, Commercial Fer-
tilizers, and Manures. Interim Report, Project 99-PUM-2T.
Water Environment Research Foundation, Alexandria.
O’Connor G A, Sarkar D. 1999. Fate of Land Applied Residuals-
Bound Phosphorus. DEP WM 661. Florida Environmental
Protection Agency, Tallahassee.
O’Connor G A, Elliott H A. 2006. The Agronomic and Environ-
mental Availability of Biosolids-P (Phase II). Rep. 99-PUM-
2T. Water Environment Research Foundation, Alexandria.
O’Connor G A, Sarkar D, Brinton S R, Elliott H A, Martin F G.
2004. Phytoavailability of biosolids phosphorus. J Environ
Qual. 33: 703–712.
Oladeji O O, Tian G, Cox A E, Granato T C, O’Connor C,
Abedin Z, Pietz R I. 2013. Effect of long-term application of
biosolids for mine land reclamation on groundwater chemi-
stry: Nutrients and other selected qualities. J Environ Qual.
42: 94–102.
Pascual J A, Garc´ıa C, Hernandez T. 1999. Lasting microbio-
logical and biochemical effects of the addition of municipal
solid waste to an arid soil. Biol Fert Soils. 30: 1–6.
Pautler M C, Sims J T. 2000. Relationships between soil test
phosphorus, soluble phosphorus, and phosphorus saturation
in Delaware soils. Soil Sci Soc Am J. 64: 765–773.
Penn C J, Sim J T. 2002. Phosphorus forms in biosolids-amended
soils and losses in runoff: effects of wastewater treatment pro-
cess. J Environ Qual. 31: 1349–1361.
Pierzynski G M, McDowell R W, Sims J T. 2005. Chemistry,
cycling, and potential movement of inorganic phosphorus in
soils. In Sims J T, Sharpley A N (eds.) Phosphorus: Agricul-
ture and the Environment. American Society of Agronomy,
Madison. pp. 53–86.
Pote D H, Daniel T C, Sharpley A N, Moore P A, Edwards D
R, Nichols D J. 1996. Relating extractable soil phosphorus to
phosphorus losses in runoff. Soil Sci Soc Am J. 60: 855–859.
Qin C, Liu H, Liu L, Smith S, Sedlak D L, Gu A Z. 2015. Bio-
availability and characterization of dissolved organic nitrogen
and dissolved organic phosphorus in wastewater effluents. Sci
Total Environ. 511: 47–53.
Quinton J N, Govers G, Oost K V, Bardgett R D. 2010. The
impact of agricultural soil erosion on biogeochemical cycling.
Nat Geosci. 3: 311–314.
Renella G, Chaudri A M, Falloon C M, Landi L, Nannipieri P,
Brookes P C. 2007a. Effects of Cd, or Zn, or both on soil
microbial biomass and activity in a clay loamsoil. Biol Fert
Soils. 43: 751–758.
Renella G, Landi L, Ascher J, Ceccherini M T, Pietramellara
G, Nannipieri P. 2006. Phosphomonoesterase production and
persistence and composition of bacterial communities during
plant material decomposition in soils with different pH va-
lues. Soil Biol Biochem. 38: 795–802.
Renella G, Landi L, Valori F, Nannipieri P. 2007b. Microbial
and hydrolase activity after release of low molecular weight
organic compounds by a model root surface in a clayey and
a sandy soil. Appl Soil Ecol. 36: 124–129.
Renella G, Szukics U, Landi L, Nannipieri P. 2007c. Quantita-
tive assessment of hydrolase production and persistence in
soil. Biol Fert Soils. 44: 321–329.
Rydin E, Otabbong E. 1997. Potential release of phosphorus
from soil mixed with sewage sludge. J Environ Qual. 26:
529–534.
Saarela I. 1998. Availability of phosphorus in different ashes,
manures and sewage sludges. In Agerlid G (ed.) Phosphorus
Balance and Utilization in Agriculture—towards Sustainabi-
lity. Kungl. Skogs-och Lantbruksakademien, Stockholm. pp.
157–163.
Sablayrolles C, Gabrielle B, Montrejaud-Vignoles M. 2010. Life
cycle assessment of biosolids land application and evaluation
of the factor impacting human toxicity through plant uptake.
J Ind Ecol. 14: 231–241.
S´anchez-Monedero M A, Mondini C, de Nobili M, Leita L, Roig
A. 2004. Land application of biosolids. Soil response to di-
fferent stabilization degree of the treated organic matter.
Waste Manage. 24: 325–332.
Sarkar D, O’Connor G A. 2004. Plant and soil responses to
biosolids-phosphorus in two Florida soils with high phospho-
rus content. Commun Soil Sci Plant Anal. 35: 1569–1589.
Scharenbroch B C, Meza E N, Catania M, Fite K. 2013. Biochar
and biosolids increase tree growth and improve soil quality
for urban landscapes. J Environ Qual. 42: 1372–1385.
15. BIOSOLID APPLICATION AND GLOBAL P RECYCLE 15
Scharer M, Sinaj S, Moosbauer G, Favre G, Vollmer T, Stamm
C, Frossard E. 2001. Effect of phospahte sorbing amend-
ments on phosphate availability in two soils. In Haygarth
P M, Condron L M, Butler P J, Chisholm J S (eds.) Con-
necting Phosphorus Transfer from Agriculture to Impacts in
Surface Waters. Proceedings of the International Phosphorus
Transfer Workshop (IPTW 2001). Institute of Grassland and
Environmental Research, Plymouth University, Devon. pp.
57–64.
Schindler D W. 1977. Evolution of phosphorus limitation in la-
kes. Science. 195: 260–262.
Schlesinger W H, Bernhardt E S (eds.). 1997. Biogeochemistry:
An Analysis of Global Change. Academic Press, San Diego.
Schroder J L, Zhang H, Zhou D, Basta N, Raun W R, Payton M
E, Zazulak A. 2008. The effect of long-term annual applica-
tion of biosolids on soil properties, phosphorus, and metals.
Soil Sci Soc Am J. 72: 73–82.
Shaheen S, Tsadilas C. 2013. Phosphorus sorption and availabi-
lity to canola grown in an Alfisol amended with various soil
amendments. Commun Soil Sci Plan. 44: 89–103.
Shannon E E, Verghese K I. 1976. Utilisation of alumized red
mud solids for phosphorus removal. J Water Pollut Control
Fed. 48: 1948–1954.
Sharpley A N, Rekolainen S. 1997. Phosphorus in agriculture
and its environmental implications. In Tunney H, Carton O
T, Brooks P C, Johnston A E (eds.) Phosphorus Loss from
Soil to Water. CABI Publ., Cambridge. pp. 1–54.
Shober A L, Hesterberg D L, Sims J T, Gardner S. 2006. Chara-
cterization of phosphorus species in biosolids and manures
using XANES spectroscopy. J Environ Qual. 35: 1983–1993.
Shober A L, Sims J T. 2003. Phosphorus restrictions for land
application of biosolids: Current status and future trends. J
Environ Qual. 32: 1955–1964.
Shober A L, Sims J T. 2007. Integrating phosphorus source and
soil properties into risk assessments for phosphorus loss. Soil
Sci Soc Am J. 71: 551–560.
Siddique M T, Robinson J S. 2003. Phosphorus sorption and ava-
ilability in soils amended with animal manures and sewage
sludge. J Environ Qual. 32: 1114–1121.
Silveira M L, Ferracci´u Alleoni L R, Guimar˜aes Guilherme L
R. 2003. Biosolids and heavy metals in soils. Sci Agr. 60:
793–806.
Silveira M L, O’Connor G A. 2013. Temperature effects on phos-
phorus release from a biosolids-amended soil. Appl Environ
Soil Sci. 2013: 981715.
Smith M T E, Cade-Menun B J, Tibbett M. 2006. Soil phospho-
rus dynamics and phytoavailability from sewage sludge at
different stages in a treatment stream. Biol Fert Soils. 42:
186–197.
Smith S R, Bellett-Travers D M, Morris R, Bell J N B.
2002a. Fertilizer value of enhanced treated and convention-
al biosolids products. In Chartered Inst. Water and Environ.
Mgmt. (ed.) Proceedings of the Chartered Institute of Wa-
ter and Environmental Management (CI-WEM). Biosolids:
The Risks and Benefits. Chartered Inst. Water and Environ.
Mgmt., London. pp. 70–75.
Smith S R, Triner N G, Knight J J. 2002b. Phosphorus release
and fertiliser value of enhanced-treated and nutrient-removal
biosolids. Water Environ J. 16: 127–134.
Smyth T J, Sanchez P A. 1980. Effects of lime, silicate, and
phosphorus applications to an Oxisol on phosphorus sorp-
tion and ion retention. Soil Sci Soc Am J. 44: 500–505.
Solis-Mejia L, Islas-Espinoza M, Esteller M V. 2012. Vermicom-
posting of sewage sludge: earthworm population and agro-
nomic advantages. Compost Sci Util. 20: 11–17.
Soon Y K, Bates T E. 1982. Extractability and solubility of
phosphate in soils amended with chemically treated sewage
sludges. Soil Sci. 134: 89–96.
Standing D, Meharg A A, Killham K. 2003. A tripartite micro-
bial reporter gene system for real-time assays of soil nutrient
status. FEMS Microbiol Lett. 220: 35–39.
Stott D E, Tabatabai M A. 1985. Identification of phospholi-
pids in soils and sewage sludges by high performance liquid
chromatography. J Environ Qual. 14: 107–110.
Stratful I, Brett S, Scrimshaw M B, Lester J N. 1999. Biological
phosphorus removal: its role in phosphorus recycling. Envi-
ron Technol. 20: 681–695.
Strawn D G, Bohn H L, O’Connor G A. 2015. Soil Chemistry.
4th Edn. Wiley-Blackwell, New York.
Stumm W, Morgan J J. 1970. Aquatic Chemistry. lst Edn.
Wiley-lnterscience, New York.
Sui Y, Thompson M L, Shang C. 1999. Fractionation of phos-
phorus in a Mollisol amended with biosolids. Soil Sci Soc Am
J. 63: 1174–1180.
Tian G, Granato T C, Cox A E, Pietz R I, Carlson C R Jr, Abe-
din Z. 2009. Soil carbon sequestration resulting from long-
term application of biosolids for land reclamation. J Environ
Qual. 38: 61–74.
Tian H Q, Lu C Q, Melillo J, Ren W, Huang Y, Xu X F, Liu M
L, Zhang C, Chen G S, Pan S F, Liu J Y, Reilly J. 2012. Food
benefit and climate warming potential of nitrogen fertilizer
uses in China. Environ Res Lett. 7: 1–8.
Tomasi N, Weisskopf L, Renella G, Landi L, Pinton R, Varani-
ni Z, Nannipieri P, Torrent J, Martinoia E, Cesco S. 2008.
Flavonoids of white lupin roots participate in phosphorus
mobilization from soil. Soil Biol Biochem. 40: 1971–1974.
Torri S I, Alberti C. 2012. Characterization of organic com-
pounds from biosolids of Buenos Aires City. J Soil Sci Plant
Nutr. 12: 143–152.
Torri S I, Corrˆea R S, Renella G. 2014. Soil carbon sequestration
resulting from biosolids application. Appl Environ Soil Sci.
38: 61–64.
Torri S, Alvarez R, Lavado R. 2003. Mineralization of carbon
from sewage sludge in three soils of the Argentine pampas.
Commun Soil Sci Plant Anal. 34: 2035–2043.
Torri S, Lavado R. 2009a. Fate of cadmium, copper, lead and
zinc on soils after the application of different treated sewage
sludge in soils of the Pampas region. In Stephens A, Fuller M
(eds.) Sewage Treatment: Uses, Processes and Impact. Nova
Science Publishers, Inc., Hauppauge. pp. 95–123.
Torri S, Lavado R. 2009b. Plant absorption of trace elements
in sludge amended soils and correlation with soil chemical
speciation. J Hazard Mater. 166: 1459–1465.
Torri S, Lavado R. 2011. Carbon sequestration through the use
of biosolids in soils of the Pampas region, Argentina. In
Dupont H C (ed.) Environmental Management: Systems,
Sustainability and Current Issues. Nova Science Publishers,
Inc., Hauppauge. pp. 221–236.
Torri S. 2009. Feasibility of using a mixture of sewage sludge
and incinerated sewage sludge as a soil amendment. In Baily
R E (ed.) Sludge: Types, Treatment Processes and Dispo-
sal. Nova Science Publishers, Inc., Hauppauge. pp. 187–208,
317.
Tran N, Drogui P, Blais J F, Mercier G. 2012. Phosphorus re-
moval from spiked municipal wastewater using either elec-
trochemical coagulation or chemical coagulation as tertiary
treatment. Sep Purif Technol. 95: 16–25.
Tsadilas C D. 2011. Heavy metals forms in biosolids, soils and
biosolid-amended soils. In Selim H M (ed.) Dynamics and
16. 16 S. I. TORRI et al.
Bioavailability of Heavy Metals in the Rootzone. CRC Press,
Taylor and Francis Group, Boca Raton. pp. 271–291.
van der Meer J R, Tropel D, Jaspers M. 2004. Illuminating the
detection chain of bacterial bioreporters. Environ Microbiol.
6: 1005–1020
Van Vuuren D P, Bouwman A F, Beusen A H W. 2010. Phospho-
rus demand for the 1970–2100 period: A scenario analysis of
resource depletion. Global Environ Chang. 20: 428–439.
Walworth J L, Summer M E. 1988. Foliar diagnosis: a review.
In Lauchli A (ed.) Advances in Plant Nutrition. Praeger Pub-
lishers, New York. pp. 193–241, 245.
Weatherley A J, Bolland M D A, Gilkes R J. 1988. A com-
parison of values for initial and residual effectiviness of rock
phosphates measured in pot and field experiments. Aust J
Exp Agr. 28: 753–763.
White J W, Coale F J, Sims J T, Shober A L. 2010. Phospho-
rus runoff from waste water treatment biosolids and poultry
litter applied to agricultural soils. J Environ Qual. 39: 314–
323.
Whitehead P, Chadwick D R, Haygarth P M, Robinson J S. 2001.
Dairy slurry effects on phosphate retention and release in four
UK grassland soils. In Haygarth P M, Condron L M, Butler
P J, Chisholm J S (eds.) Connecting Phosphorus Transfer
from Agriculture to Impacts in Surface Waters. Proceedings
of the International Phosphorus Transfer Workshop (IPTW
2001). Institute of Grassland and Environmental Research,
Plymouth University, Devon. pp. 65–76
Withers P J A, Clay S D, Breeze V G. 2001. Phosphorus trans-
fer in runoff following application of fertilizer, manure, and
sewage sludge. J Environ Qual. 30: 180–188.
Withers P J A, Hartikainen H, Barberis E, Flynn N J, War-
ren G P. 2009. The effect of soil phosphorus on particulate
phosphorus in land runoff. Eur J Soil Sci. 60: 994–1004.
Withers P J A, Jarvie H P. 2008. Delivery and cycling of phos-
phorus in rivers: a review. Sci Total Environ. 400: 379–395.
Withers P J A, van Dijk K C, Neset, T S S, Nesme T, Oene-
ma O, Rubæk G H, Schoumans O F, Smit B, Pellerin S.
2015. Stewardship to tackle global phosphorus inefficiency:
the case of Europe. Ambio. 44: 193–206.
Wong J W C, Su D C. 1997. Reutilization of coal fly-ash and
sewage sludge as an artificial soil-mix: Effects of preincuba-
tion on soil physico-chemical properties. Bioresource Tech-
nol. 59: 97–102.
Yuan Z, Pratt S, Batstone D J. 2012. Phosphorus recovery from
wastewater through microbial processes. Curr Opin Biotech.
23: 878–883.