2023.08.03.63
Files > Volume 8 > Vol 8 No 3 2023
Evaluation of the operation of the stabilization pond for agricultural irrigation purposes
Gisel - Guerra Hernández1*
, Oscar Nemesio Brown Manrique1, Nancy García Alvarez1, Beatriz Melo Camaraza2, Deynis González Garcia2, Marcos Edel Martínez Montero3 and Cristian Enrique Leiva Chamba4
, Oscar Nemesio Brown Manrique1, Nancy García Alvarez1, Beatriz Melo Camaraza2, Deynis González Garcia2, Marcos Edel Martínez Montero3 and Cristian Enrique Leiva Chamba41 Center for Hydrotechnical Studies, Faculty of Technical Sciences, University of Ciego de Ávila, Cuba.
2 Department of Hydraulic Engineering, Faculty of Technical Sciences, University of Ciego de Ávila, Cuba.
3 Faculty of Agricultural Sciences, University of Ciego de Ávila, Cuba.
4 BANARIEGO CIA LTDA.
* Correspondence: [email protected]; Tel.: +53 55883459.
Available from: http://dx.doi.org/10.21931/RB/2023.08.03.63
ABSTRACT
Improving the quality of residual water and increasing agricultural production is necessary to achieve food sovereignty in water deficit conditions. The research was carried out to evaluate the operation of the precision lagoon for agricultural irrigation purposes by determining the geometric and hydraulic parameters, kinetic coefficients and dissolved Oxygen using the Streeter & Phelps model. The main results indicate the presence of a facultative lagoon with a hydraulic retention time of 6.7 days, flow rate of 1 641,6 m3 day-1 contributed by 41 312 inhabitants, solar penetration of 0.20 m, presence of green algae, 0,36 day-1 deoxygenation coefficient, 0,60 day-1 reaeration coefficient, 0,09 day-1 sedimentation coefficient, 0,45 day-1 total removal coefficient, dissolved Oxygen of the effluent of 2 mg L-1, initial dissolved oxygen deficit of the influent and effluent of 8,4 mg L-1 and 2,43 mg L-1 respectively. These indicate that the effluents can be used as wastewater reuse for irrigation of cooked food crops according to the recommendations of the World Health Organization.
Keywords: wastewater, kinetic coefficients, dissolved Oxygen, hydraulic parameters, reuse.
INTRODUCTION
Water quality depends on its use and is linked to various physical, chemical and microbiological parameters, with concentration limits established in its natural state or altered by humans. The problems derived from the contamination of bodies of water, such as the reduction of the supply of fresh water, health risks, the uselessness of water for various uses and the negative impact on aquatic life, are some of the associated effects to water quality.1
Water quality depends on several natural factors, although human activities influence the decline in quality. It is necessary to look for tools such as mathematical modeling that improve the management of water resource quality.2
Water is a crucial component of the environment where rivers have historically been considered a source of wealth; providing essential water for the subsistence and subsequent development of living beings favors soil fertility for obtaining food. However, the continuous growth of the human population and the presence of unsustainable development models have resulted in the contamination of rivers and the loss of the availability of these resources.3, 4
One of the elements that can affect the self-purification process of rivers is their length between two points, being adapted in principle to treatment systems in stabilization ponds. To describe this capacity, Streeter & Phelps5 developed a mathematical model that considers the main mechanisms of contaminant transport, natural purification through degradation by microorganisms present in the river, and reaeration.4
Mathematical models are widely used tools that allow us to understand and describe the behavior of the variations of specific parameters that influence the quality of water bodies associated with the discharge of pollutants changes in land use. This tool is essential since it allows environmental authorities to understand cause-effect relationships associated with pollutant discharges into the river and lake streams. They can also be used to assess the benefits of installing wastewater treatment plants, environmental impact studies and sanitation plans.6
The growing contamination of water bodies requires ever more significant efforts to study and determine the self-purification capacity of the water body, with the deoxygenation coefficient of degradation of organic matter (k1) and the atmospheric re-reaction coefficient ( k2) used in the Streeter & Phelps self-cleaning model. Where the dissolved Oxygen (DO) along the longitudinal profile of a particular body, once the Biochemical Oxygen Demand (BOD) has been consumed, the dissolved Oxygen decreases, the organic matter being biologically degraded until the DO takes its initial value.7, 8
The first model proposed by Streeter & Phelps assumes, among other hypotheses, that there are two predominant processes related to Dissolved Oxygen in water: biodegradation and reaeration, both occurring according to first-order reactions. In this model, the process for the deoxygenation coefficient k1 and the reaeration coefficient k2 depend on the water temperature. Subsequently, Streeter & Phelps water quality models use the same equations to obtain the spatial distribution of DO in river streams.9
Cuba has a sanitation infrastructure comprising more than 300 stabilization ponds, 5,442 kilometers of sewerage networks, 163 waste pumping stations and 12 treatment plants to achieve adequate final disposal of effluents.10
The Ciego de Ávila province has an urban wastewater treatment system comprising ten facultative lagoons with removal efficiencies of chemical oxygen demand and biochemical oxygen demand that range between 35-55%, which is why they cause impacts negatively in surface water bodies.
The objective of the work was to evaluate the functioning of the stabilization lagoon for agricultural irrigation purposes in the municipality of Morón, Cuba, through the evaluation of geometric and hydraulic parameters, estimation of dissolved Oxygen using the Streeter & Phelps model and its kinetic coefficients. , as essential aspects in the removal of organic load.11, 6, 7, 12
MATERIAL AND METHODS
The research was carried out in the stabilization lagoon of the municipality of Morón in the province of Ciego de Ávila, Cuba, located between the planar coordinates Cuba Norte X = 744367 m and Y = 257166 m.
The stabilization pond comprises three fundamental parts: the discharge work comprising three registers and a 350 mm discharge collector, the optional stabilization pond treatment system and the outlet work with three distribution registers towards two canals, one master and the other for agricultural irrigation. This structure allows the collection of liquid waste originating in the municipality, reducing the organic load and producing an effluent that does not cause negative impacts on the environment.
The information required consisted of evaluating the quality of the residual water by applying the following techniques: direct observation, evaluation of the geometric and hydraulic parameters, modeling of dissolved Oxygen in the lagoon and analysis of total coliforms (TC). And thermo tolerant (TTC). For the TC, the recommended limit value of 1 000 mg L-1 by the World Health Organization for crop irrigation and for the TTC, the value is lower than the limit of 2 000 mg L-1 recommended by several countries of America America for irrigation with wastewater. Depending on the evaluation of each indicator, retention time and coliforms are the main parameters that define the type of irrigation to be used, being their classification as raw food crops, cooked food crops and industrial.13
Total (TC) and thermotolerant (TTC) coliforms were determined using the multiple tube technique.14, 15
Direct observation was used to determine the current situation of the community's wastewater treatment system through visual inspections and measurements with specific instruments.
The evaluation of the geometric and hydraulic parameters, estimation of dissolved Oxygen and kinetic coefficients of the stabilization pond are explained below:
The flow was determined based on the continuity equation, multiplying the cross-sectional area using a tape measure by the average current speed using the float method whose transfer time was measured with a clock in a length of co -A uniform current of 10 meters12. The average rate of the water16,17 was determined with the float method over a distance of 10 meters using the following equation:
Where A is the cross-sectional area of the discharge duct (m2), and v is the mean velocity of the water (m s-1).
The surface area and length of the lagoon were determined with a GPS of the GARMIN model.18
The average depth and thickness of the mud were determined by employing a limnimetric ruler graduated with a precision of one centimeter. Measurements were made at numerous points within the predetermined lagoon using a rectangular network.19
Sunlight penetration was determined using the standard 20 cm diameter Secchi disk.20
The volume and hydraulic retention time were determined using the Yánez surface charge empirical design method for dispersed flow facultative lagoons21, 22, using the following equations:
Where λs is the superficial organic load (kg BOD5 m-3 ha-1 day-1), T is the minimum monthly air temperature (°C), AS is the surface area of the facultative lagoon (ha), Li BOD5 of the concentrated tributary in (mg. L-1), VL is the volume of the lagoon (m3), H the average depth of the residual water in the lagoon (m), Trh the hydraulic retention time (day), Q flow rate of the tributary ( m3 day-1), Li the BOD5 concentration of the influent (mg L-1).
The water quality was evaluated by applying the Streeter & Phelps mathematical model and the values obtained in field and laboratory work of the physical, chemical, microbiological and hydraulic parameters reflected in (table 1) to simulate the self-purification capacity of the organic matter in a length of 210 m distance between the influent and effluent. The mass transport equations describe the variation of the dissolved oxygen concentration and the BOD concentration at different spaces in the direction of the surface current path.11, 6, 4
Table 1. Physical, chemical, microbiological and hydraulic parameters for modeling.
The evaluation of the deoxygenation and reaeration coefficients12, 9, 2, 24 and the dissolved oxygen concentration23, 7 were determined from the difference between the dissolved oxygen saturation concentration and the dissolved oxygen déficit11, 6, using the following equations:
Where Qaverage balance of the average water flow (m3 s-1), Qeffluent effluent water flow (m3 s-1), Qafluent tributary water flow (m3 s-1), ODm average dissolved oxygen balance of the water (mg L-1), 𝑂S dissolved oxygen saturation concentration (mg L-1), T water temperature (oC), DDO initial dissolved oxygen deficit (mg L-1), BODm biochemical oxygen demand balance average in the water (mg L-1), v average velocity of the water transformed into (m d-1) (0.20 m s-1= 17 280 m d-1), L length of the lagoon (m), t the travel time of the float for the specified length (s), k1 deoxygenation coefficient (day-1), DBOD biochemical oxygen demand deficit at the specified distance (mg L-1), 𝐿𝑜 the BOD modeled on the lagoon (mg L-1) where 𝐿𝑜 = BODm, x specific distance (m), k2 the reaeration coefficient (day-1), 𝐷x is the total dissolved oxygen deficit or estimation of the dissolved oxygen deficit at a distance downstream (mg L-1), ODx estimate of dissolved Oxygen at the total distance from the lagoon (mg L-1).
The sedimentation coefficient of organic matter25 and the total removal coefficient24 were determined using the following equations:
Where vs the sedimentation rate of organic matter (m day-1) from the Stokes equation, α reflective factor approximately 1, ρs density of the particle (1.93 g cm-3), ρw density of the water, dp diameter of the particle24 of (1 to 2 μm), k3 the coefficient of sedimentation of the organic matter (day-1), kr the coefficient of total removal (day-1). The sedimentation coefficient of organic matter (k3) was estimated based on the average depth, the sedimentation rate of organic matter, the size of the particle and its density.25
Dissolved Oxygen (DO) analysis was also determined using the Winkler26 method for a range of 2 to 7 mg L-1 and was carried out by the laboratory staff of the National Technical Services Company of the province of Ciego de Ávila.
RESULTS AND DISCUSSION
Evaluation of geometric parameters
The geometric parameters that evaluate the lagoon are the length of 210 m, width of 100 m and depth of 1.52 m. The value of this depth indicates that it is a facultative-type lagoon for a range of 1,5 – 2,2 m, compared to results from (Treviño & Cortés, 2016)21, which are potentially more efficient in removing of the organic load and are those recommended for the use of its effluents for agricultural purposes13. The shallowness of the facultative lagoons favors sunlight penetration and photosynthetic activity during daylight hours.27
Evaluation of hydraulic parameters
The results of the direct observation method identified the presence of a stabilization lagoon composed of three fundamental elements: the discharge structure, the facultative lagoon and the outlet work.
The results of the field measurements and analytical calculations determined that the lagoon has a flow of 1 641,60 m3 d-1, an area of 7 083 m2 (0.70 ha), a volume of 10 767,44 m3, retention time hydraulics 6,7 days, average speed of the water 0,20 m s-1, penetration of sunlight 0,20 m and thickness of the mud variable between 0,20 and 0,40 m. The behavior of the thickness of the mud indicates the presence of an essential organic charge that influences the solar penetration to be 20 cm. Studies carried out by Cortés et al. (2017)28 and Treviño & Cortés (2016)21 demonstrated the usefulness of analyzing the hydraulic parameters of stabilization ponds in understanding their operation and decision-making.
The tributary is contributed by 41 312 inhabitants with an average flow of drinking water consumption of 600 L inhabitants-1 day-1, which generates a surface organic load of 345 kg BOD5 m-3 day-1 with a concentration of BOD5 of tributary of 176 mg BOD5 L-1 and effluent BOD5 concentration of 112 mg BOD5 L-1.
Dissolved Oxygen Assessment
The dissolved Oxygen concentrations in the influent and effluent carried out by the water quality laboratory were 0 mg L-1 and 2 mg L-1, respectively, lower results about the range (2 to 7 mg L-1) . These values are common due to the low penetration of sunlight, as well as the abundance and activity of specific groups of microorganisms.29, 26, 6, 4
The tributary Streeter & Phelps mathematical model analysis presented an initial dissolved oxygen deficit of 8,40 mg L-1 to assume the decomposition of organic matter by bacteria that are mainly dependent on dissolved Oxygen. The effluent presented a total dissolved oxygen deficit of 2,43 mg L-1 and a biochemical oxygen demand deficit of 1,85 mg L-1. The behavior obtained from the estimation of dissolved Oxygen in the lagoon effluent by the mathematical model was 6,87 mg L-1 compared to the analyses carried out in the laboratory of 2,00 mg L-1. Similar studies were carried out by (Menéndez et al., 2022)11; (Quiñones et al., 2020)6; Pazmino et al. (2018).12
In (figure 1), the results of the coefficients of deoxygenation (k1), reaeration (k2), sedimentation (k3) and total removal of BOD5 (kr) are presented. It can be seen that the highest values corresponded to the reaeration coefficient with 0,60 day-1 and the complete removal coefficient with 0,45 day-1. The sedimentation coefficient is very low, a parameter closely related to the short hydraulic retention time of 6,7 days (less than the range of 20 days for facultative lagoons).
Figure 1. Values of the coefficients of deoxygenation (k1), reaeration (k2), sedimentation (k3) and total removal of BOD5 (kr).
The deoxygenation coefficient k1 is related to the degradation produced by the bacteria at the bottom of the stabilization pond, reaching a result of 0,36 day-1, which is within the established range (0,10 < k1 ≤ 0,60 day-1) for shallow currents (0 < H ≤ 2,40 m)12, 25. Similar results were found in Chile and Colombia.24, 9
The reaeration coefficient k2 is linked to the renewal process of Oxygen and other gaseous components of the air in the body of water. In this research, the result achieved was 0,60 day-1, a value within the range of (0,30 < k2 ≤ 0,60 day-1) for wastewater streams 11, 30, 31. These values are sensitive in shallow bodies of water.7
The sedimentation coefficient k3 was 0,09 day-1 for a sedimentation rate of organic matter of 0,14 m day-1. A similar result was obtained by Cesar & Coelho (2014).25
The total removal coefficient of the BOD5 kr reached a value of 0,45 day-1. This kinetic coefficient responds to the conditions of the lagoon and can be used in other facultative types in similar situations.24
The observation technique showed that the lagoon had a green color, indicating good functioning due to the green algae of the genus Chlorella, Scene-desmus and Chalamydonomas, which are significant oxygen producers. The photosynthetic activity of these algae and surface reaeration favor oxygen production necessary for the purification process 32. The existence of typical odor, absence of foam, floating material and weeds was also verified.
Analysis of microbiological characteristics
The values of thermotolerant coliforms were 92 000 mg L-1 and 1 200 mg L-1 in the influent and effluent, respectively. The effluent value is lower than the limit established of 2,000 mg L-1 used in several Latin American countries for irrigation with wastewater.14, 33, 15, 13
Total coliform values were 1 60 000 mg L-1 and 1 200 mg L-1 in the influent and effluent, respectively. The effluent value is slightly higher than the limit value of 1 000 mg L-1, recommended by the World Health Organization for crop irrigation.14, 15, 13 Thus, the effluent obtained is not suitable for irrigation. of food crops that are eaten raw, but yes, for cooked food crops.
CONCLUSIONS
The stabilization lagoon of the municipality of Morón is of the facultative type with an average depth of 1,52 m, average velocity of 0,20 m s-1, hydraulic retention time of 6,7 days and solar penetration of 0,20 m.
The calculated kinetic coefficients showed values of 0,36, 0,60, 0,09, and 0,45 day-1 for the coefficients of deoxygenation (k1), reaeration (k2), sedimentation (k3) and total BOD5 removal (kr) respectively.
The dissolved Oxygen concentration in the effluent was low, with a value of 2,00 mg L-1, due to the low penetration of sunlight.
The Streeter and Phelps, mathematical model analysis showed an initial dissolved oxygen deficit of 8,40 mg L-1 in the influent and a total dissolved oxygen deficit of 2,43 mg L-1 in the effluent, indicating a tendency to decrease.
The effluent obtained is not suitable for irrigation of raw food crops, but yes, for cooked food crops.
Acknowledgments: The authors thank the Center for Hydrotechnical Studies of the University of Ciego de Ávila Máximo Gómez Báez and the National Company for Analysis and Technical Services of Water Quality of Ciego de Ávila.
Conflicts of interest: "The authors declare that they have no conflict of interest".
REFERENCES
1. Gil JE, Flores AH, Ochoa KJ, Valencia NA. Determinación de la pérdida de calidad de un río urbano en Cusco: Caso Saphy. Revista Científica Multidisciplinaria Ciencia Latina. 2022;6(1):3722-3748. Disponible en: https://doi.org/10.37811/cl_rcm.v6i1.1765
2. Matovelle C. Modelo matemático de calidad del agua aplicado en la microcuenca del río Tabaca. Revista técnica Killkana. 2017;1(1):39-48. Disponible en: https://biblioteca.uazuay.edu.ec/buscar/item/81241
3. Galal M, Nash S, Olbert AI. Una revisión de los modelos de índices de calidad del agua y su uso para evaluar la calidad del agua superficial. Indicadores Ecológicos. 2021;122:1-21. Disponible en: https://doi.org/10.1016/j.ecolind.2020.107218
4. Quiroz LS, Izquierdo E, Menéndez C. Estudio del impacto ambiental del vertimiento de aguas residuales sobre la capacidad de autodepuración del río Portoviejo, Ecuador. Revista Centro Azúcar. 2018;45(1):73-83. Disponible en: https://centroazucar.uclv.edu.cu
5. Streeter HW, Phelps EB. Un estudio de la contaminación y purificación natural del río Illinois. Revista - Asociación Estadounidense de Obras Hidráulicas. 1927;18(6):753–756. Disponible en: https://doi.org/10.1002/j.1551-8833.1927.tb13530.x
6. Quiñones L, Milla M, Gamarra O, Salas R, Bazán JF. Uso del Modelo de Streeter & Phelps para estimar el oxígeno disuelto en el río Utcubamba. Revista Científica Ecuatoriana. 2020;4(2):12-16. Disponible en: https://doi.org/10.46480/esj.4.2.59
7. Moraes D, Cuba FJ, Aguiar PG. Evaluación de la influencia del coeficiente de desoxigenación en el modelo de autodepuración utilizando efluentes de Laticínio. Revista Internacional de Ciencias. 2019;9(3):32-46. Disponible en: https://www.epublicacoes.uerj.br/ojs/index.php/ric/10.12957/ric.2019 9.42731
8. Benjumea C. Determinación de coeficientes cinéticos de degradación de materia orgánica en el río Negro (municipio de Rionegro, Colombia). Revista bionatura. 2018;3(1):1-17. Disponible en: http://dx.doi.org/10.21931/RB/2018.03.01.10
9. Feria JJ, Náder D, Meza SJ. Tasas de desoxigenación y reaeración del río Sinú. Revista Ingeniería y Desarrollo, Colombia. 2017. Disponible en: http://dx.doi.org/10.14482/inde.35.1.8940
10. Gil Y. Principales indicadores y datos de la infraestructura hidráulica. Instituto Nacional de Recursos Hidráulicos. Disponible en: https://www.hidro.gob.cu/sites/default/files/INRH/Publicaciones/Principales%20indicadores.pdf
11. Menéndez JY, Flores JA, Noles PJ, Menéndez CJ, Espinel VD. Capacidad de autodepuración del río Carrizal sobre efluentes de la laguna de oxidación. Media. Revista de inversiones. Facultad. Minas de metales. Ciencia. geográfico. 2022;25(49):65–72. Disponible en: https://doi.org/10.15381/iigeo.v25i49.19681
12. Pazmiño JC, Zambrano GL, Coello HA. Modelización de la calidad del agua del estero Aguas Claras. Revista DINA. 2018;85(204):204-214. Disponible en: https://dx.doi.org/10.15446/dyna.v85n204.65847
13. Salas AG, Gatto ML, Garcés V, Rodríguez S. Uso actual y potencial de aguas residuales domésticas (RDA) para riego en la provincia de Salta, Argentina. Revista ASADES Avances en Energías Renovables y Medio Ambiente. 2014;18:01-07. Disponible en: https://www.cricyt.edu.ar/asades/modulos/averma/trabajos/2014/2014-t001-a001.pdf
14. Baird R, Eaton A, Rice E. Métodos estándar para el examen de agua y aguas residuales. Asociación Estadounidense de Salud Pública (APHA), Asociación Estadounidense de Obras Hidráulicas (AWWA), Federación Ambiental del Agua (WEF). Disponible en: https://scholar.google.es/scholar?cluster=10785928223407825158&hl=es&as_sdt=2005&sciodt=0,5
15. Gamboa R, Cifuentes G, Rocha Z. Indicadores bacterianos de contaminación fecal en el agua del embalse La Copa, municipio de Toca, Boyacá/Colombia. Revista I+3 Investigación Innovación Ingeniería. 2016;3(1):10-23. Disponible en: https://revistasdigitales.uniboyaca.edu.co/index.php/reiv3/article/view/157
16. Mendoza CJ, Ceja JL. Comparación entre el método de flotación y la aplicación de Descarga, caso canal de riego Mascota. Revista Interdisciplinaria de Ingeniería Sostenible y Desarrollo Local. 2021;7(1):513-521. Disponible en: https://itsta.edu.mx/wp-content/uploads/2022/02/40-2021.pdf
17. Mott R, Untener J. Mecánica de fluidos. Educación Pearson. Disponible en: https://biblioteca.uazuay.edu.ec/bustar/item/79419
18. Barboza I, Maicelo J, Vigo C, Castro J, Oliva SM. Análisis morfométrico y batimétrico del lago Pomacochas (Perú). Revista india. 2016;2(2):90-97. Disponible en: https://doi.org/10.25127/indes.201402.009
19. Rodríguez JJ, Linero J, Barros LJ. Caracterización morfométrica de una laguna costera neotropical (Ciénaga el Chino, Magdalena, Colombia). intrópico. 2018;13(1):21-29. Disponible en: https://dx.doi.org/10.21676/23897864.2355
20. Fernández D, Muñoz L, Flor E. Secchi profundidad del disco y su relación con turbiedad y clorofila “a” en el embalse San Jacinto, Tarija, Bolivia. Revista AIDIS de Ingeniería y Ciencias Ambientales: Investigación, desarrollo y práctica. 2022;15. [Internet]. Disponible en: https://dx.doi.org/10.22201/iingen.0718378xe.2022.15.2.80136.
21. Treviño A, Cortés F. Reduced design method for stabilization ponds. Mexican Journal of Agricultural Sciences. 2016;7(4):729-742. [Internet]. Disponible en: https://www.redalyc.org/pdf/2631/263146721001.pdf.
22. Cortés F, Treviño A, Alcorta MA, Sáenz A, González JL. Optimization in the design of stabilization ponds with non-linear programming. Technology and Water Sciences. 2015;6(2):85-100. [Internet]. Disponible en: https://www.scielo.org.mx/scielo.php?script=sci_arttext&pid=S2007-24222015000200006.
23. Peixoto B, Leite G, Lima IE Neto. Monitoring and modeling of water quality in a semiarid watershed. Eng Sanit Ambient. 2018;23(1):125-135. [Internet]. Disponible en: https://dx.doi.org/10.1590/S1413-41522018167115.
24. Rivera JV. Determination of oxidation, nitrification and sedimentation rates in the self-purification process of a mountain river. Chilean engineering magazine. 2016;24(2):314-326. [Internet]. Disponible en: https://www.scielo.cl/scielo.php?script=sci_arttext&pid=S0718-33052016000200013.
25. Cesar F, Coelho S. Qualitative Modeling Simulation for Preliminary Assessment of Water Quality in the Ribeirão das Perdizes Basin in Campos do Jordão/SP, as Subsidy to the Framework. Brazilian Magazine of Water Resources. 2014;19(3):309-326. [Internet]. Disponible en: https://pdfs.semanticscholar.org/7f08/025acc9b33e2b55488f285e9ee5d69e7d228.pdf.
26. Recalde LS. Comparative analysis of the optical dissolved oxygen sensor with respect to the Winkler method to establish the reliability of the instrument [tesis de maestría]. Higher Polytechnic School of the Coast, Guayaquil, Ecuador. 2022. [Internet]. Disponible en: https://www.dspace.espol.edu.ec/handle/123456789/56508.
27. Cedeño JR, Cedeño EJ. Design proposal for facultative lagoons for wastewater from the city of Manta. Scientific-Educational Magazine of Granma Province. 2022;18(1):152-173. [Internet]. Disponible en: https://revistas.udg.co.cu/index.php/roca/article/view/2866.
28. Cortés F, Treviño A, Espinoza AT, Sáenz A, Alcorta MA, González JL, Martínez R, De la Cruz FJ. Optimization in the design of a wastewater treatment system integrated by three stabilization lagoons. Technology and Water Sciences Magazine. 2017;8(4):139-155. [Internet]. Disponible en: https://10.24850/j-tyca-2017-04-09.
29. Huinil R. Dynamics of dissolved Oxygen in a facultative lagoon. Water, Sanitation & Environment Magazine. 2020;15(1):81-88. [Internet]. Disponible en: https://revistas.usac.edu.gt/index.php/asa/article/download/1136/774/4534.
30. Mello C, Luczkievicz C, Santos P, Rebelatto T, Cól L, Ferrari KD, Neves EC. Use of the Streeter & Phelps mathematical model of dissolved Oxygen applied to the water quality of the Quilombo River in the western region of Santa Catarina. Revista ANAIS de Engenharia Química. 2021;2:1-22. [Internet]. Disponible en: https://uceff.edu.br/anais/index.php/quimica/article/view/312.
31. Rivera JV. Evaluation of the kinetics of oxidation and removal of organic matter in the self-purification of a mountain river. DYNA Magazine. 2015;82(191):183-193. [Internet]. Disponible en: http://www.redalyc.org/articulo.oa?id=49639089023.
32. Vanegas CM, Reyes RV. Maximum surface charge in facultative stabilization ponds in Nicaragua. Nexus Scientific Magazine. 2017;30(1):01-18. [Internet]. Disponible en: https://dx.doi.org/10.5377/nexo.v30i01.5169.
33. Food and Agriculture Organization of the United Nations [FAO]. Water reuse for agriculture in Latin America and the Caribbean. States, principles and needs. 2017. [Internet]. Disponible en: https://www.fao/3/a-i7748s.
Received: 25 June 2023/ Accepted: 26 August 2023 / Published:15 September 2023
Citation: Gisel - Guerra H, Brown Manrique O N, Alvarez N G, Melo Camaraza B, González Garcia D, Martínez Montero M E and Leiva Chamba C E. Evaluation of the operation of the stabilization pond for agricultural irrigation purposes. Revis Bionatura 2023;8 (3) 63. http://dx.doi.org/10.21931/RB/2023.08.03.63