compounds. Boyd and Tucker (1998) confirmed the use of Gypsum (Pulverized ...... Zelaya, O., Boyd, C.E., Teichert-Coddington, D.R and Green, B.W.(2001):.
Cairo University Faculty of Veterinary Medicine Department of Veterinary Hygiene and Management
ENVIRONMENTAL IMPACT OF WATER QUALITY USED IN EARTHEN POND AQUACULTURE ON FRESHWATER FISH PERFORMANCE Thesis Presented By
Hisham Ahmed Mohamed Abdel-Rahman (B.V. Sc., Cairo University 2006)
For The degree of M .V .Sc. Animal , Poultry and Environmental Hygiene Under the Supervision of
Prof. Dr. Zakia Attia Mohamed Ahmed Professor of Animal Hygiene Faculty of Veterinary Medicine Cairo University
Dr. Wael Anwar Hussein Assistant Professor of Animal Hygiene Faculty of Veterinary Medicine Cairo University 2010
DEDICATION
TO my dear kind parents, my wife, my lovely daughter Mariam, my brothers and my sister.
Acknowledgment First of all, my prayerful thanks to Allah for everything in my life and for being my God. The author wishes to express his sincerest gratitude to the supervisor Prof. Dr. Zakia Attia Mohamed Ahmed, Professor of Veterinary Hygiene, Faculty of Veterinary Medicine, Cairo University, for her helpful suggestion, valuable guidance, advice and criticism which made possible the completion of this study. Sincere thanks are due to Dr .Wael Anwar Hussein, Assistant Professor of Veterinary Hygiene, Faculty of Veterinary Medicine, Cairo University. Sincere and heartily thanks are due to Dr. Faten Fathy Mohammed, Lecturer of Pathology, Faculty of Veterinary Medicine, Cairo University for kind help and assistance for accomplishing the histopathological examination section in this work. Lot of thanks to the highly appreciated efforts which are presented by all members of the Department of the Animal Hygiene and Management.
CONTENTS Subject
Page
I. INTRODUCTION
1
II. REVIEW OF LITERATURE
4
1-Environmental monitoring of some aquaculture systems in Al-Fayoum governerate.
5
2-Evaluation of water quality in the studied earthen ponds.
13
3 -Evaluation of the water quality impact on fish health.
22
III.
30
MATERIALS AND METHODS
IV. RESULTS
36
V. DISCUSSION
111
VI. SUMMARY
141
VII. CONCLUSION
148
VIII. REFERENCES
150
IX. ARABIC SUMMARY
List of Tables Table
Title
Page
(1-a) Environmental monitoring of the studied aquaculture farms.
36
(1-b) Environmental monitoring of the studied earthen ponds.
37
(2)
Seasonal mean value ± SE of temperature of water in each examined pond.
38
(3)
Seasonal mean values ± SE of dissolved oxygen of water in each examined pond.
38
(4)
Seasonal mean values ± SE of chloride of water in each examined pond.
39
(5)
Seasonal mean values ± SE of hardness of water in each examined pond.
39
(6)
Seasonal Mean values ± SE of pH of water in each examined pond.
40
(7)
Seasonal mean values ± SE of NO2 of water in each examined pond.
40
(8)
Seasonal mean ± SE of ammonia values of water in each examined pond.
41
(9)
Seasonal mean ± SE of phosphate values of water in each examined pond.
41
(10)
Seasonal mean ± SE of alkalinity values of water in each examined pond.
42
(11)
Seasonal mean ± SE of electrical conductivity values of water in each examined pond.
42
(12)
Seasonal mean ± SE of total solids of water in each examined pond.
43
(13)
Seasonal mean ± SE of total suspended solids of water in each examinedpond.
43
(14) Seasonal mean ± SE of total dissolved solids of water in each examined pond.
44
Seasonal Mean ± SE of NaCl % of water in each examined pond.
44
(15)
Table
Title
Page
(16)
Seasonal mean ± SE of chemical oxygen demand values of water in each examined pond.
45
(17)
Seasonal [(mean values ± SE) x 102] of total coliform count of water in each examined pond.
45
(18)
Seasonal [(mean values ± SE) x 102] of total colony count of water in each examined pond.
46
(19)
Seasonal [(mean values ± SE) x 102] of total fungal count of water in each examined pond.
46
(20-a) Mean values ± SE of physical and chemical parameters of water in each pond during the study period.
47
(20-b) [(Mean values ± SE) x 102] of microbial load of water in each pond during the study period.
48
(21-a) Seasonal impact on the physicochemical characters of water from all examined ponds.
49
(21-b) Seasonal impact on the microbial load of water from all examined ponds.
50
(22)
Total mean values ± SE of all physicochemical parameters and microbial load of water from all examined ponds in three different seasons.
51
(23)
Complete, strong and moderate direct and indirect correlations between values of all physicochemical parameters and microbial load of water from all examined ponds.
52
(24)
Mean values ± SE of some fish performance indices in studied ponds.
53
(25)
Correlations between body weight, body size, liver somatic index and spleen somatic index.
54
List of Figures Figure
Title
Legend 1 ( Fig.1-18) The mean values of water quality parameters (physical, chemical and microbial) in each pond during the study period. Mean values of dissolved oxygen in each pond during the study period. Fig.1 Mean values of chloride in each pond during the study period. Fig.2 Mean values of hardness in each pond during the study period. Fig.3 Mean values of pH in each pond during the study period. Fig.4 Mean values of nitrites in each pond during the study period. Fig.5 Mean values of ammonia in each pond during the study period. Fig.6 Mean values of phosphate in each pond during the study period. Fig.7 Mean values of electrical conductivity in each pond during the study Fig.8 period. Mean values of total solids in each pond during the study period. Fig.9 Fig.10 Mean values of total suspended solids in each pond during the study period. Fig.11 Mean values of total dissolved solids in each pond during the study period. Fig.12 Mean values of salinity in each pond during the study period. Fig.13 Mean values X102of total coliform count in each pond during the study period. Fig.14 Mean values of X102 total colony count in each pond during the study period. Fig.15 Mean values X102 of total fungal count in each pond during the study period. Legend 2 ( Fig1-18) The seasonal mean values of physicochemical and microbial characters of water in each studied pond. Seasonal mean values of temperature of water in each studied pond. Fig.1
Page 55
55 55 56 56 57 57 58 58 59 59 60 60 61 61 62
63 63 63
Fig.3
Seasonal mean values of dissolved oxygen of water in each studied pond. Seasonal mean values of chloride of water in each studied pond.
Fig.4
Seasonal mean values of hardness of water in each studied pond.
64
Fig.5
Seasonal mean values of pH of water in each studied pond.
65
Fig.6
Seasonal mean values of NO2 of water in each studied pond.
65
Fig.7
Seasonal mean values of ammonia of water in each studied pond.
66
Fig.8
Seasonal mean values of phosphate of water in each studied pond.
66
Fig.9
Seasonal mean values of alkalinity of water in each studied pond.
67
Fig.2
64
Figure
Title
Page 67
Fig.14
Seasonal mean values of electrical conductivity of water in each studied pond. Seasonal mean values of total solids of water in each studied pond. Seasonal mean values of total suspended solid of water in each studied pond. Seasonal mean values of total dissolved solid of water in each studied pond. Seasonal mean values of salinity of water in each studied pond.
Fig.15
Seasonal mean values of COD of water in each studied pond.
70
Fig.16
Seasonal mean values of total coliform count X102of water in each studied pond. Seasonal mean values of total colony count X 102 of water in each studied pond. Seasonal mean values of total colony count X 102 of water in each studied pond.
70
Fig.10 Fig.11 Fig.12 Fig.13
Fig.17 Fig.18
Legend 3 (Fig.1-18) The total mean values of all physicochemical and microbial characters of water from all studied ponds along the study period. Fig.1 Mean values of water temperature in studied ponds along the study period. Fig.2 Mean values of dissolved oxygen in water of studied ponds along the study period. Fig.3 Mean values of hardness of water in studied ponds along the study period. Fig.4 Mean values of chloride of water in studied ponds along the study period. Fig.5 Mean values of pH of water in studied ponds along the study period. Fig.6 Mean values of nitrite of water in studied ponds along the study period. Fig.7 Mean values of ammonia of water in studied ponds along the study period. Fig.8 Mean values of phosphate of water in studied ponds along the study period. Fig.9 Mean values of alkalinity of water in studied ponds along the study period. Fig.10 Mean values of electrical conductivity of water in studied ponds along the study period. Fig.11 Mean values of total solids of water in studied ponds along the study period. Fig.12 Mean values of total suspended solid of water in studied ponds along the study period. Fig.13 Mean values of total dissolved solid of water in studied ponds along the study period. Fig.14 Mean values of NaCl of water in studied ponds along the study period.
68 68 69 69
71 71 72
72 72 73 73 74 74 75 75 76 76 77 77 78 78
Figure
Title
Page
The mean values of chemical oxygen demand of water in studied ponds along the study period. Mean values of total coliform count X102 of water in studied ponds along the study period. Mean values of total colony count X 102 of water in studied ponds along the study period. Mean values of total fungal count X 102 of water in studied ponds along the study period.
79
Legend 4 (Fig.1-28) The significant correlations between different physicochemical characters of water within each studied pond.
81
Fig.1
Correlation between TSS and NaCl% within each pond.
81
Fig.2
Correlation between TSS and EC within each pond.
81
Fig.3
Correlation between TSS and TDS within each pond.
82
Fig.4
Correlation between chloride and EC within each pond.
82
Fig.5
Correlation between chloride and TDS within each pond.
83
Fig.6
Correlation between hardness and Chloride within each pond.
83
Fig.7
Correlation between chloride and NaCl %within each pond.
84
Fig.8
Correlation between TDS and EC within each pond.
84
Fig.9
Correlation between EC and NaCl %within each pond.
85
Fig.10
Correlation between TDS and NaCl% within each pond.
85
Fig.11
Correlation between TSS and TS within each pond.
86
Fig.12
Correlation between TS and EC within each pond.
86
Fig.13
Correlation between TDS and TS within each pond.
87
Fig.14
Correlation between TS and NaCl %within each pond.
87
Fig.15
Correlation between hardness and EC within each pond.
88
Fig.15 Fig16 Fig17 Fig18
79 80 80
Figure
Title
Page
Fig.16
Correlation between hardness and TDS within each pond.
88
Fig.17
Correlation between chloride and TS within each pond.
89
Fig.18
Correlation between hardness and NaCl %within each pond.
89
Fig.19
Correlation between hardness and TS within each pond.
90
Fig.20
Correlation between chloride and TSS within each pond.
90
Fig.21
Correlation between hardness and TSS within each pond.
91
Fig.22
Correlation between EC and phosphate within each pond.
91
Fig.23
Correlation between TDS and phosphate within each pond.
92
Fig.24
Correlation between NaCl %and phosphate within each pond.
92
Fig.25
Correlation between TS and phosphate within each pond.
93
Fig.26
Correlation between TSS and phosphate within each pond.
93
Fig.27
Correlation between alkalinity and pH within each pond.
94
Fig.28
Correlation between temperature and alkalinity within each pond.
94
Legend 5 ( Fig.1-2) Mean values of some fish performance parameters and correlations between them.
95
Fig.1
Mean values of body size and final body weight of fish in each pond.
95
Fig.2
Mean value of spleen somatic index, liver somatic index and log final body weight of fish from each studied pond.
95
Legend 6 Micrographs (1-30) of studied fish organs from all ponds.
96
ABBREVIATONS Alk.
Alkalinity
COD
Chemical Oxygen Demand
DO
Dissolved oxygen
EC
Electric Conductivity
ECGS
European Commission Guide Standard
EGCs
Eosinophilic Granular Cells
EDTA
Ethylene Diamine Tetra-acetic Acid
FAO
Food and Agricultural Organization
FAS
Ferrous ammonium sulfate
FBW
Final Body Weight
Hd
Hardness
HN
Hepatocellular Necrosis
HI
HANNA Instrument
HPA
Histopathological Alterations
LD
Lymphoid Depletion
LEp
Lamellar Epithelium
LEpCs
Lamellar Epithelial Cells
LE
Lamellar Edema
LBC
Lamellar Blood Capillaries
LHp
Lamellar Hyperplasia
Max.
Maximum
MCs
Mononuclear Cells
Min.
Minimum
MMCs
Melanomacrophages Cells
MMC
Melanomacrophages Centre
MPN
Most probable number
ppm
Part per million ( for salinity measure)
ppt
Part per thousand
SI
Somatic Index
SPSS
Statistical package for the social sciences
SSI
Spleen Somatic Index
SGR
Specific Growth Rate
TS
Total Solids
TDS
Total Dissolved Solids
TSS
Total Suspended Solids
TAN
Total Ammonia nitrogen
TCC
Total Colony Count
TFC
Total Fungal Count
T. Coliform C. Total Coliform Count
I. Introduction
Fish is considered as one of the cheapest and promising source of animal production especially in regard to the fact that man easily digests 93.2% and 93.7% of fish protein and fat respectively (Onusiriuka, 2002). Aquaculture is the rearing of aquatic organisms (fish, mollusks, crustaceans and aquatic plants) in fresh, brackish or salt water under controlled or semi controlled environment (FAO ,2000). The term ‗aquaculture‘ covers all forms of cultivation of aquatic animals and plants in fresh-, brackish- and saltwater (Carballo et al., 2008). Aquaculture is the fastest growing food-producing sector in the world .The global population is increasing, thus, the demand for aquatic food products is also increasing. Production from capture fisheries has leveled off and most of the main fishing areas have reached their maximum potential. Understanding the benefits of fish products had triggered a substantial increase in consumption, particularly in developed nations, but not so much in developing countries (Subasinghe et al., 2009). Great attention has been paid to Tilapia culture in recent years .Their culture is being practiced in most of the tropical and subtropical regions (ElSayed, 2002). Tilapia is common name given to a group of fishes within the family Cichlidae. Tilapias have 1524 species (Eli, 2005).
1
Tilapias are arguably the ideal candidate for culture and have been st
heralded as culture species of the 21 century and referred to as ‗aquatic chicken‘ (Ramnarine, 2005). Water quality in aquaculture fish ponds is controlled by a complex interplay of many factors. The amount of dissolved oxygen (DO) is controlled by factors such as photosynthesis, respiration by fish and microorganisms, air-water-exchange and oxygen input in the water flowing into the pond. (Gulliver and Stefan, 1984). Managing the water used for aquaculture is one of the most essential components of managing an aquaculture system. It is essential to monitor the water quality frequently and remove waste constantly, particularly in an intensive system, as the TAN waste produced by fish is highly toxic. Ensuring that water quality is maintained at a premium reduces the risks associated with stress and disease (Furey et al. 2006).
The current field study was conducted to fulfill the following: Aim of work. 1-Environmental monitoring of some aquaculture systems in Egypt (Al-Fayoum governorate) regarding to systems, management and species. 2-Evaluation of the water quality used in the available and field investigated aquacultures through the following examination:2-a: Physical water examination on site and at laboratory. 2-b: Chemical water examination on site and at laboratory. 2-c: Microbial examination of the water at laboratory.
2
3-Investigating the impact of water quality on fish performance via recording of the following:3-a: Impact on some fish performance parameters as body sizes, organosomatic indices and final body weight). 3-b: Histopathological profiles of some organs of randomly selected fish at the end of rearing.
3
II. REVIEW OF LITERATURE
According to the previously mentioned historical view of the aquaculture importance for human need as source of animal protein, the presented review of literature will discuss the following topics 1--Environmental monitoring of some aquaculture systems in Al-Fayoum governorate. 1-a- Aquaculture industry. 1-b-Management and water quality in aquaculture . 1-c- Systems of aquaculture. 2- Evaluation of water quality in studied earthen ponds. 3- Evaluation of the water quality impact on fish performance. 3- a- Fish performance. 3-b-Histopathological profile of the freshwater fish reared in earthen ponds.
4
1 -Environmental monitoring of some aquaculture systems in AlFayoum governorate 1-a-Aquaculture industry Essa and Salama (1994) investigated that in Egypt, Tilapia production recently surpassed the production of common carp and thus tilapia had become the pre- eminent culture fish species. El Gamal (1997) reported that aquaculture is being practiced in different forms in Egypt. Earthen pond aquaculture is the major type of aquaculture in Egypt where only waste lands are allowed to be used for fish mainly because of their high salt and alkali content and poor drainage. Corpei (2001) reported that Tilapias are considered suitable for culture, because of their high tolerance to adverse environmental conditions, their relatively fast growth and the ease with which they can breed good utilization of artificial diets, resistance to disease, excellent quality of its firmly textured flesh and finely appetizing fish to consumers. FAO (2001) recorded that aquaculture production increased from 7.4 million tons in 1980 to more than 42 million tons in 1999. The sector's production is growing at an average rate of more than 10% per year. Asian aquaculture farmers continue to contribute about 90% of the world's aquaculture production .Projections of world fishery production in 2010 range between 107 and 144 million tons, of which about 30 million tons will probably be reduced to fish meal and oil for non-food use. Most of the increase in fish production is expected to come from aquaculture. Fitzsimmons (2001) mentioned that the major producers of Tilapia in the world are (in decreasing order of production) China, Thailand, the
5
Philippines, Indonesia, Taiwan, Egypt, Colombia, Cuba, Mexico and Israel. In recent years, Tilapias have been begun to be used as alternative to fishes . Zwirn (2002) mentioned that the farming of fish is viewed as a vital growing sector within food production worldwide because of aquaculture's ability to provide inexpensive protein while allowing over depleted capture fisheries to replenish. Yet despite its perceived food security and environmental benefits, aquaculture poses serious potential for exacerbating environmental and resource allocation conflicts. Egypt, a nation with a long history in fish farming, provides examples of both positive and negative consequences of aquaculture development. Pillay and Kutty (2005) declared that Tilapias (family Cichlidae) are natives of Africa, introduced into a large number of tropical and sub-tropical countries around the world since the 1960s.Tilapias have been introduced for commercial culture in sub-tropical areas and even in temperate areas for indoor culture under controlled temperature conditions .Tilapias are euryhaline and grow well in brackish and salt waters .The most common and widely practiced system of culture of tilapia is in earthen ponds and similar impoundments. In many areas, tilapias are produced mainly by polyculture. FAO (2006a) stated that global production of fish from aquaculture has grown rapidly over the past four decades, contributing significant quantities to the world‘s supply of fish for human consumption. Aquaculture now accounts for almost half (45%) of the world‘s food fish. FAO (2006b) reported that Near East and North African aquacultures are confined to a few countries; in particular, Egypt dominates the production of Tilapia, making a significant contribution to the regional production. 6
Altun et al. (2006) stated that Food and Agricultural Organization (FAO) introduced Tilapia to many places in south of Pacific as a solution of animal protein necessity. Economically important species as table fish belong to three genera (Tilapia, Oreochromis, and Sarotherodon) .Tilapia culture has been carried out in different culture systems (earthen pond, concrete tank, super-aerated pond raceway and cage), management strategies (extensive, semi-intensive or intensive, monoculture, polyculture, monosex, and mixed sex) and in different environment (fresh water and saline water). Naylor et al. (2006) mentioned that aquaculture is a fast-expanding mode of food production in the world. Currently fish farming accounts for more than one-quarter of the total fish directly consumed by humans, using about 220 finfish and shellfish species. Tilapia, milkfish, catfish, carps and marine mollusks contribute 80 % of the global aquaculture output amounting to 29 million tons in 1997. 1-b-Management and water quality in aquaculture Piper et al. (1982) mentioned that "Water quality determines to a great extent the success or failure of a fish cultural operation". Crisman and Beaver (1990) found that the carrying capacity and production of fishponds could be increased by fertilization that encourages growth of phytoplankton and in turn zooplankton that is required as natural food for fish. Westers (1991) figured out that lowered water quality in ponds increases the pollution potential of pond effluents so, should know the feed requirements of the cultured species to determine percent of body weight per
7
day. Use size of fish, water temperature, projected growth rates, and biomass in the system to determine appropriate feeding rates. Hall et al. (1992) attributed the excretion of nitrogenous compounds by cultured fish and microbial decomposition of organic matter to food leftovers are the main source of ammonia, nitrates, nitrites, phosphates and other inorganic substances. Buttner et al. (1993) confirmed the importance of water quality as it determines how well fish will grow in an aquaculture operation and whether or not they survive. Fish influence water quality through processes like nitrogen metabolism and respiration. Some water quality factors are involved with fish losses such as DO, temperature, and ammonia. Others, such as pH, alkalinity, hardness and clarity affect fish, but not directly toxic. The minimum DO level that fish can safely tolerate depends upon temperature and to a certain extent the species. Solubility of oxygen increases as temperature decreases. Warm water fish can tolerate lower DO concentrations than coldwater fish. DO should be maintained above 3.0 ppm for warm fish. As pH and temperature increase, the amount of TAN in the toxic un-ionized form increases. Ammonia is removed by bacteria that initially convert it into nitrite and subsequently into nitrate. Ruimei et al. (1995) reported that water is the essential habitation for fish and other water biology. The growth and developing of the fish are carry out in the water, there should be a better water quality to ensure the fish to grow and develop. Along with the developing of the aquaculture, the intensive grade of the centralized aquaculture is higher and higher, as a result of the enhancing of the density of the aquaculture, the management of
8
the water has been one of the main factors that constricting the increasing for the fish yield. Asmal (1996) investigated the impact of nitrite in solution when enters the circulatory system of fish through the gills .The amount of permeable nitrite depends on the fish species and environmental pH. The resulted characteristic met-hemoglobin symptom had given nitrite poisoning the common name of brown blood disease .The toxic effects of nitrite result from impairment of oxygen transport and cause anoxia. Goldburg (1997) stated that aquaculture systems can produce large quantities of polluting wastes, which are often released directly into natural bodies of water. These wastes consist primarily of uneaten fish feed, faecal material and other excretory wastes. The waste is a source of nutrient pollution-carbon-based
organic
matter,
nitrogen
and
phosphorous
compounds. Boyd and Tucker (1998) confirmed the use of Gypsum (Pulverized Calcium sulphate) in aquaculture as a pond treatment for flocculating clay particles, increasing concentrations of calcium and total hardness, precipitating phosphate, and reducing pH. Jinwonse and Boyd (2001) stated that draining, drying and tilling of the aquaculture ponds bottom can be an effective way of aerating soil and increasing the potential of phosphorus removal from pond water. During the production period, periodic applications of gypsum could be made to reduce the availability of phosphorus in the water to phytoplankton. High quality feeds without excessive phosphorus content should be used, and feed should not be applied in quantities greater than fish will consume.
9
Zelaya et al. (2001) recorded the ponds water quality variables included total phosphorus , total ammonia nitrogen , nitrites, nitrates, and total suspended solids .The main sources of ammonia in fish ponds are : 1fish excretion 2-ammonia diffusion from the sediment into the water column, where large quantities of organic matter are produced by algae or added to ponds as feed ,3-fecal solids excreted by fish and dead algae settle to the pond bottom, where they decompose and produces ammonia .The measured ammonia value is the sum of both forms (Ionized and un-ionized) as ―total ammonia‖ or simply ―ammonia‖. Un-ionized ammonia is the toxic form and predominates when pH is high. Ammonium ion is relatively nontoxic and predominates when pH is low. Less than 10% of ammonia is in the toxic form when pH is less than 8.0.This proportion increases dramatically as pH increases. Hargreaves and Tucker (2002) stated that DO concentration is considered the most important water quality variable in fish culture.Over a matter of hours or even minutes, DO can change from optimum to lethal levels .The dynamic nature of DO results from the interaction of three factors. Oxygen is not very soluble in water so water has only a limited capacity to hold oxygen .The rate of oxygen use by fish, plankton and organisms living in the pond mud can be high. Oxygen diffuses very slowly from the atmosphere into undisturbed water. Ka-Oud (2002) confirmed the pronounced effect of temperature on chemical and biological processes .When temperature increases 10°C causes increase in rates of chemical and biological reactions to double or triple times .Thus, fish will consume 2 to 3 times as much DO at 30 °C as at 20
10
°C, and their biochemical reactions will progress at double or triple the rate at 30 °C as that at 20 °C. Mmochi et al. (2002) stated that conversion of wetlands into aquaculture ponds had resulted in increase in nutrients and organic wastes, leading to general deterioration of water quality. The water quality problem was associated with both physical and chemical factors such as high or low DO and high concentration of nitrogenous compounds. Hargreaves and Tucker (2004) found out that ammonia is toxic to fish when accumulate in fish production systems where fish cannot extract energy from feed efficiently. If the ammonia concentration gets high enough, the fish will become lethargic and eventually fall into a coma and die. In properly managed fish ponds, ammonia seldom accumulates to lethal concentrations. Ammonia can have ―sublethal‖ effects such as reduced growth and reduced disease resistance at lower concentrations than lethal concentrations. The main source of ammonia in fish ponds is fish excretion. The rate at which fish excrete ammonia is directly related to the feeding rate and the protein level in feed. Rowland et al. (2006) clarified that formalin is a selective, short-term parasiticide, with no major concerns about chemical residues in fish flesh or the pond environment. It is recommended that a concentration of 30 mg L _1 formalin is used to control infestations of monogeneans on silver perch in earthen ponds at temperatures below 25 ºC. Treatment may need to be repeated after 30 days .Water quality should be monitored, and ponds aerated for 24 h day_1 for at least 3 days to ensure adequate concentrations of DO. Further research is required to evaluate other chemo-therapeutants for use at higher temperatures.
11
1-c-Systems of aquaculture Hansen (1999) found Nile Tilapia (Oreochromis niloticus) production occurs primarily in semi-intensive ponds where fertilizers are used to increase fish yields at low levels of production. Guangzhi and Auðunsson (2001) recorded that aquaculture systems can be divided into three types according to the scale of operation. In semiintensive system: pond aquaculture density is a little bit higher than the natural environment. In intensive system: usually land-based, closed system aquaculture.The systems are open (flow-through water) or closed (recirculating water). Adhikari (2003) mentioned that pond management in fish culture was concerned with fertilization requirements and strategies; and with good management of pond soil and water quality .The combined use of both organic and inorganic fertilizers is another strategy for increased production of fish. Acidic pond soils reduce microbial activity and the availability of nutrients in pond water and may render fertilization ineffective. Therefore, the application of lime is the first step of management for all stages of fish culture. Liming raises the soil pH to a desirable level (near neutral) and establishes a strong buffer system in the aquatic environment, improving the effectiveness of fertilization. Liming stimulates the microbial decomposition of organic matter, supplies calcium to the pond, increases nitrate content in the pond and maintains sanitation in the pond environment. Careful use of organic manures and chemical fertilizers in combination is a sound strategy. Occasional development of un-hygienic conditions in the pond may be avoided by using pre-decomposed organic manure.
12
Yanong (2003) declared the most pathogens in aquaculture are considered opportunistic, causing disease only in fish with suppressed immune systems. If pathogens become sufficiently numerous they can also cause disease in healthy fish. The continuous flow of water throughout a system can spread pathogens rapidly, especially in a system lacking adequate disinfection protocols, such as ultraviolet sterilization or ozone. 2- Evaluation of water quality in studied earthen ponds Roberts (1998) mentioned that the aquatic environment incorporates a large range of parameters which play a role in maintaining equilibrium and homeostasis. The parameters include physical factors like temperature, pH, light, space, and food availability, with possibly the most important being the chemical composition of the water and its biological content. Yanong (2003) reported that water quality must be compatible with the requirements of the fish being held with regard to ammonia, nitrite, nitrate (in marine systems), pH, temperature, DO, hardness, alkalinity, and salinity .Water from the source should be evaluated by an aquaculture specialist and a water-testing laboratory before a system is established . Water from different sources may have different potential problems that must be addressed. Marchand et al. (2009) reported that physical, chemical factors and biological contents of water in fish ecosystems are parameters influence growth, reproduction and health of aquatic organisms, especially fish. If any parameter is changed past tolerable limits, it may create a tendency to, or be the cause of disease.
13
2-a- Physical and chemical examination of water used in aquaculture. Benson and Krause (1980) mentioned that the distribution of DO is affected by the solubility of many inorganic nutrients, which are governed by seasonal shifts from aerobic to anaerobic environments in some regions of the ponds. Wetzel (1983) attributed the recorded maximum values of salinity in summer to the increase in the evaporation rate, where the temperature influences the rate of rock weathering and the rate of evaporation precipitation process. Borberg and Persson (1988) mentioned that cycling of phosphorus within lakes and river was dynamic and complex; involving adsorption and precipitation reactions, interchange with sediments and uptake by aquatic biota. Delince (1992) stated that aquatic ecosystem affected the organisms, as well as the chemical and physical characteristics of water. Cruz and Ridha (1995) stated that Tilapias are among the most resistant fishes known against diseases and relatively bad environmental conditions such as high stocking density of fish, lower water quality, organically pollutant water, and low DO level of the water (less than 0. 5 mg -1
l ).They have tolerance to salinity in wide range and are suitable for maintaining and feeding conditions in culture. Asmal (1996) reported that elevated phosphate levels can be found where large quantities of organic matter are decomposing or as fertilizers in agriculture, runoff from these areas often contains elevated concentrations of
14
phosphate.TDS is the mass of the dissolved inorganic and organic compounds in water. Ammonium tend to be elevated in waters where organic decomposition under anaerobic conditions takes place .The major factor controlling the toxicity of ammonia is pH, which, together with temperature, governs the proportion of un-ionized ammonia . Un-ionized ammonia (NH3) increased with increased pH and temperature and may be evident under pond culture conditions. .Low concentrations of DO increased the toxicity of NH3. Increased salinity concentrations, up to 30 g/L reduced the ammonia fraction. Ammonia can be reduced by aeration, decreasing the pH, biological filtration, nitrifying bacteria, decreasing the pH, keeping temperatures low (if possible) and/or increasing oxygen supply. Possible sub-lethal effects in warm-water fish occur in the range of 0.3 - 0.8 mg NH3 /L. Hargreaves and Tucker (2002) declared that DO levels can be managed with aeration. DO concentrations in ponds vary with depth, from one side of a pond to the other and from one time of day to another .On calm, sunny days, there may be substantial differences in DO concentrations from the surface of the pond to the bottom, even in relatively shallow ponds. On large commercial farms it is often impractical to sample from more than one location in each pond, so management decisions often must be made on the basis of a single sample. It is important to always sample each pond at the same location and at the same time of day to minimize variations. Yanong (2003) pointed out that Alk .is very important as a pH buffer. If the alk. does reach a critically low level, the pH of the water will drop rapidly and have detrimental effects on the fish. Ammonia is converted to nitrite, and nitrite is converted to nitrate, Hydrogen ions (H+) are released
15
into the water .Drops in alk. may result in ammonia and nitrite spikes. Low DO can occur as the result of many different causes as inadequate water flow, inadequate aeration, high organic loads in the system that lead to large numbers of bacteria or the use of certain chemicals such as formalin. Abdo (2005) reported that the pH values of the water of Abu Za'baal ponds was found in the alkaline side (pH > 7.0) .The higher values of pH were recorded during hot period 8.34 – 8.90, while the lower values were found in the cold period 8.02 – 8.46. The decrease in pH values during cold period, especially in autumn, is mainly related to the high bicarbonate content. The ranges of NH3 were found to be from 2.34 –3.73, 3.69 – 4.24, 3.22 – 4.89 and 2.38 – 3.65 mg/l during winter, spring, summer and autumn respectively. The relative increase in the ammonia during hot period may be attributed to the high evaporation rate, in addition to the denitrification process by the reduction of NO2- and NO3- into NH3 .The water temp. varied from 17 – 20, 30 – 32, 30 – 34 and 19 – 24 C° during winter, spring, summer and autumn respectively .The seasonal variations of total phosphate (TP) were fluctuated in the ranges from 89.06 – 200.27, 76.63 – 192.10, 100.14 – 455.73 and 75.61 –209.50 μg/L during winter, spring, summer and autumn respectively. The high values of the TP noticeable during summer 455.73 μg/L were probably, due to the increase in the evaporation rate as well temp. facilitating of phosphorus release from the decay organisms. The seasonal variations of PO4 concentration were found to be from 41.90 – 73.57, 28.61 – 85.83, 26.57 – 44.96 and 28.61 – 61.30 μg/L during winter, spring, summer and autumn respectively .The minimum values of salinity was recorded during winter and ranged from 2.80 – 3.90 ‰.The maximum values was recorded during summer and ranged from 3.50 – 4.30 ‰. The
16
high values of EC were recorded during hot seasons (spring and summer) 470 – 8090 μmohs/cm, while the lower values (337 – 6000 μmohs/cm) were recorded during cold seasons (autumn and winter). TS and TDS were found in the same trend of the EC and salinity. The higher values of TS and TDS were recorded during hot period and they ranged from 4182 – 5624 mg/L and 4062 – 5600 mg/L. The lower values were recorded during cold period and they ranged from 3468 – 5084 mg/L and 3412 – 4988 mg/L. Pillay and Kutty (2005) mentioned that some species have wide salinity tolerance limits and it had been noted that some fresh-water fish grow faster in slightly saline water and some brackish-water fish faster in fresh water.
The most suitable pH of water for aquaculture farms was
considered to lie in the range 6.7–8.6 and values above or below this inhibited growth and production depending on the species and environmental conditions. Acid water with a pH range of 5.0 –5.5 can be harmful to the adults of many species. Acidity reduces the rate of decomposition of organic matter and inhibits nitrogen fixation and affecting the overall productivity. A pH level of 11 may be lethal to fish. High turbidity of water caused by suspended solids can affect productivity and fish life. Konsowa (2007) monitored the fish farms of El-Fayoum province where these farms were extending along the eastern bank of Lake Qarun. They derive the water and drainage wastes into Diar El-Berka Drain. PH values at the chosen farms ranged between 7.43 and 8.91 and its values are certainly optimum for fish culture. Salinity levels at fish farms adjacent to Lake Qarun (2, 9.5‰) were generally much higher than the other fishing ponds due to seepage from the lake water. Nitrogen concentrations that
17
represented by NO2-N, NO3-N and NH4-N indicated the dominance of NH4N over NO2-N and NO3-N at the selected fish farms (0.59 mg/L, 0.026 & 0.091 respectively) .Total organic phosphorus (TOP) concentrations at the chosen farms were much higher than the corresponding values of orthophosphate. Lewbart and Harms (2008) stated that most freshwater aquariums and ponds were best maintained at a pH of about 7.0 . Ammonia found in water was generally either in the toxic unionized form (NH3) or in the nontoxic ionized form (NH4+). The ratio between the two compounds depends on temperature, pressure, salinity and most importantly, pH .The higher the pH; the more unionized (harmful) ammonia present .The total ammonia nitrogen (TAN) reading represented both forms of ammonia. A total ammonia measurement of 3.0 ppm would be deadly at a pH of 8.5 in freshwater but relatively harmless at a pH of 6.0 for a few days. Nitrite is converted to nitrate by a healthy biological filter. In freshwater levels above 1.0 ppm will likely be harmful to the fish. Nitrate is usually not toxic to fish but persistently high levels (over 50 ppm) are probably stressful to some species. Elevated levels may lead to excess algal growth. Regular water changes and nitrogen monitoring will help alleviate this problem. EL-Sherief and Amal (2009) found out the differences among the mean weight of Nile Tilapia obtained from pH levels 6, 8 and 9 were significant (P≤0.05), but it was not significant (P≥0.05) between pH 7 and 8.The mean weight gain decreased with increasing pH; whereas, it decreased at pH 6. The decrease in growth at pH 6 was attributed to a decrease in feed consumption. There were significant differences (P≤0.05) among pH levels
18
(6, 8 & 9) but no significant difference (P≥0.05) was found between pH 7 and 8. 2-b- Microbial profile of water used in earthen ponds Boyd (1990) reported that depletion of DO after manure application often leads to heterotrophic organisms in the water utilizing NO 3 – N as electron receptors instead of oxygen, thus converting it to nitrite. A.P.H.A. (1995) confirmed the use of indicator bacteria such as faecal coliforms and faecal streptococci for assessment of faecal pollution and possible water quality deterioration in fresh water sources was widely used. Baron (1996) confirmed that several species of gram-negative bacteria present in municipal wastewater were pathogenic. This pathogenicty was usually associated with certain components of the cell walls, in particular the lipopolysaccharide also known as endotoxin layer. Plumb et al. (1997) recorded water quality deterioration in warm water ponds could result in bacterial infections in channel catfish. Reno (1998) mentioned that there were many other predisposing factors which contribute in the development of the infectious disease. Environmental circumstances (poor water quality, changes in temperature, poor nutrition, crowding and transporting) usually produced in intensive fish farming systems, represent a considerable stress making fish more susceptible to a wide variety of pathogens. Michiels and Moyson (2000) pointed out that Heterotrophic plate count is an estimate of the total number of viable microorganisms (yeast, mould, and bacteria) in water, is used routinely to assess the water quality.
19
Youn- Joo et al. (2002) monitored coliform bacteria and E. coli in Lake Marinas to determine the microbial pollution in the lake environment. Chao et al. (2003) pointed out that a high number of fecal coliforms in water suggested fecal contamination , which might had resulted in the introduction of pathogenic microorganisms in the water that present potential health risks to individuals using the water. Fecal coliforms were better indicators of the presence of pathogenic bacteria in water than total coliforms. There are indications that many members of fecal coliforms can grow and multiply in tropical and subtropical aquatic environments. Karaboze et al. (2003) confirmed that the microbial contamination is one of the most important factors of water pollution; especially with pathogenic microorganisms. Enteric pathogens are typically responsible for waterborne sickness. Gehan et al. (2005) reported that bacterial counts showed no significant correlation with the physical parameters (temp., salinity and pH). Giannoulis et al. (2005) recorded that coliforms and E.coli are of great importance among bacterial indicators used in water quality definition and health risk. Chigbu and Sobolev (2007) stated that it was important to identify harmless organisms that could be used as predictors of the presence of pathogenic organisms in water. Coliforms are a group of gram-negative, rodshaped bacteria that are nonpathogenic and non spore forming. Coliforms were shed in feces along with pathogenic organisms present in the gut of infected animals, and could be detected in water with relative ease; total coliforms have been used by the US Public Health Service since 1914 as the
20
standard for sanitary quality of water. Heterotrophic plate count was estimated by counting the number of colonies on culture media. Edum et al. (2007) mentioned that fish from polluted water might carry bacteria derived from human and animal sources. The microbial flora of raised fish in different earthen ponds at the African Regional Aquaculture Center from the skin, gills, gastrointestinal of Oreochromis niloticus. Fourteen species of bacteria, 8 species of fungi and 6 species of parasites were identified. Sabae and Rabeh (2007) described the River Nile in Egypt receives heavy loads of industrial, agricultural and domestic wastes. One of the most important factors of water pollution was the microbial contamination; especially with pathogenic microorganisms. Contamination of water is a serious environmental problem as it adversely affects the human health and the biodiversity in the aquatic ecosystem. Several species of gram-negative bacteria present in municipal wastewater were pathogenic. Identification of these pathogenic agents in water resources was beneficial for controlling and prevention planning of the infectious diseases. Jha et al. (2008) attributed the variations in the abundance of heterotrophic bacteria in the water samples to the differences in management practices resulting in different organic loads in the pond system. Al-Harbi and Uddin (2008) clarified the quantitative and qualitative estimation of bacterial flora present in pond water, sediment where common carp Cyprinus carpio cultured in Saudi Arabia were performed and identified to species level where possible. Mean total viable bacterial counts in pond water ranged from 1.2 ± 2.9 104 to 2.5 ± 3.5 105 CFU/ml; in sediments, 9.3 ± 2.1 107 to 2.7 ± 3.5 109 CFU/ g . Gram-negative rod-shaped 21
bacteria dominated (76%) the populations. In total, 12 bacterial genera and 15 species were identified. Pond water and sediment bacteria had the reflection on bacterial composition of gills and intestine of carp. Flick (2008) stated that while fish were no more hazardous than other animal protein sources, many pathogenic microorganisms and parasites could conceivably be transmitted to humans through fish. The United States centers for disease control and prevention reported that fish and shellfish account for 5% of the individual cases and 10% of all food-borne illness outbreaks, with most of the outbreaks resulting from the consumption of raw molluscan shellfish. 3-Evaluation of the water quality impact on fish performance 3- a- Fish performance Hillaby and Randall (1979) found that ammonia could accumulate in fish to toxic levels, either as a consequence of exposure to elevated water ammonia concentrations or when excretion of the endogenous metabolite was inhibited .Within fish the primary form of total body ammonia at physiological pH (7.0 to 8.0) was NH4+, and it was this chemical species that was responsible for toxic effects. Krom et al. (1985) figured out that large amount of organic matter consumed oxygen in the decomposition process, causing its depletion. Too high DO levels caused death due to emboli that occurred as a result of bubble formation in the blood vessels of fish. Carballo et al. (1991) tested the effects of ammonia and nitrite on susceptibility to infection. In 10-d exposures to 0.05 mg/L NH3-N or 0.12 mg/L NO2-N at inoculums concentrations of 1.4 x 106, 9.75x105, and 5x105
22
zoospores /L they found that 75% of ammonia-exposed fish tested at the highest inoculums concentration and 50% of the nitrite-exposed fish at the highest inoculums concentration developed infection. Infection occurred in 20% of ammonia-exposed fish at the medium fungal dose. No infection occurred in nitrite-exposed fish at the medium dose, and no infection occurred in either ammonia- or nitrite-exposed fish at the lowest fungal dose tested. No infection was found with copper and cyanide exposures. Westers (1991) explained the deterioration of water quality from increased nutrient inputs stresses fish, and caused them to eat less, grow slowly, and been more susceptible to disease. Prolonged exposure to low, non lethal levels of DO constitutes a chronic stress and will cause fish to stop feeding, reduced their ability to convert ingested food into fish flesh, and make them more susceptible to disease. Fish continuously exposed to more than 0.02 ppm of the un-ionized form of ammonia might exhibit reduced growth and increased susceptibility to disease. Nitrite was toxic to fish and causes ―brown blood‖ disease .Concentrations of 0.5 ppm had reduced growth and adversely affected fish. Fish can tolerate nitrate to several hundred ppm. Hopkins and Pauly (1993) showed that in pure O.niloticus stocks, mortality increases with increasing salinity, while O. niloticus x O. mossambicus hybrid stocks show the opposite trend. Buttner et al. (1993) recorded that prolonged exposure to low, nonlethal levels of DO constitutes a chronic stress and will cause fish to stop feeding, reduce their ability to convert ingested food into fish flesh, and make them more susceptible to disease. Intensive fish production in ponds requires aeration to maintain DO at safe levels. Some water quality factors
23
are more likely to be involved with fish losses such as DO, temp., and ammonia .Nitrite was toxic to fish and caused ―brown blood‖ disease. Concentrations of 0.5 ppm have reduced growth and adversely affected fish. Alk. in excess of 300 ppm does not adversely affect fish, but it does interfere with action of certain commonly used chemicals (e.g. copper sulfate). Chang and Plumb (1996) reported that the effect of 0, 15, and 30 parts per thousand (ppt) salinities on three isolates of Streptococcus infection of injured Nile Tilapia at 25 and 30°C were determined. Susceptibility to Streptococcus was associated with elevated salinities at 25 and 30°C. Lorenzen (1996) found out that the natural mortality rates of fish were closely related to their body weight. Among the culture systems, mortality–weight relationships in ponds and cages were not significantly different and a joint relationship was estimated. Popma and Masser (1999) stated that all Tilapia were tolerant to brackish water. The Nile Tilapia was the least saline tolerant of the commercially important species, but grows well at salinities up to 15 ppt. optimal water temp. for Tilapia growth is about 85 to 88o F. Growth at this optimal temp. was typically three times greater than at 72oF. Tilapia survives routine dawn DO concentrations of less than 0.3 mg/L, considerably below the tolerance limits for most other cultured fish. In research studies Nile Tilapia grew better when aerators were used to prevent morning DO concentrations from falling below 0.7 to 0.8 mg/L (compared with unaerated control ponds). Zelaya et al. (2001) stated that ammonia was toxic to fish if allowed to accumulate in fish production systems so fish couldn't extract energy from feed efficiently. If the ammonia concentration gets high enough, the fish will 24
become lethargic and eventually fall into a coma and die . In properly managed fish ponds, ammonia seldom accumulates to lethal concentrations. Ammonia can have sub lethal effects -such as reduced growth; poor feed conversion, and reduced disease resistance-at concentrations that are lower than lethal concentrations. Plumb (2002) mentioned that water provides a nutrient rich environment in which opportunistic fish pathogens can grow and proliferate, thus serving as a pathogen source as well as a primary mode of transmission. When DO dropped below 1 mg/L fish began to die .The addition of fresh water and remedial aeration arrested mortality and clinical signs of infection. Salinity not only affects osmoregulation it also influences the concentration of un-ionized ammonia. To control bacteria, municipal water supplies are typically treated with chlorine at 1.0 ppm. If municipal waters were used to culture fish, residual chlorine must be removed by aeration, with chemicals such as sodium thiosulfate, or filtration through activated charcoal. Chlorine levels as low as 0.02 ppm can stress fish. Yanong (2003) illustrated the effect of water quality fluctuations, such as temporary increases in ammonia or nitrite, result in disease or significant losses. These environmental fluctuations often lead to suppressed immune systems and greater susceptibility to pathogens and disease outbreaks. Most pathogens are considered opportunistic, causing disease only in fish with suppressed immune systems. If pathogens become sufficiently numerous they can also cause disease in healthy fish. The continuous flow of water throughout a system can spread pathogens rapidly, especially in a system lacking adequate disinfection protocols or components, such as ultraviolet sterilization or ozone.
25
De Croux et al. (2004) showed the acute lethal effects of elevated pH on C. macropomum juveniles. They found no mortality at pH 6 (control) and 7 but it was 10-20% at pH 8 and 100% at pH 9. Scott et al. (2005) found that ammonia excretion increased with increasing pH (alk.), while growth decreased. It was attributed to a decrease in feed consumption. Suvajdzic et al. (2006) recorded that ammonia could exist in the ionized (NH4+) and unionized (NH3) form, the latter being the most toxic to fish. Unionized ammonia levels had been reported to be as high as 1.2 mg l1 in the Salton Sea, which exceeds the US EPA water quality criterion. El-Sherief and Amal (2009) found that the final average body weight showed great differences among different pH levels with a decrease at low pH. The level of pH 7 showed the highest fingerlings body weight (36.1 g) followed by pH 8 (35.1 g), then pH 9 (30.8 g) and finally pH 6 (23.3 g).The average individual body weights of Tilapia observed pH 7 and 8 were found to be the best. The mean weight gain decreased with increasing pH; whereas, it decreased at pH 6. The decrease in growth at pH 6 was attributed to a decrease in feed consumption. There were significant differences (P≤0.05) among pH levels (6, 8 & 9) but no significant difference (P≥0.05) was found between pH 7 and 8. 3-b-Histopathological profile of the freshwater fish reared in earthen ponds. Meyers and Hendricks (1985) showed that there was a need for sensitive and precise bio-monitoring tools with a predictive capability in toxicant impact assessment. Aquatic ecosystem health cannot be measured
26
directly .Histology and histopathology can be used as biomonitoring tools or indicators of health in toxicity studies as they provide early warning signs of disease. Hinton and Lauren (1990) stressed on the liver as an important in many aspects of nutrition, including lipid and carbohydrate storage. Alterations in liver structure may be useful as biomarkers that indicate prior exposure to environmental stressors. Hepatocytes found near bile ducts often show toxicant-induced alteration while hepatocytes at other sites may appear normal. Stressor-associated alterations of hepatocytes may be found in the nucleus or cytoplasm or both. Hinton et al. (1992) confirmed the use of histopathological alterations as biomarkers of effect exposure to environmental stressors, revealing prior alterations in physiological and/or biochemical function. Stegeman et al. (1992) confirmed that biochemical or molecular alterations were usually the first detectable and quantifiable responses to environmental change. Roganovic-Zafirova and Jordanova (1998) figured out an increased number of macrophages aggregates could be found in the liver and spleen in fish exposed to chemical pollutants, bacteria, fungi or parasites Zapata-Pe´rez et al. (2000) recorded that liver necrosis had been shown in Nile Tilapia (O. niloticus) after exposure to sediment containing a variety of organic chemicals. Ip et al. (2001) illustrated that in freshwater fishes, ammonia was thought to traverse the gill epithelium almost exclusively via passive diffusion of ammonia as a gas in solution.
27
Roberts (2001) mentioned that there were many potential toxicants whose occurrence caused a reduction in the quality of the aquatic environment. Protection of natural environments and water resources was vital. Gernhofer et al. (2001) confirmed that one of the great advantages of using histopathological biomarkers in environmental monitoring was that this category of biomarkers allowed examining specific target organs, including gills, and liver, those were responsible for vital functions, such as respiration, excretion and the accumulation and biotransformation of xenobiotics in the fish. Wester et al. (2002) stated that effects of environmental change on the histological level could be visible at a lower dosage compared with toxicological endpoints such as mortality or behavior changes. Fanta et al. (2003) mentioned that the alterations found in gills and liver were normally easier to identify than functional ones. Velkova-Jordanoska
and
Kostoski
(2005)
stated
that
histopathological biomarkers were closely related to other biomarkers of stress since many pollutants had to undergo metabolic activation in order to be able to provoke cellular change in the affected organism. For example, the mechanism of action of several xenobiotics could initiate the formation of a specific enzyme that caused changes in metabolism, further leading to cellular intoxication and death, at a cellular level, whereas this manifested as necrosis. Pillay and kutty (2005) confirmed that the suspended solids in freshwater may clog fish gills. The gills of fish may be injured by turbid
28
water .Although the effect will depend on the species and the nature of the suspended matter, pronounced effects were seen when the water contains about 4 percent by volume of solids. Crestani et al. (2007) declared that liver tissue showed many histopathological alterations. This could be expected as the liver was the main detoxification organ involved in the metabolism and excretion of xenobiotic chemicals. It was therefore a target organ of various xenobiotic substances. Histological analysis of silver catfish (Rhamdia quelen) showed vacuolation in the liver after exposure to the herbicide clomazone . Marchand et al. (2009) assessed the physical and chemical water parameters to relate the histopathological alterations to toxicants present in the water as well the health status of fish by implementing a qualitative histology-based assessment, fish necropsy, and organosomatic indices. They confirmed the histopathological assessment as sensitive bio-monitoring tools in toxicant impact on fish health in polluted aquatic ecosystems. Alterations were described morphologically, and the extent of the alterations was assessed using a scale such as mild, moderate, and severe. Vinodhini and Narayanan (2009) demonstrated the liver of control fish which provide normal structure with no path-morphological abnormalities. A homogenous cytoplasm with a large central spherical nucleus was the characteristic nature of control hepatocytes. Hori et al. (2010) reported that the daily and seasonal changes in temp. are challenges that fish within aquaculture settings cannot completely avoid, and are known to elicit complex organismal and cellular stress responses.
29
III. Materials and Methods 1-Ecological monitoring of the studied aquaculture earthen ponds: Data was collected by questionnaire directed to the owners of the available aquaculture farms and illustrated in Table (1-a, b).The collected data included: Type of aquaculture facility, area of the aquaculture farm ,no. of rearing ponds and hatcheries ,availability of electricity and aerators ,rate of water exchange ,type of fuel material which was used for water exchange ,the applied methods of pond disinfection and fertilization ,usage of formulated ration ,presence or absence of veterinary supervision with application of regular water analysis ;data of area ,dimensions and direction of ponds were collected also ;Type ,no. and source of reared spp. 2-Sample collection for water quality analytical methods A total 160 water samples were collected from the available 10 ponds biweekly (two times monthly) between 12.00 and 02.00 pm during the period from April to November 2009 (8 months). Water temp., DO and pH were measured in field. Water samples were transported to the laboratory for chemical and microbiological examination. Collection, preservation and transportation of water samples were conducted according to the (A.P.H.A., 1998). 2-a-Sampling Method: by manual sampling. 2-b-Type of sample: composite samples were obtained by collecting at many different sampling points and depths. 2-c-Sample Containers: *For chemical analysis: Clean, dry, screw capped plastic bottles of one liter capacity were used for collecting the water samples. 30
*For microbiological analysis: Clean, dry, screw capped glass bottles of 150 ml capacity were used for collecting the water samples. The bottles were sterilized in hot air oven at 170° C for 60 min. 2-d-Procedures Before filling, sample bottles were rinsed two or three times with the water being collected. Surface scum was avoided. Special weighted containers are required for sampling water from depths. The container was filled fully (for organic compound determinations) but space was leaved for aeration, mixing, etc. (for microbiological and inorganic analyses). 3- Physical and chemical analysis of water samples: Temp. ,pH ,DO ,Hd ,TS ,TDS ,TSS ,EC ,salinity ,chloride ,alk. , PO4 and NO2 were determined according to methods described by (A.P.H.A., 1998), but TAN was determined according to described by (A.P.H.A, 1989) while organic matter was determined as described by (Boyd, 1979). 3-1-Temperature: Temperature of water samples was measured at the time of sampling by means of an ordinary thermometer (range 0 – 100 °C). 3-2-Measurement of pH: pH values of water samples were determined by means of electrometric pH meter (pHep® HI 98107- Italy). 3-3- Dissolved Oxygen (DO): Dissolved oxygen was measured by membrane electrode method through using portable waterproof DO meter (HI 9142-Italy) according to (Hargreaves and Tucker, 2002).
31
3-4-Total Hardness (Hd): Hardness of water samples was measured by ethylene diamine tetra acetic acid (EDTA) titrimetric Method. 3-5 Total Solids (TS): Procedures: Clean dish was heated to 103 to 105°C for 1 h. Dish was weighed immediately before use. 100 ml of well-mixed sample was pipetted to a preweighed dish and was evaporated to dryness in a drying oven at 103–105°C. The evaporated sample was dried for at least 1 h in an oven at 103 to 105°C; dish was cooled in desiccator and was weighed. Cycle of drying, cooling, desiccating, and weighing was repeated until a constant weight was obtained. The total solids were represented by increase in weight over that of the empty dish. Calculation: (A – B) x 1000 mg TS /L = ـــــــــــــــــــــــــــــــــــــــــــــــــــــــــــــــــــــــ Volume of water sample in milliliters Where: A = weight of dried residues + dish (mg). B = weight of dish (mg). 3-6-Total Dissolved Solids (TDS) TDS were measured by using waterproof EC/TDS/NaCl % /°C meter (HI 9835- Italy). 3-7-Total Suspended Solids (TSS): TSS was obtained by calculation of the difference between total dissolved solids and total solids. TSS (g/L) = TS – TDS
32
3-8- Electrical Conductivity (EC): EC was measured by using waterproof EC/TDS/NaCl/°C meter (HI 9835- Italy). 3-9-Salinity (NaCl %): Salinity was measured by using waterproof EC/TDS/NaCl/°C meter (HI 9835- Italy). 3-10-Chlorides: Chlorides were determined by using (argentometric method). 3-11-Total Alkalinity: Total alk. was determined by Potentiometric titration to end-point pH. 3-12-Organic matter: Organic matter was determined by using chemical oxygen demand that was measured using the ‗heat-of-dilution‘ dichromate oxidation method. 3-13-Total Ammonia Nitrogen (TAN): TAN was determined by using (direct nesslerization method). 3-14-Nitrite (NO2): Nitrite was determined by using colorimetric method. 3-15-Phosphate (PO4): PO4 was determined by using the stannous chloride colorimetric method.
4-Microbiological examination of water samples:
33
TCC, T. coliform C. and TFC were determined according to methods described by A.P.H.A. (1998). 4-1-Heterotrophic plate count (the standard plate count) Heterotrophic plate count was determined by pour plate method. 4-2-Total fungal count (TFC) of water: TFC was determined by using Pour Plate Technique. 4-3-Standard Total Coliform Fermentation Technique T. Coliform C. was determined by using multiple tube fermentation technique. 5-Evaluation of some fish performance parameters: 5-1-Fish body size (BS) and body weight (BW): A total 100 fish were randomly selected from 10 examined ponds to measure final body weight, organs weight as well as the fish body size to the nearest gram and cm² and finally organosomatic indices %. 5-2- Organosomatic indices: Immediately after dissection was made, the liver, spleen were removed and weighed for calculating their weights and somatic indices. Organosomatic indices are ratios of organ weight to body weight as described by (Goede and Barton, 1990). 6-Histopathological Investigation: (tissue sampling, processing and light microscopic studies). Samples were collected from gills, liver, spleen and brain of the Tilapia fish and fixed in the 10% buffered formalin for 24 h, dehydrate through a graded series of ethanol and clear with xylene solutions. They were embedded in a block using melted paraffin .The paraffin blocks were sectioned at 4-5 μm thickness using a rotary microtome and stained with
34
hematoxylin and eosin (H&E) according to (Bancroft and David, 1996).The tissue sections were examined for histopathological alterations by a Nikon E600 light microscope and photographed by a Nikon DXM 1200 digital camera. 7-Statistical Analysis: Descriptive and analytical tests are carried out using student ―LSD to compare between the different results of physicochemical character and microbial load within ponds and in between ponds during seasons of the study. The highly significant differences and correlations were at P≤0.001, moderate significance at P≤0.005 and the less significance were at P≤0.05 Pearson 2-tailed correlation test is used (SPSS, 16).
35
Pond disinfection
Pond fertilization
Formulated ration
Water analysis
Vet. Supervision
5
Twice/ week
Electricity
Removal upper layer
Poultry litter
Used (25% protein) + poultry litter
No
No
Electricity
Removal of upper layer
No
Used (25% protein)
No
No
No
Used (25% protein) + broken rice
No
No
Poultry litter
Used (25% protein)
No
No
No
Used(25% protein)
No
No
Aerators
7
Fuel material
E
2
Rate
D
3
Water Exchange Electricity
C
50
Earthen ponds
B
Hatcheries
5
Farm compartments Rearing ponds
A
Farm area (acre)
Facility
Farm
Table (1-a): Environmental monitoring of the studied aquaculture farms.
Yes
No
No
24hr/ day
Kerosene
Yes
6
3
2
No
No
Twice/ week
13.5
4
3
Yes
No
12hr /day
Kerosene
15
7
2
Yes
Used
Triple/ week
Electricity
36
Dryness 15 d. +removal upper layer Dryness 15 d. + removal upper layer Lime + removal of upper layer
Table (1-b): Environmental monitoring of the studied earthen ponds.
Farms
Pond Studied Pond depth ponds direction (m)
1
A 2 3
B 4 5
C 6 7
D 8 9
E 10
Pond width with wind direction Pond width opposite to wind direction Pond width with wind direction
No. of No. of Pond Source of Length Reared cultivated cultivated area Tilapia's :width spp. Tilapia Mugil (acre) fries ratio (acre) (acre) 1
2: 1
1.5 1.5
2: 1
8
2:1
1.5 - 2 6
2:1
1.25
Square 1: 1
1.5 - 2
Pond width 1.5-2 with wind direction Pond width 1.3- 1.8 with wind direction
1.25
Square 1: 1
1.5
2: 1
1.5
4: 1
2
Square 1: 1
3
2: 1
Tilapia only Tilapia and Mugil
Tilapia only Tilapia and Mugil Tilapia and Mugil
37
Source of Mugil's fingerlings
20,000
Out farm (ElFayoum)
ــــ
ــــ
10,000
In farm
500
Alex.
20,000
In farm
ــــ
ــــ
10,000
Out farm (ElFayoum)
1000
Kafr el shekh
10,000
Out farm (ElFayoum)
500
Kafr el shekh
Table (2): Seasonal mean value ± SE of temperature (C°) of water in each examined pond. Pond Season Spring Summer Autumn
1
2
3
4
5
6
7
8
9
10
Total
26.50 ± 0.86 28.08 ± 0.83 20.25 ± 0.66
26.75 ± 1.36 29.25 ± 0.69 21.25 ± 0.66
26.92 ± 1.43 30.42 ± 0.65 22.75 ± 0.85
26.92 ± 1.43 30.25 ± 1.20 21.25 ± 0.66
28.17 ± 1.20 30.42 ± 1.25 21.50 ± 0.20
28.17 ± 0.99 29.00 ± 0.72 21.38 ± 0.24
25.58 ± 1.20 28.50 ± 0.18 21.50 ± 0.20
27.42 ± 0.58 28.33 ± 0.73 22.50 ± 0.20
25.08 ± 1.39 27.50 ± 0.52 21.50 ± 1.71
25.92 ± 1.59 28.58 ± 0.71 21.25 ± 1.39
26.74 ± 0.38 29.03 ± 0.27 21.51 ± 0.26
Table (3): Seasonal mean values ± SE of dissolved oxygen (mg/L) of water in each examined pond. Pond Season Spring Summer Autumn
1
2
3
4
5
6
7
8
9
10
Total
11.35 ± 2.25 9.93 ± 1.29 9.55 ± 0.32
9.98 ± 0.40 10.86 ± 1.07 10.38 ± 0.09
13.23 ± 0.81 13.58 ± 1.39 12.50 ± 0.34
13.44 ± 0.51 11.98 ± 1.19 14.72 ± 0.92
13.23 ± 0.28 11.93 ± 0.29 13.34 ± 0.70
11.63 ± 0.62 12.21 ± 0.36 12.64 ± 0.13
10.55 ± 0.67 12.31 ± 0.49 13.86 ± 0.32
9.28 ± 0.93 11.12 ± 0.45 12.39 ± 0.38
11.10 ± 0.68 11.62 ± 0.64 10.51 ± 0.49
11.55 ± 0.20 14.28 ± 0.44 10.88 ± 0.58
11.54 ± 0.32 11.98 ± 0.30 12.08 ± 0.29
38
Table (4): Seasonal mean values ± SE of chloride (mg/ L) of water in each examined pond. Pond Season Spring Summer Autumn
1
2
3
4
5
6
7
8
9
10
Total
2628 ± 76.64 2281.83 ± 58.41 2439.75 ± 60.87
2704.17 ± 76.22 2187.50 ± 76.02 2205.00 ± 85.39
2858.33 ± 132.77 3555.83 ± 98.96 3817.00 ± 6.44
3348.33 ± 124.64 4166.00 ± 67.44 4240.00 ± 34.16
1483.33 ± 194.04 5112.50 ± 669.38 6960.75 ± 14.91
2469.67 ± 28.96 5198.00 ± 589.47 6967.50 ± 25.62
1447.50 ± 47.99 1651.67 ± 61.73 1983.75 ± 12.81
1383.33 ± 130.31 1602.50 ± 55.13 1703.13 ± 96.07
1505.50 ± 29.14 1487.50 ± 74.65 1256.25 ± 106.74
1552.17 ± 36.41 1479.17 ± 41.54 1343.75 ± 64.04
2138.03 ± 95.64 2872.25 ± 203.83 3291.69 ± 329.50
Table (5): Seasonal mean values ± SE of hardness (mg/ L) of water in each examined pond. Pond Season Spring Summer Autumn
1
2
3
4
5
6
7
8
9
10
Total
1480.00 ± 20.94 1398.33 ± 31.67 1404.50 ± 36.25
1540.00 ± 23.63 1390.00 ± 43.20 1453.25 ± 27.79
1901.67 ± 41.37 1948.33 ± 28.33 2073.25 ± 27.79
1950.00 ± 44.63 2235.00 ± 17.61 2157.00 ± 61.87
1034.17 ± 224.95 2831.67 ± 325.69 3833.75 ± 12.81
1545.83 ± 167.82 3238.33 ± 58.83 3774.38 ± 66.18
925.83 ± 11.21 1015.00 ± 19.92 1138.75 ± 29.89
855.83 ± 81.07 999.17 ± 24.85 1031.88 ± 57.64
1030.83 ± 39.67 1106.67 ± 74.19 935.63 ± 104.60
1179.17 ± 71.04 1035.83 ± 34.07 951.56 ± 65.11
1344.33 ± 56.66 1719.83 ± 105.27 1875.39 ± 168.27
39
Table (6): Seasonal Mean values ± SE of pH of water in each examined pond. pond season Spring Summer Autumn
1
2
3
4
5
6
7
8
9
10
Total
7.61 ± 0.01 8.02 ± 0.07 8.25 ± 0.02
7.69 ± 0.03 7.88 ± 0.09 7.92 ± 0.11
8.04 ± 0.07 8.23 ± 0.14 8.36 ± 0.02
8.10 ± 0.08 8.24 ± 0.15 8.50 ± 0.00
7.57 ± 0.18 8.06 ± 0.11 8.25 ± 0.02
7.99 ± 0.04 8.01 ± 0.12 8.46 ± 0.02
8.17 ± 0.03 8.30 ± 0.12 8.80 ± 0.00
7.54 ± 0.68 8.32 ± 0.10 8.67 ± 0.06
7.50 ± 0.03 7.93 ± 0.10 8.35 ± 0.02
7.66 ± 0.06 8.03 ± 0.04 8.36 ± 0.02
7.79 ± 0.07 8.10 ± 0.04 8.39 ± 0.04
Table (7): Seasonal mean values ± SE of nitrite (mg/L N) of water in each examined pond. Pond
1
2
3
4
5
6
7
8
9
10
Total
Spring
0.03 ± 0.00
0.03 ± 0.01
0.49 ± 0.05
0.07 ± 0.00
0.06 ± 0.01
0.05 ± 0.00
0.02 ± 0.00
0.02 ± 0.00
0.02 ± 0.01
0.02 ± 0.00
0.08 ± 0.02
Summer
0.05 ± 0.01
0.03 ± 0.00
0.20 ± 0.04
0.08 ± 0.00
0.06 ± 0.01
0.05 ± 0.01
0.02 ± 0.00
0.02 ± 0.00
0.02 ± 0.00
0.03 ± 0.01
0.06 ± 0.01
Autumn
0.02 ± 0.00
0.02 ± 0.00
0.64 ± 0.05
0.09 ± 0.00
0.06 ± 0.00
0.07 ± 0.01
0.03 ± 0.01
0.02 ± 0.00
0.02 ± 0.00
0.02 ± 0.00
0.10 ± 0.03
Season
40
Table (8): Seasonal mean ± SE of total ammonia nitrogen values (mg/L N) of water . Pond
1
2
3
4
5
6
7
8
9
10
Total
Spring
0.56 ± 0.05
0.85 ± 0.05
0.94 ± 0.03
0.96 ± 0.03
0.52 ± 0.07
0.60 ± 0.06
0.05 ± 0.00
0.05 ± 0.01
0.05 ± 0.01
0.04 ± 0.01
0.46 ± 0.05
Summer
1.18 ± 0.03
1.71 ± 0.14
0.76 ± 0.03
1.10 ± 0.04
0.50 ± 0.04
0.63 ± 0.06
0.08 ± 0.00
0.05 ± 0.01
0.04 ± 0.00
0.06 ± 0.01
0.61 ± 0.07
Autumn
1.40 ± 0.03
1.58 ± 0.35
1.88 ± 0.35
1.58 ± 0.11
0.43 ± 0.01
0.80 ± 0.07
0.08 ± 0.01
0.09 ± 0.00
0.07 ± 0.00
0.07 ± 0.00
0.80 ± 0.12
Season
Table (9): Seasonal mean ± SE of phosphate values (mg/L PO4) of water in each examined pond. Pond
1
2
3
4
5
6
7
8
9
10
Total
Spring
9.92 ± 0.80
13.05 ± 1.41
22.73 ± 0.67
20.58 ± 0.66
27.67 ± 1.38
21.79 ± 2.04
21.31 ± 0.40
18.49 ± 1.13
15.65 ± 0.91
17.88 ± 0.49
18.91 ± 0.71
Summer
14.51 ± 0.83
14.97 ± 0.56
18.50 ± 0.48
22.27 ± 0.69
25.48 ± 2.15
24.26 ± 2.71
21.42 ± 0.68
19.10 ± 0.98
15.62 ± 0.38
20.83 ± 1.11
19.69 ± 0.60
Autumn
11.88 ± 1.28
13.30 ± 0.34
24.51 ± 0.76
24.34 ± 0.13
28.51 ± 0.19
29.89 ± 0.73
20.44 ± 1.92
24.08 ± 0.26
17.48 ± 0.21
19.17 ± 0.41
21.36 ± 0.94
Season
41
Table (10): Seasonal mean ± SE of alkalinity values (mg/L) of water. Pond Season Spring Summer Autumn
1
2
3
4
5
6
7
8
9
10
Total
253.50 ± 9.11 368.67 ± 42.77 589.00 ± 53.58
315.17 ± 17.16 349.67 ± 42.51 632.75 ± 40.77
414.00 ± 51.76 320.67 ± 28.69 461.25 ± 67.85
427.17 ± 45.34 372.83 ± 26.89 443.25 ± 70.87
141.67 ± 29.24 417.50 ± 61.36 667.50 ± 76.85
194.58 ± 22.31 409.33 ± 4.61 467.00 ± 10.25
402.42 ± 4.81 354.67 ± 15.70 672.19 ± 16.01
364.83 ± 34.35 419.17 ± 24.90 675.13 ± 20.92
327.00 ± 11.22 318.33 ± 20.40 437.31 ± 31.38
310.33 ± 18.58 316.17 ± 18.60 390.06 ± 49.31
315.07 ± 14.36 364.70 ± 10.70 543.54 ± 22.05
Table (11): Seasonal mean ± SE of electric conductivity values (ms/cm) of water . Pond Season Spring Summer Autumn
1
2
3
4
5
6
7
8
9
10
Total
6.89 ± 0.08 6.77 ± 0.17 6.82 ± 0.01
6.69 ± 0.11 6.89 ± 0.05 7.06 ± 0.05
10.55 ± 0.12 10.57 ± 0.31 11.43 ± 0.15
11.17 ± 0.10 12.08 ± 0.42 12.57 ± 0.02
7.46 ± 0.24 14.44 ± 1.59 18.64 ± 0.07
9.12 ± 0.11 14.90 ± 1.19 18.75 ± 0.24
5.08 ± 0.07 5.81 ± 0.23 6.38 ± 0.16
4.80 ± 0.44 5.44 ± 0.20 5.41 ± 0.47
4.77 ± 0.08 4.72 ± 0.17 3.60 ± 0.30
5.22 ± 0.13 5.04 ± 0.11 4.81 ± 0.34
7.18 ± 0.30 8.66 ± 0.53 9.55 ± 0.85
42
Table (12): Seasonal mean ± SE of total solids (g. /L) of water. Pond Season
1
2
3
4
5
6
7
8
9
10
Total
Spring
5.8 ± 0.07
5.92 ± 0.1
10.8 ± 0.12
11.28 ± 0.1
7.9 ± 0.25
8.98 ± 0.11
3.37 ± 0.04
3.14 ± 0.29
3.67 ± 0.06
4.02 ± 0.1
6.49 ± 0.38
Summer
5.7 ± 0.15
6.08 ± 0.03
10.86 ± 0.32
12.21 ± 0.42
15.19 ± 1.69
14.7 ± 1.17
3.85 ± 0.15
3.56 ± 0.13
3.67 ± 0.14
3.88 ± 0.09
7.97 ± 0.62
Autumn
5.76 ± 0.01
6.25 ± 0.04
11.71 ± 0.16
12.69 ± 0.02
19.76 ± 0.07
18.47 ± 0.23
4.24 ± 0.11
3.54 ± 0.31
2.77 ± 0.23
3.7 ± 0.26
8.89 ± 0.97
Table (13): Seasonal mean ± SE of total suspended solids (g. /L) of water. Pond
1
2
3
4
5
6
7
8
9
10
Total
Spring
2.35 ± 0.03
2.58 ± 0.04
5.53 ± 0.06
5.7 ± 0.05
4.18 ± 0.13
4.42 ± 0.05
0.83 ± 0.01
0.74 ± 0.07
1.29 ± 0.02
1.41 ± 0.03
2.9 ± 0.24
Summer
2.31 ± 0.06
2.65 ± 0.02
5.57 ± 0.16
6.17 ± 0.21
8.03 ± 0.89
7.24 ± 0.57
0.95 ± 0.04
0.84 ± 0.03
1.29 ± 0.05
1.36 ± 0.03
3.64 ± 0.36
Autumn
2.33 ± 0.01
2.72 ± 0.02
6 ± 0.08
6.41 ± 0.01
10.44 ± 0.04
9.09 ± 0.11
1.05 ± 0.03
0.84 ± 0.07
0.97 ± 0.08
1.3 ± 0.09
4.11 ± 0.55
Season
43
Table (14): Seasonal mean ± SE of total dissolved solids (g. /L) of water. Pond
1
2
3
4
5
6
7
8
9
10
Total
Spring
3.45 ± 0.04
3.34 ± 0.06
5.27 ± 0.06
5.59 ± 0.05
3.73 ± 0.12
4.56 ± 0.05
2.54 ± 0.03
2.40 ± 0.22
2.39 ± 0.04
2.61 ± 0.07
3.59 ± 0.15
Summer
3.39 ± 0.09
3.43 ± 0.02
5.29 ± 0.16
6.04 ± 0.21
7.16 ± 0.80
7.46 ± 0.59
2.90 ± 0.12
2.72 ± 0.10
2.38 ± 0.09
2.52 ± 0.06
4.33 ± 0.26
Autumn
3.43 ± 0.01
3.53 ± 0.02
5.71 ± 0.08
6.28 ± 0.01
9.32 ± 0.03
9.38 ± 0.12
3.19 ± 0.08
2.70 ± 0.23
1.80 ± 0.15
2.40 ± 0.17
4.77 ± 0.42
Season
Table (15): Seasonal Mean ± SE of NaCl % of water in each examined pond. Pond Season
1
2
3
4
5
6
7
8
9
10
Total
Spring
13.17 ± 0.19
12.95 ± 0.16
20.58 ± 0.24
21.80 ± 0.19
14.18 ± 0.45
17.33 ± 0.20
9.41 ± 0.12
8.89 ± 0.81
7.46 ± 0.08
9.76 ± 0.22
13.55 ± 0.62
Summer
12.87 ± 0.42
12.65 ± 0.06
20.56 ± 0.60
23.41 ± 0.81
27.63 ± 3.12
28.86 ± 2.37
10.76 ± 0.43
10.07 ± 0.36
8.27 ± 0.30
9.39 ± 0.18
16.45 ± 1.05
Autumn
13.13 ± 0.06
13.01 ± 0.04
22.29 ± 0.30
24.51 ± 0.04
35.79 ± 0.04
35.97 ± 0.29
11.83 ± 0.28
10.01 ± 0.88
6.71 ± 0.53
9.19 ± 0.49
18.24 ± 1.65
44
Table (16): Seasonal mean ± SE of chemical oxygen demand values (mg O2/L) of water. Pond Season Spring Summer Autumn
1
2
3
4
5
6
7
8
9
10
Total
63.97 ± 1.64 70.70 ± 1.16 75.33 ± 1.39
64.77 ± 4.47 66.05 ± 0.71 66.88 ± 3.48
61.48 ± 1.97 46.90 ± 3.20 62.73 ± 2.48
60.75 ± 2.95 59.75 ± 2.09 66.40 ± 3.56
68.33 ± 3.51 64.52 ± 5.02 67.28 ± 3.14
52.57 ± 5.15 56.48 ± 7.40 63.35 ± 4.61
74.82 ± 0.83 75.11 ± 2.60 83.11 ± 0.98
62.63 ± 6.00 71.01 ± 2.98 83.19 ± 0.30
77.04 ± 7.55 73.52 ± 3.59 97.86 ± 4.23
65.38 ± 1.63 71.23 ± 2.35 71.04 ± 3.05
65.17 ± 1.48 65.53 ± 1.52 73.72 ± 1.91
Table (17): Seasonal [(mean values ± SE) x 102] of total coliform count (CFU/100ml water) of water in each examined pond. Pond Season Spring Summer Autumn
1
2
3
4
5
6
7
8
9
10
Total
7.88 ± 2.23 12.60 ± 1.52 14.30 ± 1.70
8.52 ± 2.96 4.12 ± 1.04 14.30 ± 1.70
16.33 ± 0.33 10.58 ± 2.95 11.40 ± 2.20
17.00 ± 0.45 11.62 ± 3.04 16.50 ± 0.50
2.60 ± 0.64 6.97 ± 2.25 2.15 ± 0.12
4.07 ± 1.16 9.27 ± 2.60 9.95 ± 2.21
3.35 ± 0.56 7.65 ± 2.11 12.60 ± 1.96
2.82 ± 1.29 5.87 ± 2.34 6.35 ± 0.95
8.13 ± 2.24 12.53 ± 2.62 16.50 ± 0.50
8.12 ± 1.83 14.10 ± 2.23 11.65 ± 2.63
7.88 ± 0.80 9.53 ± 0.79 11.57 ± 0.83
45
Table (18): Seasonal [(mean values ± SE) x 102] of total colony count (CFU/ml water) of water in each examined pond. Pond Season Spring Summer Autumn
1
2
3
4
5
6
7
8
9
10
Total
819.33 ± 174.62 561.67 ± 59.74 542.50 ± 25.62
165.17 ± 31.92 202.67 ± 42.81 237.50 ± 8.54
1085 ± 214.41 516.33 ± 187.23 1032.50 ± 78.89
11450 ± 3058.73 6621.67 ± 4404.78 872.50 ± 219.67
880 ± 178.23 520 ± 189.67 645 ± 173.23
247.33 ± 121.33 1006.67 ± 143.94 637.50 ± 253.52
529.75 ± 231.81 373.67 ± 168.35 6150 ± 1537.04
338.67 ± 129.68 222.50 ± 91.09 480 ± 136.63
93.33 ± 49.53 287.17 ± 87.11 302.50 ± 93.93
1948.33 ± 422.85 791.67 ± 183.13 2150 ± 210.16
1755.69 ± 513.95 1110.40 ± 473.37 1305 ± 305.87
Table (19): Seasonal [(mean values ± SE) x 102] of total fungal count (CFU/ml water) of water . Pond Season Spring Summer Autumn
1
2
3
4
5
6
7
8
9
10
Total
16.05 ± 3.74 20.33 ± 2.17 19.75 ± 0.85
47.89 ± 13.65 73.50 ± 19.18 62.75 ± 12.81
53.13 ± 14.35 43.08 ± 28.96 2.40 ± 0.20
13.20 ± 3.94 12.22 ± 8.13 1.59 ± 0.39
14.12 ± 2.78 12.13 ± 2.72 10.48 ± 2.81
11.21 ± 3.44 26.83 ± 4.35 20.83 ± 7.63
6.83 ± 1.13 23.12 ± 12.16 37.76 ± 8.90
26.60 ± 4.22 9.50 ± 4.12 7.20 ± 2.36
20.77 ± 10.93 7.70 ± 2.42 15.75 ± 0.25
89.63 ± 40.17 4.05 ± 1.70 15.00 ± 1.47
29.94 ± 5.38 23.25 ± 4.39 19.35 ± 3.22
46
Table (20-a): Mean values ± SE of physical and chemical parameters of water in each pond during the study period. Pond Parameter Temperature Dissolved oxygen Chloride Hardness pH NO2 Ammonia PO4 Alkalinity Electrical conductivity Total solids Total suspended solids Total dissolved solids NaCl% COD
1
2
3
4
5
6
7
8
9
10
25.53 ± 0.92 10.37 ± 0.94 2451.13 ± 53.35 1430.50 ± 18.55 7.92 ± 0.07 0.03 ± 0.00 1.00 ± 0.09 12.13 ± 0.72 380.56 ± 38.91 6.83 ± 0.07 5.75 ± 0.06
26.31 ± 0.98 10.41 ± 0.42 2385.63 ± 76.65 1462.06 ± 24.99 7.82 ± 0.05 0.03 ± 0.00 1.36 ± 0.14 13.83 ± 0.59 407.50 ± 38.58 6.86 ± 0.06 6.06 ± 0.05
27.19 ± 0.97 13.18 ± 0.59 3359.56 ±119.00 1962.06 ± 25.59 8.19 ± 0.07 0.42 ± 0.05 1.11 ± 0.14 21.59 ± 0.73 390.81 ± 29.78 10.77 ± 0.16 11.05 ± 0.16
26.75 ± 1.13 13.21 ± 0.57 3877.88 ±117.64 2108.63 ± 39.32 8.25 ± 0.07 0.08 ± 0.00 1.17 ± 0.07 22.15 ± 0.51 410.81 ± 25.67 11.86 ± 0.21 11.98 ± 0.21
27.34 ± 1.10 12.77 ± 0.27 4213.63 ±626.95 2408.13 ±324.26 7.92 ± 0.11 0.06 ± 0.00 0.49 ± 0.03 27.06 ± 0.96 376.56 ± 60.87 12.87 ± 1.29 13.60 ± 1.37
26.78 ± 0.92 12.10 ± 0.28 4617.19 ±509.28 2737.66 ±252.71 8.11 ± 0.07 0.05 ± 0.00 0.66 ± 0.04 24.74 ± 1.46 343.19 ± 31.42 13.69 ± 1.08 13.50 ± 1.06
25.47 ± 0.80 12.28 ± 0.42 1663.75 ± 62.83 984.32 ± 42.55 8.37 ± 0.08 0.02 ± 0.00 0.07 ± 0.01 21.36 ± 0.51 456.83 ± 33.99 5.68 ± 0.17 3.77 ± 0.11
26.53 ± 0.69 10.75 ± 0.49 1545.47 ± 64.16 953.59 ± 38.18 8.11 ± 0.27 0.02 ± 0.00 0.06 ± 0.01 20.12 ± 0.80 462.78 ± 35.86 5.19 ± 0.21 3.40 ± 0.14
25.09 ± 0.88 11.15 ± 0.36 1436.41 ± 45.80 1035.47 ± 41.54 7.88 ± 0.09 0.02 ± 0.00 0.05 ± 0.00 16.09 ± 0.41 351.33 ± 16.80 4.46 ± 0.16 3.44 ± 0.12
25.75 ± 1.01 12.41 ± 0.44 1472.66 ±31.97 1068.52 ± 39.35 7.97 ± 0.07 0.02 ± 0.00 0.06 ± 0.00 19.31 ± 0.55 332.45 ± 16.80 5.05 ± 0.11 3.89 ± 0.08
2.33 ± 0.02
2.64 ± 0.02
5.66 ± 0.08
6.05 ± 0.11
7.19 ± 0.72
6.65 ± 0.52
0.94 ± 0.03
0.80 ± 0.03
1.21 ± 0.04
1.36 ± 0.03
3.42 ± 0.03 13.05 ± 0.17 69.33 ± 1.40
3.42 ± 0.03 12.85 ± 0.07 65.78 ± 1.79
5.39 ± 0.08 21.00 ± 0.31 56.33 ± 2.38
5.93 ± 0.11 23.08 ± 0.41 61.79 ± 1.66
6.41 ± 0.65 24.63 ± 2.50 66.64 ± 2.32
6.85 ± 0.54 26.31 ± 2.11 56.73 ± 3.52
2.84 ± 0.08 10.52 ± 0.32 77.77 ± 1.17
2.59 ± 0.11 9.61 ± 0.40 70.91 ± 3.14
2.24 ± 0.08 7.58 ± 0.23 80.93 ± 4.02
2.52 ± 0.05 9.48 ± 0.16 68.99 ± 1.42
47
Table (20-b): [(Mean values ± SE) x 102] of microbial load of water in each pond during the study period. Pond Parameter Total coliform count (CFU /100 ml) Total colony count ( CFU / ml) Total fungal count ( CFU / ml)
1
2
3
4
5
6
7
8
9
10
11.25 ± 1.24 653.50 ± 73.44 18.59 ± 1.62
8.31 ± 1.55 197.31 ± 20.33 61.21 ± 9.29
12.94 ± 1.35 858.63 ± 123.10 36.68 ± 12.57
14.86 ± 1.27 6995 ± 2172.91 9.93 ± 3.43
4.13 ± 1.01 686.25 ± 107.82 12.46 ± 1.56
7.49 ± 1.32 629.63 ± 121.87 19.48 ± 3.14
7.25 ± 1.29 1956.94 ± 723.60 22.27 ± 5.90
4.85 ± 1.05 330.44 ± 68.83 15.34 ± 3.13
11.88 ± 1.49 218.31 ± 48.20 14.61 ± 4.22
11.24 ± 1.36 1565 ± 230.38 38.88 ± 17.51
48
Table (21-a): Seasonal impact on the physical and chemical characters of water from all examined ponds. Season Parameter
Spring Summer Autumn
-2.49*** 5.23*** 0.000 0.000 Dissolved -0.46 -0.54 oxygen 0.27 0.25 ppm ** *** Chloride -734.25 -1153.66 mg/L 0.01 0.000 ** -531.01*** Hardness -375.50 mg/L 0.01 0.000 *** -.31 -.60*** PH 0.000 0.000 ** -228.46*** Alkalinity -49.68 mg/L 0.01 0.000 0.02 -0.02 NO2-N mg/L 0.37 0.46 -0.15 -.34*** NH3-N mg/L 0.15 0.000 -0.8 -2.45* PO4 mg/L 0.41 0.03 * Electrical -1.49 -2.37*** Conductivity 0.04 0.000 ms/cm Total solids -1.48 -2.40** g/L 0.08 0.01 Total -0.74 -1.21* suspendsd 0.13 0.03 solid (g/L) * Total -.75 -1.19*** dissolved 0.04 0.000 solid g/L -2.89* -4.69*** NaCl % 0.04 0.000 -0.35 -8.55*** COD mgO2/L 0.87 0.000 *** Highly significant at P ≤ 0.001 * Low significant at P ≤ 0.05 Temperature C°
Summer Spring Autumn
Autumn Spring Summer
2.49*** 7.72*** -5.22*** -7.72*** 0.000 0.000 0.000 0.000 0.46 -0.08 0.54 0.08 0.27 0.86 0.24 0.86 ** *** 734.2 -419.41 1153.6 419.41 0.01 0.17 0.000 0.17 ** *** 375.5 -155.51 531.01 155.51 0.01 0.32 0.000 0.33 *** *** *** .31 -.29 .60 .29*** 0.000 0.000 0.000 0.000 ** *** *** 49.68 -178.78 228.46 178.78*** 0.01 0.000 0.000 0.000 -0.02 -0.04 0.02 0.04 0.37 0.12 0.46 0.12 *** 0.15 -0.19 .34 0.19 0.15 0.11 0.000 0.11 * 0.8 -1.65 2.45 1.65 0.41 0.13 0.03 0.13 * *** 1.49 -0.88 2.37 0.88 0.04 0.27 0.000 0.27 1.48 -0.92 2.40** 0.92 0.08 0.33 0.01 0.33 * 0.74 -0.47 1.21 0.47 0.13 0.39 0.03 0.39 * *** .75 -0.44 1.19 0.44 0.04 0.27 0.000 0.27 2.89* -1.8 4.69*** 1.8 0.04 0.26 0.000 0.26 *** *** 0.35 -8.19 8.55 8.19*** 0.87 0.000 0.000 0.000 ** significant at P≤0.01
49
Table (21-b): Seasonal impact on the microbial load of water from all examined ponds. Spring Summer Autumn
Summer Spring Autumn
Autumn Spring Summer
Total coliform count (CFU /100 ml)
-164.73 0.13
-368.77* 0.05
164.73 0.13
-204.03 0.09
368.77* 0.05
204.03 0.09
Total colony count ( CFU / ml)
645.29
450.69
-645.29
-194.60
-450.69
194.60
0.31 669.65 0.29
0.52 1059.49 0.13
0.31 -669.65 0.29
0.78 389.84 0.58
0.52 -1059 0.13
0.78 -389.84 0.58
Seasons Parameters
Total fungal count ( CFU / ml) * Low significant at P ≤ 0.05
50
Table (22): Total mean values ± SE of all physical and chemical parameters and microbial load of water from all examined ponds in three different seasons.
Seasons parameter
Spring
Summer
Autumn
Temperature
26.74 ± 0.38
29.03 ± 0.27
21.51 ± 0.26
Dissolved oxygen
11.53 ± 0.32
11.98 ± 0.29
12.07 ± 0.28
Chloride
2138.00 ± 95.64
2872.21 ± 203.83
3291.66 ± 329.49
Hardness
1344.33 ± 56.66
1719.83 ± 105.27
1875.34 ± 168.27
PH
7.79 ± 0.07
8.1 ± 0.03
8.38 ± 0.03
Nitrite
0.08 ± 0.02
0.05 ± 0.01
0.10 ± 0.03
Total ammonia nitrogen
0.46 ± 0.05
0.61 ± 0.07
0.80 ± 0.12
Phosphate
18.91 ± 0.71
19.69 ± 0.60
21.36 ± 0.94
Alkalinity
315.03 ± 14.36
364.70 ± 10.70
543.49 ± 22.05
Electrical conductivity
7.18 ± 0.30
8.66 ± 0.53
9.55 ± 0.85
Total solids
6.49 ± 0.38
7.97 ± 0.62
8.89 ± 0.97
2.90 ± 0.24
3.64 ± 0.36
4.11 ± 0.55
3.59 ± 0.15
4.33 ± 0.26
4.77 ± 0.42
13.55 ± 0.62
16.45 ± 1.05
18.24 ± 1.65
65.17 ± 1.48
65.52 ± 1.51
73.71 ± 1.91
7.88 ± 0.80
9.53 ± 0.79
11.57 ± 0.83
1755.69 ± 513.95
1110.40 ± 473.37
1305.00 ± 305.87
29.94 ± 5.38
23.25 ± 4.39
19.35 ± 3.22
Total suspended solid Total dissolved solid NaCl % Chemical oxygen demand Total coliform count X 102 Total colony count X 102 Total fungal count X 102
51
Table (23):Complete, strong and moderate direct and indirect correlations between values of all physicochemical parameters and microbial load of water from all examined ponds. Parameter 1
Parameter 2 Total dissolved solid 1 Electrical conductivity NaCl% 2 Total dissolved solid NaCl% 3 Total solids Total suspended solid 4 Total solids 5 Electrical conductivity Total dissolved solid 6 Total solids NaCl% 7 NaCl% 8 Total suspended solid 9 Electrical conductivity Total suspended solid 10 Total suspended solid Total dissolved solid Electrical conductivity 11 Total dissolved solid 12 Chloride Hardness 13 NaCl% 14 Electrical conductivity 15 Hardness Total dissolved solid 16 Chloride Total solids 17 NaCl% 18 Hardness Total solids 19 Chloride Total suspended solid 20 Hardness Total suspended solid 21 Electrical conductivity 22 Total dissolved solid 23 Phosphate NaCl% 24 Total solids 25 Total suspended solid 26 PH Alkalinity 27 Temperature Alkalinity 28
52
P-value
≤ 0.001
≤ 0.01
≤ 0.01
R 1 0.999 0.999 0.996 0.992 0.992 0.992 0.978 0.977 0.977 0.971 0.97 0.968 0.968 0.956 0.956 0.953 0.952 0.944 0.931 0.925 0.565 0.565 0.565 0.561 0.553 0.537 - 0.533
Strength
Complete
Strong
Moderate
Moderate
Table (24): Mean values ± SE of some fish performance indices in studied ponds. No. of pond 1 2 3 4 5 6 7 8 9 10 All ponds
Body size BS/ (cm2) 185.9 ± 7.69 137.4 ± 2.76 99.2 ±4.56 100.6 ±4.44 93.2 ±2.97 96.3 ±2.20 204.7 ±3.98 197.6 ±4.65 169.2 ±6.34 156.0 ±16.01 144.01 ±6.34
Final body weight. FBW/g 239.82 ± 8.27 148.85 ± 2.34 78.48 ±5.49 80.69 ±5.02 71.08 ±3.21 74.70 ± 2.38 295.00 ±6.01 309.38 ±4.07 200.50 ±7.78 193.20 ±25.86 169.17 ±12.84
Liver weight LW/g
Liver Somatic Spleen weight Index SW/g LSI 1.61 ± 0.59 1.67 ±0.10 0.81 ±0.01 0.80 ±0.01 0.82 ±0.003 0.81 ±0.003 1.43 ±0.20 1.19 ±0.08 1.95 ±0.06 1.67 ±0.08 1.28 ±0.08
3.79 ± 1.35 2.48 ± 0.11 0.63 ±0.04 0.64 ±0.03 0.58 ±0.02 0.61 ±0.02 4.16 ±0.49 3.67 ±0.22 3.89 ±0.03 3.16 ±0.33 2.36 ±0.25
53
0.53 ±0.16 0.27 ±0.02 0.09 ±0.01 0.09 ±0.01 0.07 ±0.01 0.08 ±0.003 0.21 ±0.03 0.39 ±0.06 0.25 ±0.04 0.37 ±0.10 0.23 ±0.03
Spleen Somatic Index SSI 0.23 ±0.07 0.18 ±0.02 0.11 ±0.003 0.11 ±0.004 0.10 ±0.004 0.11 ±0.002 0.07 ±0.01 0.12 ±0.02 0.12 ±0.01 0.18 ±0.03 0.13 ±0.01
Table (25): Correlations between Body Weight, Body Size, Liver Somatic Index and Spleen Somatic Index.
2
Body size (cm ) Final Body Weight /g LSI SSI *** **
Body size / cm2
Final body weight /g
LSI
SSI
1
.981***
.431**
.172
.000
.002
.232
1
.385**
.137
.006
.342
1
.622***
.981*** .000 .431**
.385**
.002
.006
.172
.137
.622***
.232
.342
.000
Highly significant at P ≤ 0.001
significant at P ≤ 0.01
54
.000 1
Legend -1 :( Fig.1-15): Illustrates the mean values of water quality parameters (physical, chemical and microbial) in each pond during the study period. 20
Dissolved oxygen
10
0 1
2
3
4
5
6
7
8
9
10
Fig.1: Mean values of dissolved oxygen (mg/L) in each pond during the study period. 5000
chloride
4500 4000 3500 3000 2500 2000 1500 1000
500 0 1
2
3
4
5
6
7
8
9
10
Fig.2: Mean values of chloride (mg /L) in each pond during the study period.
55
3000
Hardness
2500 2000 1500 1000 500 0 1
2
3
4
5
6
7
8
9
10
Fig.3: Mean values of hardness (mg /L) in each pond during the study period.
8.5
pH
8.4
8.3 8.2 8.1 8.0 7.9 7.8 7.7 7.6 7.5 1
2
3
4
5
6
7
8
9
Fig.4: Mean values of pH in each pond during the study period. 56
10
0.45
NO2
0.40 0.35 0.30 0.25 0.20 0.15 0.10 0.05 0.00 1
2
3
4
5
6
7
8
9
10
Fig.5: Mean values of NO2 (mg /L N) in each pond during the study period. 1.6
Ammonia
1.4 1.2 1.0 0.8 0.6 0.4 0.2 0.0 1
2
3
4
5
6
7
8
9
10
Fig.6: Mean values of total ammonia nitrogen (mg /L N) in each pond during the study period.
57
30
Phosphate
25 20 15 10 5 0 1
2
3
4
5
6
7
8
9
10
Fig.7: Mean values of phosphate (mg /L PO4) in each pond during the study period. 16
E.C.
14
12 10 8 6 4 2 0 1
2
3
4
5
6
7
8
9
10
Fig.8: Mean values of electrical conductivity (ms/cm) in each pond during the study period. 58
16
Total Solids
14 12 10 8 6 4 2 0 1
2
3
4
5
6
7
8
9
10
Fig.9: Mean values of total solids (g /L) in each pond during the study period.
8
TSS
7 6 5 4 3 2 1 0 1
2
3
4
5
6
7
8
9
10
Fig.10: Mean values of total suspended solids (g /L) in each pond during the study period.
59
8
TDS 7 6 5 4
3 2 1 0
1
2
3
4
5
6
7
8
9
10
Fig.11: Mean values of total dissolved solids (g /L) in each pond during the study period.
30
NaCl % 25 20 15 10
5 0 1
2
3
4
5
6
7
8
9
10
Fig.12: Mean values of NaCl % in each pond during the study period.
60
16
Total Coliform Count
14 12 10 8 6 4 2 0 1
2
3
4
5
6
7
8
9
10
Fig.13: Mean values X 102 of total coliform count (CFU /100 ml) in each pond during the study period. 8000
TCC 7000 6000 5000 4000 3000 2000 1000 0 1
2
3
4
5
6
7
8
9
10
Fig.14: Mean values of X 102 total colony count (CFU /ml) in each pond during the study period.
61
70
TFC 60 50 40 30 20 10 0 1
2
3
4
5
6
7
8
9
10
Fig.15: Mean values X 102 of total fungal count (CFU /ml) in each pond during the study period.
62
Legend 2, (Fig1-18): Demonstrates the seasonal mean values of physicochemical and microbial characters of water in each studied pond. 35
Spring
Summer
Autumn
Temperature (C°)
30 25
20 15 10
5 0 1
2
3
4
5 6 Ponds
7
8
9
10
Fig. 1: Seasonal mean values of temperature (C°) of water in each studied pond. 16
Spring
Summer
Autumn
14
D.O. (ppm)
12 10 8 6 4 2 0 1
2
3
4 5 Ponds
6
7
8
9
10
Fig.2: Seasonal mean values of dissolved oxygen (mg/L) of water in each studied pond. 63
8000
Spring
Summer
Autumn
7000 Chloride (mg/L)
6000 5000 4000 3000 2000 1000 0 1
2
3
4
5 6 Ponds
7
8
9
10
Fig.3: Seasonal mean values of chloride (mg/L) of water in each studied pond.
4500
Spring
Summer
Autumn
4000 Hardness (mg/L)
3500 3000 2500 2000 1500 1000 500 0 1
2
3
4
5 6 Ponds
7
8
9
10
Fig.4: Seasonal mean values of Hardness (mg/L) of water in each studied pond. 64
9.0 Spring
Summer
Autumn
8.5
PH
8.0
7.5
7.0
6.5 1
2
3
4
5
6
7
8
9
10
Ponds
Fig.5: Seasonal mean values of pH of water in each studied pond. 0.7 Spring
Summer
Autumn
0.6
NO2 (mg /L N)
0.5 0.4 0.3 0.2 0.1 0.0 1
2
3
4
5
6
7
8
9
10
Ponds
Fig.6: Seasonal mean values of Nitrite (mg /L N) of water in each studied pond. 65
2.0
Spring
Ammonia (mg /L N)
1.8
Summer
Autumn
1.6 1.4
1.2 1.0 0.8 0.6 0.4 0.2 0.0 1
2
3
4
5 6 Ponds
7
8
9
10
Fig.7: Seasonal mean values of total ammonia nitrogen (mg /L N) of water in each studied pond. 35
Spring
Summer
Autumn
Phosphate (mg /L PO4)
30
25 20 15 10 5 0 1
2
3
4
5 6 Ponds
7
8
9
10
Fig.8: Seasonal mean values of phosphate (mg /L PO4) of water in each studied pond.
66
800
Spring Summer Autumn
Alkalinity (mg /L)
700
600 500 400 300 200 100 0 1
2
3
4
5 6 Ponds
7
8
9
10
Fig.9: Seasonal mean values of alkalinity (mg /L) of water in each studied pond.
20 Spring
16
Summer
14
Autumn
E.C. (ms/cm)
18
12 10 8 6 4 2 0
1
2
3
4
5 6 Ponds
7
8
9
10
Fig.10: Seasonal mean values of electrical conductivity (ms/cm) of water in each studied pond. 67
25
Spring
Summer
Autumn
Total Solids (g. /L)
20 15
10 5
0 1
2
3
4
5 6 Ponds
7
8
9
10
Fig.11: Seasonal mean values of total solids (g. /L) of water in each studied pond.
12
Spring
Summer
Autumn
TSS (g. /L)
10 8 6 4 2 0 1
2
3
4
5 6 Ponds
7
8
9
10
Fig.12: Seasonal mean values of total suspended solids (g. /L) of water in each studied pond. 68
10
Spring
9
Summer
8
Autumn
TDS (g. /L)
7 6 5 4 3 2 1 0 1
2
3
4
5
6
7
8
9
10
Ponds
Fig.13: Seasonal mean values of total dissolved solids (g. /L) of water in each studied pond. 40
Spring
35
Summer Autumn
30 NaCl %
25 20 15 10 5 0 1
2
3
4
5 6 Ponds
7
8
9
10
Fig.14: Seasonal mean values of NaCl % of water in each studied pond.
69
120
Spring
Summer
Autumn
COD (mg O2/L)
100 80 60 40
20 0 1
2
3
4
5 6 Ponds
7
8
9
10
Fig.15: Seasonal mean values of chemical oxygen demand (mg O2/L) of water in each studied pond.
18
Spring
Summer
Autumn
X 102 (CFU/100ml)
16 14 12 10 8 6 4 2 0 1
2
3
4
5 6 Ponds
7
8
9
10
Fig.16: Seasonal mean values of total coliform count X 102 (CFU/100ml) of water in each studied pond.
70
14000
Spring
Summer
Autumn
12000 X 102 (CFU/ml)
10000 8000
6000 4000 2000 0 1
2
3
4
5
6
7
8
9
10
Ponds
Fig.17: Seasonal mean values of total colony count X 102 (CFU/ml) of water in each studied pond.
100
Spring
Summer
Autumn
90
X 102 (CFU/ml)
80 70 60 50 40
30 20 10 0 1
2
3
4
5 6 Ponds
7
8
9
10
Fig.18: Seasonal mean values of total fungal count X 102 (CFU/ml) of water in each studied pond.
71
Legend 3, (Fig.1-18): Demonstrates the total mean values of all physicochemical and microbial characters of water from all studied ponds along the study period. 35
Temperature (C°)
30
25 20 15 10 5 0 spring
summer
autumn
Fig.1: Histogram illustrates the mean values of water temperature (C°) in studied ponds during spring, summer and autumn. 12.2 Dissolved Oxygen (ppm)
12.1 12.0 11.9 11.8 11.7 11.6 11.5 11.4 11.3 spring
summer
autumn
Fig.2: Histogram illustrates the mean values of dissolved oxygen (mg/L) in water of studied ponds during spring, summer and autumn. 72
2000 1800 Hardness (mg/ L)
1600 1400 1200 1000 800 600 400 200
0
spring
summer
autumn
Fig.3: Histogram illustrates the mean values of Hardness (mg/ L) of water in studied ponds during spring, summer and autumn.
3500
Chloride (mg/ L)
3000 2500 2000 1500 1000 500 0 spring
summer
autumn
Fig.4: Histogram illustrates the mean values of chloride (mg/ L) of water in studied ponds during spring, summer and autumn.
73
8.5 8.4 8.3 8.2
PH
8.1 8.0 7.9 7.8 7.7 7.6 7.5 7.4 spring
summer
autumn
Fig.5: Histogram illustrates the mean values of pH of water in studied ponds during spring, summer and autumn.
0.12
Nitrite (mg/L N)
0.10 0.08
0.06 0.04 0.02 0.00 spring
summer
autumn
Fig.6: Histogram illustrates the mean values of nitrite (mg/L N) of water in studied ponds during spring, summer and autumn.
74
0.9
Ammonia (mg/L N)
0.8 0.7
0.6 0.5 0.4 0.3 0.2 0.1 0.0 spring
summer
autumn
Fig.7: Histogram illustrates the mean values of total ammonia nitrogen (mg/L N) of water in studied ponds during spring, summer and autumn.
22.0 Phosphate (mg/L PO4)
21.5 21.0 20.5 20.0 19.5 19.0 18.5 18.0 17.5 spring
summer
autumn
Fig.8: Histogram illustrates the mean values of phosphate (mg/L PO4) of water in studied ponds during spring, summer and autumn.
75
600
Alkalinity (mg/ L)
500 400 300 200 100 0
spring
summer
autumn
Fig.9: Histogram illustrates the mean values of alkalinity (mg/ L) of water in studied ponds during spring, summer and autumn.
Electric Conductivity (ms/ cm)
12 10 8 6 4 2 0 spring
summer
autumn
Fig.10: Histogram illustrates the mean values of electrical conductivity (ms/ cm) of water in studied ponds during spring, summer and autumn.
76
10 9 Total Solids (g. / L)
8 7 6 5 4 3 2 1 0
spring
summer
autumn
Fig.11: Histogram illustrates the mean values of total solids (g/ L) of water in studied ponds during spring, summer and autumn.
Total Suspended Solids (g. / L)
4.5 4.0 3.5 3.0 2.5 2.0 1.5
1.0 0.5 0.0 spring
summer
autumn
Fig.12: Histogram illustrates the mean values of total suspended solids (g. / L) of water in studied ponds during spring, summer and autumn.
77
Total Dissolved Solids (g. / L)
6 5 4 3 2 1 0
spring
summer
autumn
Fig.13: Histogram illustrates the mean values of total dissolved solids (g. / L) of water in studied ponds during spring, summer and autumn.
20 18 16
NaCl %
14 12 10 8 6 4 2 0 spring
summer
autumn
Fig.14: Histogram illustrates the mean values of NaCl % of water in studied ponds during spring, summer and autumn.
78
76
C.O.D. (mg O2/L)
74 72 70
68 66 64
62 60 spring
summer
autumn
Fig.15: Histogram illustrates the mean values of chemical oxygen demand (mg O2/L) of water in studied ponds during spring, summer and autumn.
Total Coliform X 102 (CFU/100ml)
14 12 10 8 6 4 2 0 spring
summer
autumn
Fig16: Histogram illustrates the mean values of total coliform count X 102 (CFU/100ml) of water in studied ponds during spring, summer and autumn. 79
2000 1800 T.C.C. X 102 (CFU/ml)
1600 1400 1200 1000 800 600 400 200 0 spring
summer
autumn
Fig17: Histogram illustrates the mean values of total colony count X 102 (CFU/ml) of water in studied ponds during spring, summer and autumn. 35
T.F.C. X 102 (CFU/ml)
30 25 20 15 10 5 0 spring
summer
autumn
Fig18: Histogram illustrates the mean values of total fungal cont X 102 (CFU/ml) of water in studied ponds during spring, summer and autumn. 80
Legend 4, (Fig.1-28): Illustrates the significant correlations between different physicochemical characters of water within each studied pond. TSS NaCl%
1
2
3
4
5
6
7
8
9
10
Fig.1: Correlation between TSS and NaCl% within each pond.
TSS E.C.
1
2
3
4
5
6
7
8
9
10
Fig.2: Correlation between TSS and EC within each pond.
81
TSS TDS
1
2
3
4
5
6
7
8
9
10
Fig.3: Correlation between TSS and TDS within each pond.
Chloride E.C.
1
2
3
4
5
6
7
8
9
10
Fig.4: Correlation between chloride and EC within each pond.
82
Chloride TDS
1
2
3
4
5
6
7
8
9
10
Fig.5: Correlation between chloride and TDS within each pond.
Hardness Chloride
1
2
3
4
5
6
7
8
9
10
Fig.6: Correlation between Hd and chloride within each pond.
83
Chloride NaCl%
1
2
3
4
5
6
7
8
9
10
Fig.7: Correlation between chloride and NaCl% within each pond.
TDS E.C.
1
2
3
4
5
6
7
8
9
10
Fig.8: Correlation between TDS and EC within each pond.
84
E.C. NaCl%
1
2
3
4
5
6
7
8
9
10
Fig.9: Correlation between EC and NaCl % within each pond. TDS NaCl%
1
2
3
4
5
6
7
8
9
10
Fig.10: Correlation between TDS and NaCl % within each pond.
85
TSS TS
1
2
3
4
5
6
7
8
9
10
Fig.11: Correlation between TSS and TS within each pond.
TS E.C.
1
2
3
4
5
6
7
8
9
10
Fig.12: Correlation between TS and EC within each pond.
86
TDS TS
1
2
3
4
5
6
7
8
9
10
Fig.13: Correlation between TDS and TS within each pond.
TS NaCl%
1
2
3
4
5
6
7
8
9
10
Fig.14: Correlation between TS and NaCl % within each pond.
87
Hardness E.C.
1
2
3
4
5
6
7
8
9
10
Fig.15: Correlation between Hd and EC within each pond.
Hardness TDS
1
2
3
4
5
6
7
8
9
10
Fig.16: Correlation between Hd and TDS within each pond.
88
Chloride TS
1
2
3
4
5
6
7
8
9
10
Fig.17: Correlation between chloride and TS within each pond.
Hardness NaCl %
1
2
3
4
5
6
7
8
9
10
Fig.18: Correlation between Hd and NaCl % within each pond.
89
Hardness TS
1
2
3
4
5
6
7
8
9
10
Fig.19: Correlation between Hd and TS within each pond.
Chloride TSS
1
2
3
4
5
6
7
8
9
10
Fig.20: Correlation between chloride and TSS within each pond.
90
Hardness TSS
1
2
3
4
5
6
7
8
9
10
Fig.21: Correlation between Hd and TSS within each pond.
E.C. Phosphate
1
2
3
4
5
6
7
8
9
10
Fig.22: Correlation between EC and PO4 within each pond.
91
TDS phosphate
1
2
3
4
5
6
7
8
9
10
Fig.23: Correlation between TDS and PO4 within each pond.
NaCl % phosphate
1
2
3
4
5
6
7
8
9
10
Fig.24: Correlation between NaCl % and PO4 within each pond.
92
TS phosphate
1
2
3
4
5
6
7
8
9
10
Fig.25: Correlation between TS and PO4 within each pond.
TSS phosphate
1
2
3
4
5
6
7
8
9
10
Fig.26: Correlation between TSS and PO4 within each pond.
93
Alkalinity
1
2
3
4
5
6
7
8
9
10
Fig.27: Correlation between Alk. and pH within each pond.
Temperature Alkalinity
1
2
3
4
5
6
7
8
9
10
Fig.28: Correlation between temp. and alk. within each pond.
94
Legend 5, (Fig.1-2): Illustrates the mean values of some fish performance parameters and correlations between them. Body size (cm²)
Final body weight(gram)
350 300 250 200 150 100 50 0 1
2
3
4
5
6
7
8
9
10
Fig.1: Illustrates the mean values of BS (cm²) and FBW (g) of fish in each pond. 3.0
SSI
LSI
log (final B.Wt.)
2.5 2.0 1.5 1.0 0.5 0.0 1
2
3
4
5
6
7
8
9
10
Fig.2: Illustrates the mean value of SSI, LSI and log (FBW) of fish from each studied pond. 95
Legend 6, (Micrograph 1-30): Include micrographs of studied fish organs from all ponds. 1
Micrograph (1) Tilapia's gill arch showing dense aggregation of eosinophilic granular cells (EGCs) (H & E 200 X).
2
C
Micrograph (2) Tilapia's gill arch showing perivascular aggregation of EGCs (arrow) with congestion of blood vessel(C) (H & E 400 X). 96
3
EGCs
Micrograph (3) Tilapia's gill arch showing aggregation of EGCs with leucocytic infiltration and edematous fluid exudation (H & E 400 X).
4
Micrograph (4) Tilapia's gill filament showing lamellar hyperplasia and fusion of secondary gill lamellae. (E 400 X). 97
5
Micrograph (5) Tilapia's gill filament showing lamellar telangiectasis (arrow) (H &E400 X).
6
Micrograph (6) Tilapia's gill filament showing congestion of main branchial blood vessel (C) associated with lamellar edema (H & E 100 X).
98
7
Micrograph (7) Tilapia's gill filament showing lamellar hyperplasia associated with lamellar edema (H & E 200 X).
8
Micrograph (8) high power of the previous, note proliferation of lamellar epithelium of secondary gill lamellae with edematous separation of cells (H & E 400 X). 99
9
Micrograph (9) Tilapia's gill filament showing lamellar edema associated with edematous separation and sloughing of lamellar epithelium (H & E 400 X).
10
Micrograph (10) Tilapia's gill filament showing lamellar edema with extensive destruction, sloughing and necrosis of lamellar epithelium (H & E 400 X). 100
11
EGCs
Micrograph (11) Tilapia's gill filament showing sloughing and necrosis of
lamellar
epithelium
with
leucocytic
infiltration
and
melanomacrophage aggregation, note aggregation of EGCs (arrow) (H & E 400 X).
12
Micrograph (12) Tilapia's liver showing vacuolar degeneration of hepatocytes
with
individual
hepatocellular
mononuclear cell aggregation (H & E 400 X). 101
necrosis
and
focal
13
c
Micrograph (13) Tilapia's liver showing congestion of hepatoportal blood vessel (C) and hepatic sinusoid, with diffuse hepatocellular vacuolation (H & E 100 X).
14
Micrograph (14) Tilapia's liver showing hepatocellular vacuolation and necrosis with Kupffer cell activation (arrow) (H & E 400 X). 102
15
Micrograph (15) Tilapia's liver showing dissociation of hepatocytes with individual
hepatocellular
necrosis
and
focal
mononuclear
cell
aggregation (H & E 400 X).
16
Micrograph (16) Tilapia's liver showing perivascular aggregation of mononuclear cells with diffuse hepatocellular necrosis (H & E 200 X).
103
17
Micrograph (17) Tilapia's liver showing hepatocellular necrosis with loss of structural integrity and diffuse mononuclear cell infiltration (H & E 400 X).
18
Micrograph (18) Tilapia's liver showing hepatocellular necrosis with melanomacrophage aggregation with releasing of its content (melanin pigment) (arrow) (H & E 400 X).
104
19
Necrosis
Micrograph (19) Tilapia's liver showing necrosis of pancreatic acinar epithelium of hepatopancrease with melanomacrophage aggregation (H & E 400 X).
20
Micrograph (20) Tilapia's spleen showing lymphoid depletion (arrow) (H & E 200 X).
105
21
Micrograph
(21)
Tilapia's
spleen
showing
activation
of
melanomacrophage center (H & E 200 X).
22 20 20
N
Micrograph (22) Tilapia's spleen showing sub capsular necrosis (N) (H & E 200 X). 106
23
Micrograph (23) Tilapia's spleen showing necrosis of spleenic ellipsoids (arrow) (H & E 400 X).
24
Micrograph (24) Tilapia's spleen showing encysted metacercaria within splenic tissue. (H & E 200 X).
107
25 20 20
Micrograph (25) Tilapia's brain showing brain edema (H & E 400 X).
26 20 20
C
Micrograph (26) Tilapia's brain showing congestion of cerebral blood vessel (C) associated with brain edema and gliossis .
108
27 20 20
N
Edema
N
Micrograph (27)Tilapia's brain showing neuronal degeneration and necrosis (N) associated with brain edema and necrosis (H&E 400 X). 28 20 20
Micrograph (28) Tilapia's brain showing edema, necrosis and demylination with gliosis (H& E 200 X).
109
29 20 20
Micrograph (29) High power of the previous showing vacuolation and necrosis of brain tissue associated with gliosis, note the presence of free RBCs (arrow) (H& E 400 X).
30 20 20
EGCs
N
Micrograph (30) Tilapia's brain showing aggregation of eosinophilic granular cells (EGCs) associated with neuronal degeneration and necrosis (H&E 400). 110
V. DISCUSSION The estimated water quality parameters and their impacts on some fish performance parameters in the field studied earthen ponds will be illustrated. The obtained data are shown in tables and histograms. The tables have descriptive analysis, the significant differences between all parameters within ponds data and between ponds data through the three studied seasons as well as the significant correlations between the estimated and recorded data. Results shown in Table (1-a,b) obtained through collected personnel questionnaires data directed to the farms owners, revealed that total surface area of surveyed farms ranged from 5-50 acres .Surface area of studied ponds ranged from 1-8 acre .Pond depth ranged from 1.3 -2 meter. Number of stocked Tilapia fries ranged 10000-20000 /acre ,while number of stocked Mugill fingerlings ranged 500-1000 /acre .Number of rearing ponds ranged from 3-7 and number of hatcheries from 2-5. Electricity was available in 4/5 of farms. Aerators was available in one farm only and used in two ponds of this farm .The rate of water exchange was varied from 24hr every day to triple/week. Oxygen is dissolved into water at the water air interface. This process is slow but under Aquacultural conditions can be enhanced by agitation (using paddle wheels or other agitators), aeration (using compressed air generated by blowers or compressors) or by supplying pure oxygen into the water as reported by (Asmal, 1996). The elevators power used for water inflow was electricity in 60% of ponds and kerosene in 40% of ponds. Ponds disinfection program was applied via removal of upper surface layer alone or accompanied by use of lime or removal and dryness for 15 days between different crops. Using of fertilizers was applied in farms
111
A, C, D but not in farms B, E. The combined use of both organic and inorganic fertilizers is another strategy for increased production of either fish food organisms or fry as recorded by (Crisman and Beaver, 1990 and Adhikari, 2003).Despite the use of fertilizers increase the organic matter with increase of phosphates which in consequent must be interpreted in conjunction with the concentration of NO3, TSS and DO according to (Asmal, 1996). The food used had 25% protein without additives in 60% of studied ponds but with poultry litter in 20% of ponds and with broken rice in 20% of ponds. The site direction of the pond (mainly its width) Vs wind direction it was noticed that farms A, C, D and E (ponds no.1, 2, 5, 6, 7, 8, 9 and 10) were in the same wind direction which might enhance surface water proper aeration n. Farms B ,C and E (ponds no.3,4,5,6,9,10) reared mixed species namely Tilapia Spp. and Mugil Spp. while farms A and C ( ponds no. 1, 2 ,9,10) reared only Tilapia spp. Cultured Tilapia fry were obtained from external hatcheries (Alexandria and Kafr Al-Shaikh) as in farms A , D and E ( ponds no. 1,2, 7,8, 9,10 ) but from inside farms hatcheries in farms B and C (ponds no. 3,4, 5,6 ). The data in Table (2): illustrate seasonal mean value ± SE, it is indicated that the highest temp. mean value was 29.03 ± 0.07C⁰ in summer .The max. mean value in spring was 28.17 ± 1.20 C⁰ in pond no.5 .The max. mean value in summer was 30.42 ± 1.25 C⁰ in pond no.5 .The max. value mean in autumn was 22.75 ± 0.85 in pond no.3 (Fig.1, Legend 2). It is noticed that pond no.5 had the max. mean values of temp. during spring and summer . The obtained mean values were within the recommended values 112
where the optimum temp. for warm water fish and namely Tilapia spp. is 2830C⁰ as reported by (Boyd ,1990 and Lawson ,1995) . The data in Table (3): Revealed that the max. mean value of DO was 12.08 ± 0.29 mg/L in autumn .The max. mean value in spring was 13.44 ± 0.51 mg/L in pond no.4 .The max. mean value in summer was 14.28 ± 0.44 mg/L in pond no.10 .The max. mean value was 14.72 ± 0.92 mg/L in autumn in pond no.4 (Fig. 2, Legend 2). The solubility of oxygen decreases with increasing salinity; for every 9000 mg/L increase in salinity the DO solubility decreases by 5 %. DO solubility is also severely affected by temp.; at EC 10 ms/m, fresh water can hold 11.29 mg/L while at EC 30 ms/m, the value decreases to 7.56 mg/L. Low DO concentrations cause stress in fish, resulting in reduced appetite, poor growth and production and an increase in susceptibility to infectious diseases. At 0 - 0.3 mg/L Tilapia fry and adults survive for short exposure. At 0.3 - 0.75 mg/L is lethal to Tilapia if exposed to long. At 1 – 5 mg /L lead to impaired growth of Tilapia as reported by (Asmal, 1996). Warm water fish more tolerant to low DO than cold water species, > 5.0 mg/L is recommended, > 1.5 mg/L live for several days, > 1.0 mg/L live for several hours, and < 0.3 mg/L is the lethal concentration as recorded by (Lawson ,1995). The data in Table (4): Demonstrated that the max. mean value of chloride was 3291.69 ± 329.50 mg/L in autumn. The highest mean value in spring was 3348.33 ± 124.64 mg/L in pond no.4. The highest mean value in summer was 5198.00 ± 589.47 mg/L in pond no.6. Max. mean value in autumn was 6967.50 ± 25.62 mg/L in pond no.6 (Fig.3, Legend 2).
113
Summer and autumn characterized by high mean values of chloride in pond no.6 .Chloride contributed to the concentration of TDS and to the salinity of water. At high concentrations chloride had little effect on fish health or behavior and was not considered a problem in inland waters. At high concentrations near the coast, some freshwater fish may show symptoms similar to those given for salinity as reported by (Asmal ,1996).As well as the salinity not only affects osmoregulation but also it influences the concentration of un-ionized ammonia as reported by (Plumb ,2002). The data in Table (5): clarified the max. mean value of Hd was 1875.39 ± 168.27 mg/L in autumn .The highest mean value in spring was 1950.00 ± 44.63 mg/L in pond no.4 The max. mean value in summer was 3238.33 ± 58.83 mg/L in pond no.6 .The max. mean value in autumn was 3833.75 ± 12.81 mg/L in pond no.5 (Fig.4, Legend 2). The current data indicated increased Hd value in hot period and the decreased value in autumn which were exceeded that reported by (Abdo, 2005). However, Hd affects aquaculture species and operations through its chemical interactions with other species in water. Hd levels for aquaculture, as CaCO3/L are classified as, Soft at 0–75 mg/L, moderate at 75–150 mg/L ,hard 1 at 50–300 mg/L and very hard > 300 mg/L as recorded by (Zmeig et al.,1999). The data in Table (6): Indicated that the max. mean value of pH was 8.39 ± 0.04 in autumn .The max. mean value in spring was 8.10 ± 0.08 in pond no.4.The max. mean value in summer was 8.32 ± 0.10 in pond no.8.The max. mean value in autumn was 8.80 ± 0.00 in pond no. 7 (Fig.5, Legend 2).
114
Optimum pH for warm water fish is 6.5–9.0 as desirable range for fish production, 9.0–11.0 slow growth and > 11.0 alkaline death point as reported by (Zmeig et al., 1999). The increased pH values during summer and autumn were coincided with the results of (Abdo, 2005) where recorded pH during hot period ranged from 8.02-8.46 in Abu-Zaˋable pond.In addition to the influence of pH and temp. when increased, the amount of TAN in the toxic NH3 form increased as reported by (Buttner et al.,1993). The data in Table (7): Manifested that the max. mean value of NO2 was 0.10 ± 0.03 mg/L-N in autumn. Max. mean value in spring was 0.49 ± 0.05 mg/L-N in pond no. 3.Summer max. mean value was 0.08 ± 0.00 mg/LN in pond no.4. Max. mean value in autumn was 0.64 ± 0.05 mg/L-N in pond no.3 (Fig.6, Legend 2). Pond no.3 had highest NO2 mean values during spring and autumn. These recorded levels and the probable reduced growth when persisted and accompanied with high chloride level, increased susceptibility to disease were within the levels reported by (Westers, 1991; Buttner et al., 1993 and Lawson, 1995).NO2 concentrations should be interpreted in conjunction with salinity, alk. ,pH , DO and temp. measurements. Higher concentrations resulted in acute anoxia, loss of equilibrium and mortality as revealed by (Asmal, 1996 and Zmeig et al., 1999). While NO2 in freshwater levels above 1.0 ppm will likely be harmful to the fish and at persistently high levels (over 50 ppm) was probably stressful to some species. In addition to, elevated levels in an aquarium may lead to excess algal growth as stated by (Lewbart and Harms, 2008). The pond no.3 had highest temp.; TAN mean values during autumn while it had highest NO2 during autumn and spring, TFC mean values in 115
spring. These results indicated increased pond organic contents. However, if TAN concentration gets high enough, the fish will become lethargic and eventually fall into a coma and die. It also had sub-lethal effects such as reduced growth, poor feed conversion and reduced disease resistance as recorded by (Zelaya et al., 2001). The increased TAN concentration during summer may coincide with the result of (Konsowa, 2007) where he recorded increased TAN than nitrite and nitrate in Quaron Lake. The data in Table (8): Indicated that the max. value of TAN was 0.80 ± 0.12 mg/L-N in autumn .The max. mean value in spring was 0.96 ± 0.03 mg/L-N in pond no.4. Max. mean value in summer was 1.71 ± 0.14 mg/L-N in pond no.2. Highest mean value in autumn was 1.88 ± 0.35 mg/L-N in pond no.3 (Fig.7, Legend 2). This TAN mean value was more than the results recorded by (Lawson, 1995) where optimum TAN was at < 0.05 and at < 1.0 mg l-1 TAN were safe concentrations. High concentrations of TAN cause an increase in the TAN concentration and pH in fish blood. Moreover, high Ammonia and low DO concentration during the summer and spring were the major factors responsible for mortality in sewage-fed fishponds according to (Wrigley et al., 1988).Meanwhile, the maximum mean values in spring and summer were within the toxic levels of TAN according to results of (Zmeig et al., 1999) where they stated that, toxic effects of unionized ammonia were felt at concentrations between 0.6 and 2.0 ppm. They confirmed the influence of some physical characters on ammonia toxicity as temp., pH and low DO which control ratio of toxic NH 3 to NH4+ and increase ammonia toxicity.In addition to (Lewbart and Harms, 2008) who stated that a total ammonia measurement of 3.0 ppm would be deadly at a PH of 8.5 in freshwater but relatively harmless at a pH of 6.0 for a few
116
days. TAN reading represents both forms of ammonia. Moreover, ammonia toxicity increased with decreased DO and increased salinity as stated by (Asmal, 1996). The data in Table (9): revealed that the max. mean value of PO4 was 21.36 ± 0.94 mg/L PO4 in autumn .The max. mean value in spring was 27.67±1.38 mg/L PO4 in pond no.5. Max. mean value in summer was 25.48 ± 2.15 mg/L PO4 in pond no.5. Highest mean value in autumn was 29.89 ± 0.73 mg/L PO4 in pond no. 6 (Fig.8, Legend 2). Elevated PO4 levels can be found where large quantities of organic matter are decomposing. Large quantities of PO4 are applied as fertilizers in agriculture and runoff from these areas often contains elevated concentrations of PO4. Typical PO4 is 300μg/L or more in nutrient- enriched waters. High concentrations of dissolved phosphate may lead to osmotic stress, as is the case with high nitrate concentrations .PO4 concentrations should be interpreted in conjunction with the concentrations of Nitrate , TSS and DO .Site-specific conditions should also be taken into account as mentioned by (Asmal ,1996). Pond no. 1 had min . PO4 mean value characterized by its direction with wind and reared only Tilapia niloticus where the fries obtained from external hatcheries. It had no fertilizers used. The management condition of this pond might enhance minimizing organic load with absence of fertilizers as well; the site direction which allow natural surface water mixing with air temp. and O2 despite of no aerator was available. The data in Table (10): demonstrated that the max. mean value of alk. was 543.54 ± 22.05 mg/L in autumn. The highest mean value in spring was 427.17 ± 45.34 mg/L in pond no.4.The max. mean value in summer was 117
419.17 ± 24.90 mg/L in pond no.8.The highest mean value in autumn was 675.13 ± 20.92 mg/L in pond no.8 (Fig. 9, Legend 2) However, all the max. mean values in all seasons were higher than that reported by many authors .Where alk. in excess of 300 ppm didn‘t adversely affect fish but interfere with action of commonly used disinfectants (namely copper sulphate) as recorded by (Buttner et al. ,1993).As well, alk. in natural freshwater systems ranged from 5 mg l -1 to 500 mg l-1 as reported by (Lawson ,1995) .Moreover, 20 – 400 mg/L alk. was sufficient for most aquaculture purposes and 100 or 150 mg/L was desirable as recorded by (Zmeig et al. , 1999). Freshwater fish in hard water (100 - 150 mg CaCO3/L) tend to spend less energy on osmoregulation, which results in better growth as revealed by (Amsal ,1996). The data in Table (11): Indicated that the max. mean value of EC was 9.55 ± 0.85 ms/cm in autumn .The max. mean value in spring was 11.17 ± 0.10 ms/cm in pond no.4. The highest mean value in summer was 14.90 ± 1.19 ms/cm in pond no.6 .The max. mean value in autumn was 18.75 ± 0.24 ms/cm in pond no. 6 (Fig. 10, Legend 2). Pond no.6 had maximum EC mean values during summer and autumn .This pond also had maximum mean values of TDS, NaCl % and chlorides during summer, while pond 4 had max. value during spring. The increased values of TDS and EC in hot period were coincided with that recorded by Abdo (2005). However, when EC increased the DO solubility decrease where at EC 10 ms/m, fresh water can hold 11.29 mg/L, while at EC 30 ms/m, the value decreases to 7.56 mg/L as recorded by (Asmal ,1996). The data in Table (12): Demonstrated that the max. mean value of TS was 8.89 ± 0.97 g /L in autumn. The highest mean value in spring was 11.28 118
± 0.1 g /L in pond no.4.The max. mean value in summer was 15.19 ± 1.69 g /L in pond no.5.The max. mean value in autumn was 19.76 ± 0.07 g /L in pond no. 5 (Fig.11, Legend 2). Pond no. 9 had min. EC and TS. This pond had its fry from external hatcheries, reared Tilapia niloticus only (Mono-culture) and its width was in same wind direction. It had no fertilizers but had aerator. The management of this pond threw light on the preferred monoculture to minimize mixed excreta sources of polyculture , and the external source of hatchery (proved to be more valuable than from internal hatchery) and proper surface water aeration which may contribute to the low levels of TS whatever its components ( as no fertilizers used). The data in Table (13): revealed that the max. value of TSS was 4.11 ± 0.55 g /L in autumn . The highest value in spring was 5.53 ± 0.06 g /L in pond no.3.The max. mean value in summer was 8.03 ± 0.89 g /L in pond no. 5. The highest mean value in autumn was 10.44 ± 0.04 g /L in pond no.5 (Fig.12, Legend 2). The recorded mean values in all seasons were detrimental to fish in comparison with the recoded values by (Boyd, 1990), where he stated that TSS concentration had no harmful effects on fisheries at 25 mg l-1, acceptable range was 25–80 mg l-1 and the detrimental value to fisheries was 80 mg l-1. The data in Table (14): Demonstrated that the max. mean value of TDS was 4.77 ± 0.42 g /L in autumn .The max. mean value in spring was 5.59 ± 0.05 g /L in pond no.4. The highest mean value in summer was 7.46 ± 0.59 g /L in pond no.6 .The max. mean value in autumn was 9.38 ± 0.12 g /L in pond no.6 (Fig.13, Legend 2).
119
The data in Table (15): Manifested that the max. mean value of salinity was 18.24 ±1.65 % in autumn .The max. mean value in spring was 21.80 ± 0.19 % in pond no.4 .The highest mean value in summer was 28.86 ± 2.37 % in pond no.6 .The max. mean value in autumn was 35.97 ± 0.29 % in pond no.6 (Fig.14, Legend 2).The max. Values in pond no 6 during summer and autumn were exceeded the levels recorded by (Asmal, 1996) where the increased salinity decreased the solubility of oxygen, for every 9000 mg/L increased in salinity the DO solubility decreases by 5 % . As well as, Nile Tilapia perform better at salinities below 5 ppt and Tilapia prefer salinity < 0.5-1.0 ppt as recorded by (Thomas and Michael ,1999) , while the optimum salinity for Tilapia aurea and Tilapia niloticus was 0–10‰ (0.1-1%) after (Zmeig et al. , 1999). The data in Table (16): Indicated that the max. mean value of COD was 73.72 ± 1.91 mg O2/L in autumn . The highest mean value in spring was 77.04 ± 7.55 mg O2/L in pond no. 9.The max . mean value in summer was 75.11± 2.60 mg O2/L in pond no. 7. The highest mean value in autumn was 97.86 ± 4.23 mg O2/L in pond no.9 (Fig.15, Legend 2). Max. COD mean value was 80.9 mg O2/L in pond no.9 and min. was 56.3 mg O2/L in pond no.3. Pond no.9 had the highest COD mean values during spring and autumn. Sediments from highly turbid source water could contain large amounts of organic matter that exerts a high oxygen demand resulting in oxygen depletion as recorded by (Zmeig et al., 1999). From the previously mentioned data, Pond no.3 had highest mean NO2 values during spring and autumn. It had also the highest temp. and TAN mean values during autumn while it had highest TFC mean value in spring. Pond no.8 had max. alk. values during summer and autumn .Pond
120
no.5 had the max. mean values of temp. and PO4 during spring and summer. It had the max. TS and TSS mean values during summer and autumn. Pond no.6 characterized by max. mean values of chlorides, Hd, EC, TDS and NaCl%. Pond no.5 characterized by max. values of PO4 , TS and TSS. Pond no .7 had the highest pH mean values in summer and autumn. Pond no.8 had max. alk. mean values during summer and autumn .Pond no.9 had the highest COD mean values during spring and autumn. However, the degradation of organic matter and the solubility of oxygen were all influenced by temp., the type of fish, life stage, feeding practices, level of activity and DO concentrations also influence the respiration rate as stated by (Zmeig et al., 1999). The data in Table (17): Figured out that autumn characterized by high mean values T. coliform C. in 7/10 of ponds, where the highest mean value was (16.50 ± 0.50) x 102 CFU/100 ml in pond no.9. On regard to the higher mean value in spring was (17.00 ± 0.45) x 10 2 CFU/100 ml and (16.33 ± 0.33) x 102 CFU/100 ml in ponds no.4 and 3 respectively, while during summer the highest mean value was (12.60 ± 1.52) x102 CFU/100 ml in pond no.1 (Fig.16, Legend 2). The obtained data were so high than that recommended by (WHO, 1989 and Mara and Cairncross (1989) where they indicated that, in wastewater fed ponds, concentrations of 104 CFU /100 ml were acceptable for culture of fish .They assumed that a reduction of one order of magnitude taken place in-pond, so that in-pond concentrations should be less than 103 per 100 ml. In addition to, reliance on coliform standards might overestimate potential health risks, unduly burdening developing countries in their efforts to develop shellfish resources in tropical waters as recorded by (Rice, 1992).
121
The data in Table (18): Indicated that the highest mean values of TCC were noticed in 5/10 of ponds during autumn with max. mean value (6150 ± 1537.04) x102 CFU/ml in pond no.7 followed by 4/10 of ponds during spring with highest mean value (11450 ± 3058.73) x102 CFU/ml in pond no.4, while during summer the highest mean value was (6621.67 ± 4404.78) x102 CFU/ml in pond no.4 (Fig.17, Legend 2).
Some researchers
recommend that the concentration of total bacteria (standard plate count per ml) be used to assess the risk of microbial contamination. They pointed out that if total bacteria reached 1.0 to 5.0 multiplied by 10 4 / ml, then bacteria were likely to appear in muscle tissue as recorded by (Buras et al, 1985). The data in Table (19): Revealed that the highest TFC was recorded in 6/10 of ponds during spring with max. mean value (89.63 ± 40.17) x10 2 CFU/ml in pond no.10, followed by summer figures with max. mean value (73.50 ± 19.18) x102 CFU/ml in pond no.2,while during autumn the highest mean value was (62.75 ± 12.81)x102CFU/ml in pond no.2 (Fig.18, Legend 2). The previously mentioned data confirmed the seasonal impact on the microbial load where autumn characterized by the max. mean values of T. coliform C. and TCC which may be attributed to the availability of organic contents manifested via max. TAN, NO2, PO4 values and the consequent increased DO and COD values utilized by the microbial and fish biochemical activities. On regard to ponds, Pond no.5 had the highest mean values of T. Coliform. C and TCC during summer and spring respectively .This pond contained max. values of PO4 during spring and summer , TS, TSS during
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autumn. The increased heterophilic bacteria were contributed to increased organic load as documented by (Jha et al. ; 2008 ). Pond no.2 had max. mean value of TFC and lowest TCC .This pond site was in same wind direction, reared Tilapia niloticus only and obtained the fry from external hatcheries. It also had no fertilizers used. The ponds 2 & 5 didn‘t use disinfectants only, remove upper layer( no.20 and dry for 15 days in between crops(no.5) that may be contributed to the highest TFC ( no.2) and total coliform count and TCC (no.5). The data in Table (20-a): Illustrated the mean values ± SE of physical and chemical parameters of water in each pond during the study period. The highest mean value of temp. was 27.34 ± 1.10 C° in pond no.5 along the study, while the minimum mean value was 25.09 ± 0.88 C° in pond no.9 along the study . The highest mean value of DO was 13 .21± 0.57 ppm in pond no. 4 while the lowest mean value was 10.37 ± 0.94 ppm in pond no.1 (Fig. 1, Legend 1). The highest mean value of chloride was 4617.19 ± 509.28 mg/L in pond no. 6 while the lowest was 1436.41 ± 45.80 mg/L in pond no. 9 (Fig. 2, Legend 1). The highest mean value of Hd was 2737.66 ± 252.71 mg/L in pond no. 6 while lowest mean value was 953.59 ± 38.18 mg/L in pond no.8 (Fig. 3, Legend 1). The highest mean value of pH was 8.37± 0.08 in pond no.7 while lowest mean value was 7.82 ± 0.05 in pond no.2 (Fig. 4, Legend 1).The highest mean value of NO2 was 0.42 ± 0.05 mg/L-N in pond no.3 while the lower mean value was 0.02 ± 0.00 mg/L-N in ponds no.7, 8, 9 and 10 (Fig. 5 Legend 1). The highest mean value of TAN was 1.36 ± 0.14 mg/L-N in pond no.2 while lowest mean value was 0.05 ± 0.00 mg/L-N in pond no.9 (Fig.6, legend 1). The highest mean value of PO4 was 27.06 ± 0.96 mg/L-PO4 in pond no.5 while lowest mean value 123
was 12.13 ± 0.72 mg/L-PO4 in pond no.1 (Fig. 7, Legend 1). The highest mean value alk. was 462.78 ± 35.86 mg/L in pond no. 8 while the lowest mean value was 332.45 ± 16.80 mg/L in pond no.10 . The highest mean value of EC was 13.69 ± 1.08 ms/cm in pond no. 6 while lowest mean was 4.46 ± 0.16 ms/cm in pond no. 9 (Fig. 8, Legend 1). The highest mean value of TS was 13.60 ± 1.37 g. /L in pond no. 5 while lowest mean value was 3.40 ± 0.14 g. /L in pond no.8 (Fig. 9, Legend 1). The highest mean value of TSS was 7.19 ± 0.72 g. /L in pond no. 5 while lowest mean value was 0.80 ± 0.03 g. /L in pond no.8 (Fig. 10, Legend 1). The highest mean value of TDS was 6.85 ± 0.54 g. /L in pond no.6 while lowest mean value was 2.24 ± 0.08 g. /L in pond no.9 (Fig. 11, Legend 1). The highest mean value of NaCl% was 26.31± 2.11% in pond no. 6 while lowest mean value was 7.58 ± 0.23% in pond no.9 (Fig. 12, Legend 1). The highest mean value of COD was 80.93 ± 4.02 mg O2/L in pond no. 9 while lowest was 56.33 ± 2.38 mg O 2/L in pond no.3. From the obtained data, it is clear that: Pond no. 5 had highest temp., PO4, TS, and TSS. Pond no. 6 had highest mean values of chloride, Hd, EC, TDS, NaCl%. Pond no. 8 had highest mean values of Alkalinity but had lowest mean values of TS, TSS and Hd, NO2. Pond no. 9 had the lowest mean values of TDS,EC, temp., chloride, NaCl %, NO2 and TAN but it had highest mean value of COD .The increased EC with increased temp. and TDS was coincided with (Entz,1973) .However, the low quality problems is associated with high physical and chemical problem such as too high or too low DO concentration and high nitrogenous compounds (ammonia-N and Nitrite-N ) as discussed by (Mmmochi and Mwandya,2003). Pond no. 2 had the highest TAN and lowest pH values which may be attributed to the
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possible nitrification of ammonia to nitrate and nitrite, produced acid which, unless the system was adequately buffered, might cause the pH to fall lower than 6.0, and thus negatively affect bacterially mediated nitrification as reported by (Asmal ,1996). The data in Table (20-b): Revealed the mean values ± SE of microbial load of water in each pond during the study period. The results revealed the highest mean value of T. Coliform C. was recorded from water of pond no.4 (14.86 ± 1.27) x 102 CFU/100 ml while the lowest was from pond no.5 (4.13 ± 1.01) x 102 CFU/100 ml (Fig.13 ,Legend 1). The highest mean value of TCC was in pond no. 4 (6995.00 ± 21.29) x 102 CFU/ml and the lowest was in pond no.2 (197.31 ± 20.33) x 102 CFU/ml (Fig.14, Legend 1) .The highest TFC was recorded from pond no. 2 (61.21 ± 9.29) x 102 CFU/ml and the lowest was in pond no.4 (9.93 ± 3.43) x 102 CFU/ml (Fig.15, Legend 1). From the discussed data, it is obvious that pond no.2 characterized by highest TFC and the lowest TCC .This pond had highest TAN and lowest pH mean values .The temporary increase in ammonia or nitrite result in disease or significant losses due to suppressed immune system and greater susceptibility to pathogens and disease outbreaks as reported by (Yannong, 2003). Pond no.4 was characterized by the highest TCC and T. Coliform C. and the lowest values of TFC .It also had highest DO mean value. Table (21-a): Clarified the seasonal impact (LSD) on the physical and chemical characters of water from all examined ponds. The data indicated highly significant decrease (P ≤ 0.001) in temp. mean values between spring Vs summer and also between autumn Vs spring and summer .No significant difference were noticed in DO mean values between seasons. Chloride was significantly decreased (P = 0.01) in spring Vs summer while highly
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significant decreased (P ≤ 0.001) Vs autumn. Hd was significantly decreased (P ≤ 0.01) in spring Vs summer while highly significant decrease (P ≤ 0.001) was recorded Vs autumn .The data of pH mean values demonstrated highly significant decrease (P ≤ 0.001) between spring Vs summer and autumn ,and also between summer Vs autumn. Alk. decreased significantly (P = 0.01) during spring Vs summer while highly significant increase (P ≤ 0.001) was recorded between autumn Vs spring and summer. No significant difference was noticed in NO2 mean values between seasons. Highly significant decreases (P ≤ 0.001) in TAN mean values were recorded between spring Vs autumn. PO4 concentration was less significantly decreased (P = 0.03) during spring in comparison to autumn. EC was less significantly decreased during spring Vs summer (P = 0.04) while highly significant decrease (P ≤ 0.001) was recorded Vs autumn. TS were significantly decreased during spring Vs autumn (P = 0.01). TSS were less significantly decreased (P = 0.03) during spring Vs autumn. TDS were less significantly decreased during spring Vs summer (P = 0.04) while highly significant decrease (P ≤ 0.001) was recorded between spring Vs autumn .NaCl % was less significantly decreased during spring Vs summer (P = 0.04) while highly significant decrease was recorded during spring Vs autumn (P ≤ 0.001). Highly significant increase in mean values of COD (P ≤ 0.001) was recorded between autumn Vs spring and summer. From the above mentioned data it's clear that the spring season characterized by the significant differences in the mean values of TS, TSS, TDS, EC, alk., pH , PO4-, ammonia , salinity ,COD, Hd and chlorides Vs autumn and summer.
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The significant differences in mean values of these elements during spring may be due to the spring turnover of the pond water with natural mixing of water content and alteration of temp. with microbial activity and the consequent end product of chemicals in water. The absence of significant differences of mean DO values between seasons can be attributed to the absence of aerators in 8/10 of ponds with minimizing surface water movement and the subsequent decreased mixing air O2 into these ponds water. In addition to temp., oxygen solubility was also affected by salinity and impurities. The most common cause of low DO in an aquaculture operation was a high concentration of biodegradable organic matter in the water. This is especially true at high temp. as demonstrated by (Zmeig et al. ,1999). However ,Tilapia can survive below 0.3 mg/L of DO and the aerator were so important to keep morning DO from falling below 0.7-0.8 mg/L when compared with non aerated ponds as reported by (Popma and Masser ,1999) . Table (21-b): Illustrated the seasonal impact on mean differences values of the microbial load in water of all ponds .The seasonal alteration didn‘t reveal significant differences in mean values of microbial load in all ponds except for Total Coliform Count which decreased significantly during spring Vs autumn (P= 0.003). Table (22): Demonstrated the total mean values ± SE of all physicochemical parameters and microbial load of water from all examined ponds in three different seasons. Data was shown in table indicated that the highest mean value of water temp. from all ponds was 29.03 ± 0.027 C° in summer (Fig.1, Legend 3).The highest mean value of DO was 12.07 ± 0.28 ppm in autumn (Fig.2, Legend 3).The highest mean value of chloride was
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3291.66 ± 329.49 mg/L in autumn (Fig.3, Legend 3).The highest mean value of Hd was 1875.34 ± 168.27 mg/L in autumn (Fig.4, Legend 3).The highest mean value of pH was 8.38 ± 0.03 in autumn (Fig.5, Legend 3).The highest mean value of NO2 was 0.1± 0.03 in autumn mg/L-N (Fig.6, Legend 3).The highest mean value of TAN was 0.80 ± 0.12 mg/L-N in autumn (Fig.7, Legend 3).The highest mean value of alk. was 543.49 ± 22.05 mg/L in autumn (Fig.9, Legend 3).The highest mean value of PO4 was 21.36 ± 0.94 mg/L-PO4 in autumn. The highest mean value of EC was 9.55 ± 0.85 ms/cm in autumn. The highest mean value of TS was 8.89 ± 0.97 g /L in autumn. The highest mean value of TSS was 4.11 ± 0.55 g /L in autumn. The highest mean value of TDS was 4.77 ± 0.42 g /L in autumn. The highest mean value of NaCl was 18.24 ± 1.65% in autumn (Fig.8, 10, 11, 12, 13 and 14, Legend 3).The highest mean value of COD was 73.71 ± 1.91 mg O 2/L in autumn (Fig.15, Legend 3).The highest mean value of T. coliform C. was (11.57 ± 0.83) x102 CFU/100ml in autumn (Fig.16, Legend 3).The highest mean value of TCC was 1755.69 ± 513.95 CFU/ml in spring (Fig.17, Legend 3).The highest mean value of TFC was 29.94 ± 5.38 CFU/ml in spring (Fig.18, Legend 3). Microorganisms were often associated with suspended matter; hence low total suspended matter minimizes the potential for transmission of infectious diseases as reported by (Asmal ,1996) .According to the (ECGS ,1998) which accept the guide values of the investigated bacteria by 500 CFU/100 ml of water for Coliform .Meanwhile, it was shown experimentally that either low oxygen, low pH, high ammonia, or high CO2 alone did not lead to bacterial disease, but if two or more of these conditions occurred simultaneously, bacterial infection was much more likely to occur as revealed by (Plumb ,2002).The non significant correlation
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between temp., salinity and pH with the bacterial count was recorded by (Gehan et al ;2005). Table (23): clarified all correlations between all values of physicochemical parameters and microbial load of water from all examined ponds. EC had direct complete highly significant correlation with each of TDS, NaCl %, TS, TSS, chloride and Hd at P ≤ 0.001, r value ranged between 0.956 and 1. (Fig 2, 4, 8, 9, 12 and 15- Legend 4 respectively).TDS had direct complete highly significant correlation with each of TSS, chloride NaCl %, TS , and Hd at P ≤ 0.001 , r value ranged between 0.956 and 0.999 (Fig. 3,5,10 ,13 ,16 - Legend 4 respectively).while it had significant direct moderate correlation with PO4 at P ≤ 0.01, r value was 0.565 (Fig.23Legend 4).The current results coincided with that recorded by (Entz ,1973) where the conductivity increased with the increase in TDS and water temp. TDS is a composite measure of the total amount of material dissolved in it. This parameter is represented in three ways: as TDS, as salinity, or as conductivity. TDS is the mass of the dissolved inorganic and organic compounds in water, whereas salinity measures only the dissolved inorganic content. In water that contains high dissolved organic carbon content, TDS values will be much higher than those of conductivity and salinity as illustrated by (Asmal, 1996). TS had direct complete highly significant correlation with each of TSS,EC, TDS, NaCl % and chloride at P ≤ 0.001 ,R value ranged between 0.953 and 0.996 (Fig 11,12,13,14,17-Legend 4 respectively),while it had direct strong highly significant correlation with Hd at P ≤ 0.001 , r value= 0.944 (Fig 19-Legend 4) and it had significant direct moderate correlation with PO4 at P ≤ 0.01, R value = 0.561 (Fig.25- Legend 4).
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TSS had direct complete highly significant correlation with each of TS, NaCl %, EC, TDS at P ≤ 0.001, r value ranged between 0.977 and 0.996 (Fig. 11, 1, 2, 3 - Legend 4 respectively), while it had direct strong highly significant correlation with chloride and Hd at P ≤ 0.001, r values were 0.931 and 0.925 respectively (Fig 20 and 21-Legend 4 respectively) and it had significant direct moderate correlation with PO4 at P ≤ 0.01, r value was 0.553 (Fig.26- Legend 4). Chlorides had direct complete highly significant correlation with each of EC, TDS, Hd, NaCl %, TS at P ≤ 0.001, r value ranged between 0.953 and 0.971(Fig.4, 5, 6, 7 and 17- legend 4 respectively), while it had direct strong highly significant correlation with TSS at P ≤ 0.001, r value = 0.931(Fig. 20- Legend 4), but it had less significant direct weak correlations with each of PO4, TAN, alk. ,pH and NO2 at P ≤ 0.05, r value ranged between 0.226 and 0.461. Hd had complete highly significant correlation with each of chloride, EC, TDS and NaCl % at P ≤ 0.001, r value ranged between 0.952 and 0.968 (Fig. 6, 15, 16 and 18 –Legend 4 respectively), while it had direct strong highly significant correlation with TS and TSS at P ≤ 0.001, r value = 0.944 and 0.925 respectively (Fig 19 and 21 – Legend 4 respectively), but it had less significant direct weak correlations with each of with PO4, TAN, alk., pH and NO2 at P ≤ 0.05, r value ranged between 0.207 and 0.45. The optimal water Hd necessary for fish to thrive was dependent on the species of fish. Most fish grow well over a wide range of Hd values (30 100 mg Ca CO3 /L). Fish exposed to CaCO3 concentrations that do not meet their species-specific requirements generally show reduced growth,
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disruption of osmotic balance, decreased hatchability and survival of fry, and reduced resistance to disease as reported by (Asmal, 1996). PO4 had significant direct moderate correlation with each of EC, TDS, NaCl%, TS and TSS at P ≤ 0.01, r value ranged between 0.553 and 0.565 (Fig.22, 23, 24, 25 and 26–legend 4respectively). It had less significant direct weak correlations with each of chloride, Hd, NO2and pH at P ≤ 0.05, R value ranged between 0.256 and 0.461.while it had less significant reverse weak correlations with TFC at P ≤ 0.05, r value = - 0.216. Temp. had significant reverse moderate correlation with alk. at P ≤ 0.01 and R value = - 0.533(Fig. 28 –legend 4), while it had less significant reverse weak correlations with each of COD ,pH ,TFC and T. Coliform C. at P ≤ 0.05, R value ranged between - 0.190 and - 0.432. TAN had less significant direct weak correlations with each of TSS, NO2, TS, NaCl%, EC, TDS ,chloride, Hd and T. Coliform C. at P ≤ 0.05, r value ranged between 0.211 and 0.431,while it had less significant reverse weak correlations with COD at P ≤ 0.05, r value = - 0.228. NO2 had less significant direct weak correlations with each of TAN, TSS, TS, NaCl%, TDS, EC, PO4, chloride, Hd and T. Coliform C. at P ≤ 0.05, r value ranged between 0.226 and 0.43. , while it had less significant reverse weak correlations with COD at P ≤ 0.05, r value = - 0.171. Bacterial counts showed no significant correlation with the physical parameters (temp., salinity and pH) as recorded by (Gehan et al., 2005). COD had less significant direct weak correlations with each of T. coliform C., pH and alk. at P ≤ 0.05, R value ranged between 0.229 and 0.284, while it had less significant reverse weak correlations with each of
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temp., TSS, TS, NaCl%, EC, TDS, Hd, chloride, TAN and NO2 at P ≤ 0.05, r value ranged between - 0.171 and - 0.432. Table (24): illustrated the mean values ± SE of some fish performance parameters, the data clarified that the highest mean value of BS was 204.7 ± 3.98 cm² in pond no.7,while the smallest mean value was 93.2 ± 2.97 cm² in pond no.5. The highest mean value of FBW was 309.38 ± 4.07 g in pond no. 8, while the lowest mean value of FBW was 71.08 ± 3.21 g in pond no. 5. The highest mean value of LW was 4.16 ± 0.49 g in pond no. 7 while the lowest mean value of LW was 0.58 ± 0.02 in pond no. 5 .The max. mean value of LSI was 1.95 ± 0.06 in pond no. 9, while the min. mean value was 0.80 ± 0.01in pond no. 4 .The max. mean value of SW was 0.53± 0.16 g in pond no.1 while the min. mean value of SW was 0.07 ± 0.01 g in pond no. 5.The max. mean value of SSI was 0.23 ± 0.07 in pond no.1 while the min. mean value was 0.07± 0.01in pond no.7 (Fig. 1 , Legend 5). From the aforementioned data it is noticed that pond no.5 characterized by the smallest BS, lowest FBW, LW and SW .This pond also had highest pH value during summer and autumn, these values may decrease mean FBW which attributed to the decreased feed consumption and consequent growth rate as mentioned by (Mabaye, 1971; Scott et al., 2005 and El-Sherief and Amal ,2009). At a concentration of 0.19 mg NH3 /L the growth rate of channel catfish was significantly reduced. No health or sublethal effects at ammonia range 0.0 - 0.3 mg/L, at 0.3 - 0.8 possible sublethal effects in warm-water fish occurred in the range of 0.3 - 0.8 mg NH3 /L as illustrated by Asmal (1996). Table (25): Discussed the presence or absence of significant correlation between fish performance parameters (Pearson, 2-tailed).
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Highly significant correlation was recorded between BS & FBW, and also between LSI & SSI at P ≤ 0.001. LSI had significant correlation with SSI and FBW at P ≤ 0.01 (Fig 2, Legend 5). Many of water quality parameters are involved in decreased FBW, as increased pH (6-9) , ammonia (mainly unionized form) (De Croux et al., 2004 ;Scott et al; 2005) ,nitrite ( Carballo and Munoz ,1991 ;Buttner et al. ,1993 ;Konsowa, 2007), increased salinity (in fresh water fish) (Hopkins and Pauly , 1993, Laswon ,1995; Plumb ,2003) , too low (Plumb ,2002), or too high DO (Krom et al ; 1985 , Mmochi and Mwandya, 2003), increased EC, TS, TSS, TDS (Entz, 1973 ;Wetzel ,1983). All interfered with respiration and biochemical activities of fish bubble formation in blood with increased losses. Histopathological Findings Histology and histopathology can be used as bio-monitoring tools or indicators of health in toxicity studies as they provide early warning signs of disease as reported by (Meyers and Hendricks, 1985). Histopathological alterations (HPA) are biomarkers of effect exposure to environmental stressors, revealing prior alterations in physiological and/or biochemical function as demonstrated by (Hinton et al., 1992). The micrographs of the examined fish organs are listed in (Fig.128, Legend 6): The examined fish organs collected from different ponds under investigation revealed the following: 1-Gills The microscopic examination of the Tilapia's gills revealed various histopathological alterations that varied in severity.
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Concerning the gill arch, dense aggregation of eosinophilic granular cells (EGCs) was observed between muscle bundles (Micrograph 1-Legend 6). The lesion associated with congestion of blood vessel with perivascular aggregation of EGCs (Micrograph 2-Legend 6). Aggregation of EGCs associated with leucocytic infiltration and edematous fluid exudation (Micrograph 3-Legend 6).The mentioned less severe lesions were recognized in fish from ponds no.1, 2. The sites of Ponds no. 1, 2 were in wind direction and held monoculture (Tilapia niloticus), the fries were obtained from external hatchery. These ponds were used fertilizers (poultry litter), and despite pond no. 2 had increased mean values of TFC and TCC. The gill filaments showed variable lesions with varying degrees of severity .Mild cases showed lamellar hyperplasia with fusion of secondary gill lamellae by the proliferation of lamellar epithelium (LEp) (Micrograph 4-Legend 6). Areas of telangiectasis of lamellar blood capillaries (LBC) were characterized by dilatation of LBC (Micrograph 5-Legend 6).Lamellar edema (LE) associated with congestion of main branchial blood vessel were observed (Micrograph 6-Legend 6). LHp associated with LE were also noticed (Micrograph 7-Legend 6).The lesions characterized by LEp with edematous separation of lamellar epithelial cells (LEpCs) (Micrograph 8Legend 6).In severe cases of LE , the lesion was associated with necrosis and sloughing of LEp (Micrograph 9 and 10-Legend 6) . The previously mentioned severe lesions were recognized in fish from ponds no. 3 & 4. The necrosis and sloughing of LEp were associated with leucocytic infiltrations in gill filaments and aggregation of Melanomacrophages Cells (MMCs) and EGCs (Micrograph 11-Legend 6).
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Ponds no.3, 4 had polyculture (Tilapia niloticus and Mugil spp.), they were located in opposite direction to the wind. The fries were obtained from their internal hatcheries and these ponds didn‘t use fertilizers. It had increased TAN and NO2 levels (in autumn), TFC, T. Coliform. C and NO2 (in spring),temp.(in summer) and decreased COD (in summer).The increased nitrogen contents in pond no.3 exerts high oxygen demand for chemical which consumed and resulted in oxygen depletion as reported by (Zmeig et al., 1999) .Pond no.4 was characterized by increased T. Coliform .C (in spring and autumn).Increased TAN (in autumn) to toxic level mainly to gills. Histopathological effects, particularly those affecting gill's function might contribute to reduced fish growth through inducing tissue hypoxia as reported by (Wajsbrot et al., 1993). High concentrations of TAN could cause gill damage, reduced the oxygen-carrying capacity of blood, increased the oxygen demand of tissues, damage of red blood cells and the tissues that produced them, and affected osmoregulation according to (Lawson, 1995). In addition to, gills are the first target organ for waterborne pollutants due to the constant contact with the external environment as demonstrated by (Campell et al., 1999) .It is well known that changes in fish gills are among the most recognized responses to environmental pollutants as recorded by (Au ,2004). In the gills hyperemia, fusion of secondary lamellae and telangiectasis were observed; whereas hydropic degenerations in liver were observed in all examined fish as founded by (Yildirim et al., 2006). 2-Liver Liver lesions varied from mild changes which characterized by small foci of vacuolar degeneration of hepatocytes with small focal aggregation of mononuclear cells (MCs) (Micrograph 12-Legend 6) as recognized in fish
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from ponds no. 7, 8 , 9 and 10 , to diffuse hepatocellular degeneration associated with congestion of hepatoportal blood vessel (Micrograph 13Legend 6) .Kupffer cell aggregations associated with hepatocellular necrosis (HN) were noticed (Micrograph 14-Legend 6). Focal leucocytic aggregation associated with dissociation of hepatocytes and individual HN were also recorded (Micrograph 15-Legend 6). Perivascular leucocytic aggregation (Micrograph 16-Legend 6), and diffuse HN with loss of structural integrity and infiltration of MCs were noticed (Micrograph 17-Legend 6).In individual cases the HN was associated with focal aggregation of melanin carrying cells MMCs (Micrograph 18-Legend 6) , as recognized from fish in ponds no. 5, 6 and 9. Concerning the hepatopancrease , the cases of severe HN were associated with necrosis of pancreatic acinar cells with Melanomacrophages infiltrating the necrotic area (Micrograph 19-Legend 6) . Cases of hepatocellular necrosis were associated with severe endothelial destruction of hepatoportal blood vessel associated with intravascular hemolysis and dilatation of sinusoids. These severe hepatopancrease alterations were recognized and repeated in fish from ponds no. 5, 6 and 9. However, exposure to 0.33 mg UIA-N l_ 1induced gill damage and subsequent liver tissue hypoxia associated with blood anemia as illustrated by (Nasr et al., 1998). Ponds no. 5 and 6 were located in same wind direction, held polyculture (Tilapia niloticus and Mugil spp.) and the Fries were obtained from their internal hatcheries. These ponds were using fertilizers that may contribute to the increased PO4, TS and T. Coliform C., alk. and TCC Ponds
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no. 5 and 6 characterized by highest mean values of PO4 , EC,TS, TSS , NaCl% . The increased organic chemicals (may be phosphates) as well organic matter bearing highest value of T. Coliform. C and TCC may be contributed to some of liver severe lesions as denoted by (Zapata-Pe´rez et al., 2000), where they found out liver necrosis had been shown in Nile Tilapia (O. niloticus) after exposure to sediment containing a variety of organic chemicals. Ponds no. 7, 8, 9 and 10 were located in same wind direction and had polyculture (Tilapia niloticus and Mugil spp.). The fries were obtained from external hatcheries, these ponds that held polyculture may exert different sources of excreta and wastes with increased microbial load from these excreta as manifested by increased T. Coliform .C in ponds no.7 and 8. Ponds no.7and 8 had highest mean values of alk. and increased mean value of COD .These ponds didn‘t use fertilizers and had aerators (Paddlewheel).Pond no. 9 and 10 characterized by increased T. coliform C. and COD, but decreased mean values of NaCl%, EC, TS and TDS. Due to the previously recorded values and management procedures applied in the mentioned ponds, the histological alterations noticed in liver can be attributed to the multiple concurrent environmental pollutants under filed condition. Meanwhile, Fish liver is a good indicator of aquatic environmental pollution, where one of the important functions of the liver is to clean of pollutants from the blood coming from the intestine and as detoxification organ involved in the metabolism and excretion of xenobiotic chemicals , as well a constant exposure to toxicants might cause damage to liver tissue according to (Saleh , 1982; Nero et al. 2005 and Marchand et 137
al. 2009). Liver HPA as vacuolation of hepatocytes in the liver might be evident after exposure to the herbicide after (Crestani et al. ,2007). A prominent feature of chronic inflammatory responses was the presence of melanin-or other pigment-containing macrophages which form discrete aggregates of MMCs with sequestered particulate material. These cells were detected in the hepatic parenchyma of control and exposed fish (in the laboratory toxicity test) and in fish from contaminated ponds (in the field study) as illustrated by (Oropesa et al., 2008). The hepatic lesions in fish were characterized by cloudy swelling of hepatocytes, lipoid vacuoles, pyknotic nuclei and focal necrosis which grew with increasing concentration of ammonia according to (Velmurugan et al. ,2009). 3-Spleen The microscopic examination of Tilapia's spleen revealed lymphoid depletion (LD) associated with congestion of splenic sinusoids (Micrograph 20-Legend 6).The lesion associated with activation of Melanomacrophage center (MMC) (Micrograph 21-Legend 6). Large subcapsular areas of necrosis were also observed in advanced severe cases (Micrograph 22Legend 6). The necrosis involved the splenic ellipsoids (Micrograph 23Legend 6).In individual cases, encysted metacercaria in splenic tissue was noticed (Micrograph 24-Legend 6).The severe lesions of spleen were recognized as LD, necrosis in fish from ponds no. 5, 6, 9 and10. In pond no. 9 and 10, fish's liver and hepatopancrease characterized by mild and severe histopathological changes. From the recorded severe hepatic and splenic lesions, it can be postulated that these ponds might be exposed to chemical pollutants, bacteria, fungi or parasites as figured out by (Roganovic-Zafirova and 138
Jordanova, 1998). Moreover , various hazards were associated with wastefed aquaculture: excreta-related pathogens (bacteria, helminthes , protozoans and viruses) , skin irritants, vectors that transmit pathogens and toxic chemicals .Fish passively accumulate microbial contaminants on their surfaces but they rarely penetrate into edible fish flesh or muscle except for trematodes (parasitic tissue flukes) as denoted by (Edwards , 2008). In ponds no. 9 and 10 The absence of fertilizers and use of aerators may contribute to the low values of TS,TSS and EC as consequent, as previously concluded by many researchers (Asmal ,1996 and Zmeig et al. ,1999). These decreased solids decreased the impact of turbid water and the resulted less severe histopathological lesions as illustrated by (RoganovicZafirova and Jordanova, 1998) where they recorded an increased number of macrophages aggregates could be found in the liver and spleen in fish exposed to chemical pollutants, bacteria, fungi or parasites. 4-Brain Brain edema was the main characteristic HPA in most examined cases of Tilapia .The lesion characterized by vacuolation of brain tissue (Micrograph 25-Legend 6). In severe cases the brain showing encephalitis that characterized microscopically by congestion of cerebral blood capillaries (Micrograph 26-Legend 6) associated with neuronal degeneration (Micrograph 27-Legend 6) and severe necrosis and demylination of brain tissue (Micrograph 28-Legend 6) with extravasations of free RBCs (Micrograph 29-Legend 6), in addition to aggregation of EGCs in brain tissue (Micrograph 30-Legend 6).The severe lesions were recognized in fish from ponds no.5, 6, 9 and 10. These ponds were located in same wind direction, the fries were obtained from internal hatchery and had polyculture
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(Tilapia niloticus and Mugil spp.) except ponds no. 9 and 10 had fries from external hatchery. Pond no.5 had max .mean values of temp .and PO4 (in spring and summer), TS and TSS (in summer and autumn), while pond no.6 had max. values of chlorides, TDS, EC, NaCl% (summer and autumn). Ponds no.5, 6, 9 and10 had increased values of alk. Brain of 21-day old carps from alkaline water was metaplastic and smaller than in the control. Cellular anaplasia and nuclear pyknosis was observed in the diencephalon, accompanied by brain necrosis. Nuclei of the neurocytes were hypertrophic as denoted by (Ostaszewska et al., 1999)
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VI. SUMMARY Aquaculture is the fastest growing food-producing sector in the world economically important species as table fish belong to three genera (Tilapia, Oreochromis and Sarotherodon). Tilapia culture has been carried out in different culture systems (earthen pond, concrete tank, super-aerated pond, raceway and cage), management strategies (extensive, semi-intensive or intensive, monoculture, polyculture, monosex, and mixed sex) and in different environment (fresh water and saline water). The current field study was conducted to fulfill the following: 1Ecological monitoring of aquaculture systems in El-Fayoum governorate regarding to systems, management and species. 2-Evaluation of the water quality used in the available and field investigated aquacultures through physical, chemical and microbial water examination on site and at laboratory.3- Investigating the impact of water quality used in aquaculture on fish health via recording of some fish performance parameters as body sizes, organosomatic indices and final body weight .In addition to histopathological profiles of some organs of randomly selected fish at the end of rearing. First: Eco-monitoring of the available earthen ponds management and reared species. Five farms were available and 2 pond from each farm (total 10 ponds) and subjected for field investigation. The data obtained via presented questionnaires to the owners .These data clarified the following; Number of hatcheries ranged from 2-5. Electricity was available in 4/5 of farms. Aerators were available in one farm only and used in two ponds of this farm. The rate of water exchange was varied from 24hr every day to triple/week .The elevators' power used for water inflow was 141
electricity in 60% of ponds and kerosene in 40% of ponds. Site of farms A, C; D and E were in the same wind direction. Pond's disinfection program was applied via removal of upper surface layer alone or accompanied by use of lime or removal and dryness for 15 days between different crops. Farms B, C and E reared mixed species namely Tilapia spp. and Mugil spp. while farms A and C reared only Tilapia spp. Cultured Tilapia fries were obtained from external hatcheries (Alexandria and Kafr Al-Shaikh) as in farms A, D and E but from hatcheries inside farms in farms B and C. Second: Physical and Chemical Character of water from earthen ponds; A Total 160 water samples were subjected to this examination .Mean values of physicochemical characters of water during the study period, it was obvious that; Pond no.1 had min. mean values of PO4 and DO .Pond no. 2 had highest TAN and lowest pH mean values and increased mean values of TFC and TCC. The sites of Ponds no. 1, 2 were in wind direction which allows natural surface water mixing with air temp. and O2 despite of no aerator was available and held monoculture (Tilapia niloticus), the fries were obtained from external hatchery . These ponds were used fertilizers (poultry litter). Pond no.3 had highest NO2 mean values. It had highest temp.; TAN mean values during autumn, TFC mean values in spring. The mean values of TAN in spring and summer are within the toxic levels. Pond no.4 had max. mean value of DO .Pond no. 5 had highest mean values of TS and TSS during summer and autumn. It also had the max. mean values of temp. and PO4 during spring and summer .Pond no.6 had maximum mean values of EC TDS, NaCl% and chlorides during summer and autumn; it also had highest mean values of chloride, Hd, EC, TDS and NaCl% during the study period.
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Pond no.7 had the highest mean values of pH. Pond no. 8 had highest mean values of alk. but had lowest mean values of TS, TSS, NO 2 and Hd. It also had max. mean values of alk. during summer and autumn. Pond no. 9 had the lowest mean values of TDS, temp., chloride, NaCl %, NO2 and TAN but it had highest mean value of COD. This pond had its fries from external hatcheries, reared Tilapia niloticus only (Mono-culture) and its width was in same wind direction. It had no fertilizers but had aerator. Pond no.10 had lowest alk. value. On regard to each Parameter: Maximum temp. mean value was 27.3C⁰ in pond no.5 and the min. was 25.1 C⁰ in pond no. 9. Max. DO mean value was 13.2 ppm in both ponds 3 & 4 while the min. was 10.4 ppm in ponds no. 1 & 2. Max. chloride mean value was 4617.2 mg/L in ponds no. 6 while min. mean value was 1436.4 in ponds no.9. The highest mean value of Hd was 2737.66 ± 252.71 mg/L in pond no. 6 while lowest mean value was 953.59 ± 38.18 mg/L in pond no.8. The highest mean value of pH was 8.37± 0.08 in pond no.7 while lowest mean value was 7.82 ± 0.05 in pond no.2. The highest mean value of NO2 was 0.42 ± 0.05 mg/L-N in pond no.3 while the lower mean value was 0.02 ± 0.00 mg/L-N in ponds no.7, 8, 9 and 10.Max. mean value of TAN was 1.36 mg/L in pond no.2 and the min. mean value was 0.05 mg/L in ponds 9 .Max. mean value of PO4 was 27.1 mg/L PO4 in pond no.5 and min. mean value was 12.1 mg/L PO4 in pond no.1. Elevated PO4 levels can be found where large quantities of organic matter are decomposing .Highest mean value of alk. was 462.8 mg/L in pond no.8 and the lowest mean value was 332.5 mg/L in pond no.10. The highest mean value of EC was 13.69 ± 1.08 ms/cm in pond no. 6 while lowest mean was 4.46 ± 0.16 ms/cm in pond no. 9. Highest mean value of TS was 13.6 g /L in
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pond no.5 and the lowest was 3.4 g /L in ponds 8 and 9 .The max. mean value of TSS was 7.2 g /L in pond no.5 and the min. mean value was 0.8 g /L in pond no.8. The highest mean value of TDS was 6.85 ± 0.54 g /L in pond no.6 while lowest mean value was 2.24 ± 0.08 g /L in pond no.9.The highest mean value of NaCl was 26.31± 2.11% in pond no. 6 while lowest mean value was 7.58 ± 0.23% in pond no.9. The highest mean value of COD was 80.93 ± 4.02 mg O2/L in pond no. 9 while lowest was 56.33 ± 2.38 mg O2/L in pond no.3. On regard seasonal variation in water quality parameters: Summer had the increased mean value of temp. in all ponds with higher values in ponds no. 2 and 5, and it had high mean values of chloride in pond no .6. Autumn had higher DO, Hd, chloride, pH, NO2, TAN, COD, alk., PO4, EC, TS, TSS, TDS and salinity .Spring characterized by the significant differences in the mean values of TDS, EC, alk., pH, salinity, Hd, temp. and chlorides Vs autumn and summer, while it had significant differences in the mean values of TS, TSS, PO4, TAN, COD Vs autumn. The chemical parameters of water revealed the following significant correlations: EC had direct strong correlation with each of TDS, NaCl%, TS, TSS and chloride. TDS had strong highly significant correlation with each of NaCl%, TS, chloride, TSS and Hd .TS had direct complete highly significant correlation with each of TSS, EC, TDS, NaCl% and chloride .TSS had direct complete highly significant correlation with each of TS, NaCl%, EC and TDS .Chlorides had direct complete highly significant correlation with each of EC, TDS, Hd, NaCl% and TS .Hd had complete highly significant correlation with each of chloride, EC, TDS and NaCl% .PO4 had significant direct moderate correlation with each of EC, TDS,
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NaCl%, TS and TSS. PH had less significant direct weak correlations with alk. , PO4, and NaCl%, TDS, EC, COD, TS and TSS. Temp. had significant reverse moderate correlation with alk. . TAN had less significant direct weak correlations with each of TSS, NO2, TS, NaCl%, EC, TDS, chloride, Hd and T. coliform C. .NO2 had less significant direct weak correlations with each of TAN, TSS, TS, NaCl%, TDS, EC, PO4, chloride, Hd and T. Coliform. C. COD had less significant direct weak correlations with each of T. coliform C., pH and alk. Third: Microbial Load of the earthen pond water: The seasonal impact on the microbial load were confirmed where autumn characterized by the max. mean values of T. Coliform .C. which might be attributed to the availability of organic contents manifested via max. TAN, NO2, PO4 values and the consequent increased DO and COD. Values utilized by the microbial and fish biochemical activities. On regard to ponds: Pond no.2 had max. mean value of TFC and lowest TCC .Pond no.10 had highest mean value of TFC in spring. Pond no. 4 was characterized by the highest mean values of TCC and T. coliform C. and the lowest mean value of TFC. Seasonal variation in mean values of microbial load of water from all examined ponds revealed: Summer had the lowest mean value of TCC 1110.40 x102 CFU /ml. Spring characterized by high mean values of TCC in 4/10 of ponds with highest value was 11450x102CFU/ml in pond no.4. It had highest mean value of TFC 89.6 x102 CFU/ml in pond no.10 and the highest TCC mean value of water from all examined ponds was 1755.69 x102 CFU/ml. Summer
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had the lowest TCC mean value .Autumn had the lowest mean value of TFC 19.35x102 CFU /ml. It had high mean values of T. coliform C. in 7/10 of ponds, where the highest mean value was in pond no.9. It had highest mean values of TCC in 5/10 of ponds with max. mean value in pond no.7. The seasonal variation didn‘t reveal significant differences in mean values of microbial load in all ponds except for T. coliform C. which decreased significantly during spring Vs autumn. Fourth; fish performance parameters; A total 100 randomly selected fish from studied ponds were subjected to estimate the performance parameters at the end of rearing period. Pond no.5 characterized by the smallest mean value of BS, lowest mean values of FBW, LW and SW. Pond no.7 had the highest mean value of BS and LW. Highly significant correlation was recorded between BS & FBW, and also between LSI &SSI. LSI had significant correlation with SSI and FBW. Fifth; Histopathological findings of the harvested Tilapia niloticus selected organs from earthen pond at the end of rearing period: HPA are biomarkers of effect exposure to environmental stressors, revealing prior alterations in physiological and/or biochemical function. 1-Gills; the gill arch characterized by dense aggregation of EGCs with congestion of blood vessel with perivascular aggregation of EGCs in Ponds no. 1and 2. The gill filaments characterized by proliferation of LEp with edematous separation of LEpCs, telangiectasis of LBC in Ponds no.3 and 4. Less severe lesions were recognized in fish from ponds no.1 and 2.
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Histopathological effects, particularly those affecting gills function might contribute to reduce fish growth through inducing tissue hypoxia. 2-Liver ;characterized by mild lesions in fish from ponds no. 7,8,9 and 10 as (small foci of VD of hepatocytes with small focal aggregation of MCs) and severe lesions in fish from ponds no. 5, 6 and 9 as (diffuse hepatocellular degeneration ,congestion of hepatoportal blood vessel and HN associated with focal aggregation of MMCs in individual cases .In pond no. 9 , fish's liver and hepatopancrease characterized by mild and severe HPA. The HPA noticed in liver can be attributed to the impact of multiple concurrent environmental pollutants under filed condition. 3-Spleen micrographs revealed LD associated with congestion of splenic sinusoids associated with activation of MMC and necrosis involved the splenic ellipsoids .In individual cases encysted metacercaria in splenic tissue. These severe lesions were recognized in fish from ponds no. 3 and 4. The spleen less severe lesions as LD, necrosis were recognized in fish from ponds no. 5, 6 and 9. From the recorded severe hepatic and splenic lesions, it can be postulated that these ponds might be exposed to chemical pollutants, bacteria, fungi or parasites. 4-Brain micrographs revealed edema, vacuolation of brain tissue, encephalitis denoted by congestion of cerebral blood capillaries and severe necrosis and demylination of brain tissue, extravasations of free RBCs, aggregation of EGCs in brain tissue were recognized in fish from ponds no. 5, 6, 9 and 10.Fish from ponds no. 5, 6, 9 and 10 were characterized by severe lesions in liver, hepatopancrease, and brain.
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VII. CONCLUSION Ecological monitoring of aquaculture systems in El-Fayoum clarified the variety of management programs applied in the examined ponds and their impact on the water quality on regard to the physical, chemical and microbial characters which reflected directly or indirectly on the fish performance parameters. Summer had the increased mean value of temperature in all ponds with higher values in ponds no.2 and 5.It had high values of chloride in pond no.6.Autumn had higher DO, Hd, chloride, pH, NO2, TAN, COD, alk., PO4, EC, TS, TSS, TDS and salinity .Spring revealed the significant differences in the values of TDS, EC, alk., pH, salinity, Hd , temp. and chlorides Vs autumn and summer, while it had significant differences in the values of TS, TSS, PO4, TAN, COD Vs autumn. Most of the examined water chemical parameters showed various levels of direct and indirect correlations included temp., DO, pH, TAN, TS, TSS, TDS ,Chlorides, NaCl%, EC ,Hd , COD, PO4 along the study period. Autumn had lowest TFC mean value and highest mean values of T. Coliform. C in 7/10 of ponds, where pond no 9 had the highest mean value It had the highest mean values of TCC in 5/10 of ponds with maximum mean value in pond no.7.Summer had the lowest TCC mean value .Spring characterized by high mean values of TCC in 4/10 of ponds with highest value in pond no.4. It had highest mean value of TFC and TCC. The seasonal variation didn‘t reveal significant differences in mean values of microbial load in all ponds except for T. Coliform. C which decreased significantly during spring Vs autumn. The gill arch had less severe lesions in fish from Ponds no. 1, 2. The gill filaments had severe lesions in fish from Ponds no. 3,4. Liver mild 148
lesions were in fish from ponds no.7, 8, 9 and 10. The spleen severe lesions were in fish from ponds no.3, 4. Brain severe lesions were recognized in fish from ponds 5, 6, 9 and 10. The studied aquaculture earthen ponds in El-Fayoum governorate had a variety of management programs, the site direction which reflected on the efficiency and availability of aeration, available DO, used fertilizers and the organic matter load and microbial load. Absence of periodical water analysis and supervision, varied rate of water exchange and the disinfectants between crops, the probability of increased wastes and excreta of mixed reared species ,as well the influence of seasonal alteration on the water chemical and microbial contents with consequent interference with fish performance .Significant differences in FBW and the organosomatic indices and the tissue denoted by their severe lesions in all examined vital organs which considered as biomarkers of the multiple environmental pollutants (mainly TAN in toxic levels to gills and hypoxia to brain), TDS, TSS,TS, salinity, Hd ,alk.(liver , spleen and brain ), unknown chemicals may runoff from surrounding agriculture lands, to which fish may be exposed during the study period. It's recommended to examine water periodically, public awareness to minimize recirculating water between ponds or at least increase rate of water exchange and use of aerators, as well as liming or alternative disinfectants between crops. Owners must be alert to the expected seasonal alteration on the water quality of earthen ponds aquaculture from the economic aspect. Further study may be suggested to recognize the singular or concurrent effects of different environmental components on fish performance under seasonal climate change.
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VIII.
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الولخص العشثً يؼزجش اإلعزضساع اىغَن ٍِ ٚأعشع قطبػبد إّزبج األغزيخ ف ٚاىؼبىٌ ٍ .غ صيبدح اىزؼذاد اىغنبّ ٚاىنّ٘ ٚيضداد اىَزطيت ٍِ اىَْزدبد اىغزائيخ اىجسشيخ .أقيَذ اىذساعخ اىسبىيخ إلرَبً اىْقبغ اىجسثيخ اىزبىيخ -1 :اىشصذ اىجيئ ٚألّظَخ اإلعزضساع اىغَن ٚفٍ ٚسبفظخ اىفيً٘ فيَب يخص أّ٘اع اىزغنيِ ,ثشاٍح اىشػبيخ ٗاألّ٘اع اىَغزضسػخ -2 .رقييٌ خ٘دح اىَيبٓ اىَغزخذٍخ ثزيل األّظَخ ٍِ خاله اىفسص اىفيضيبئ , ٚاىنيَيبئٗ ٚاىَينشٗث ٚع٘اء ثبىَ٘قغ اىَيذاّ ٚأٗ ثئعزنَبه اىفسص ٍؼَييب -3.فسص اىزؤثيش اىعبس ىد٘دح ّٗ٘ػيخ اىَيبٓ ػي ٚثؼط ٍؼبييش إّزبج اىغَل اىَغزضسع ٗ اىَشزَيخ ػي ٚزدٌ اىدغٌ ٗ ,صُ اىدغٌ اىْٖبئٍ ٗ ٚؤششاد أٗصاُ ثؼط األػعبء ٍِ األعَبك اىَخزبسح ػش٘ائيب ثْٖبيخ دٗسح اىزشثيخ. أوال :الشصذ الجيئً ألًظوخ اإلستضساع السونً الوتبحخ للذساسخ ,ثشاهح الشعبيخ ,األًىاع: رٌ سصذ ٍ 5ضاسع ثنو ٗازذح ٌٍْٖ ثشمزبُ رشاثيزبُ ( ػذد مي 10 ٚثشك رشاثيخ ) ٍِٗ ثٌ رؼشظذ ٕزٓ اىجشك ىيفس٘صبد عبثقٔ اىزمش ٗ .زصو اىجبزث ػي ٚثيبّبد اىشصذ اىجيئ ٚثؼذ رقذئَ إعزجيبُ ٍ٘سد ثٔ ػذد ٍِ االعئئ اىَ٘خٖٔ ىيَبىل أٗ اىقبئٌ ػي ٚسػبيخ ٕزٓ اىَضاسع اىغَنيخ ( اىجشك اىزشاثيخ ) .خيصذ ٕزٓ اىجيبّبد إىٍ ٚب يي:ٚ ػذد اىَفقغبد رزشاٗاذ ثيِ ,5-2مبّذ اىنٖشثبء ٍزبزخ ف 5/4 ٚاىَضساعٗ .ر٘اخذ ثذاالد اىزٖ٘يخ ثَضسػخ ٗازذح (ػذد 2ثشمخ رشاثيخ) ٗ .رشاٗزذ ٍشاد رغييش اىَيبٓ ٍِ 24عبػخ يٍ٘يب إىٚ ثالثٔ ٍشاد إعج٘ػيب .مَب أعزخذٍذ اىنٖشثبء مَصذس ىيطبقخ ىشفغ اىَيبٓ ٍِ اىَْجغ ىزصو ىيجشمخ فٚ ٍِ ٪60اىَضاسع رسذ اىذساعخ ,ف ٚزيِ أعزخذً اىنيشٗعيِ مَصذس ىيطبقخ ف ٍِ ٪40 ٚاىَضاسع .ر٘اخذ اىَضاسع A,C,Eفّ ٚفظ إردبٓ اىشير .مبُ اىزطٖيش يزٌ ثئصاىخ اىطجقخ اىؼييب ٍِ أسظيخ اىجشمخ فقػ أٗ رضاه ٍغ إعزخذاً اىديش أٗ ردفف ىَذح 15يً٘ ثيِ مو دٗسح رشثيخ ٗاىز ٚرييٖب .مبّذ اىَضاسع ٍ B,C,Eضاسع ٍضدٗخخ اىْ٘ع ثيِ اىجيط ٗ ٚاىج٘س ٙثيَْب ٍ A,Dضاسع ٍْفشدح اىْ٘ع ٕٗ٘ اىجيط .ٚزصيذ ٕزٓ اىَضاسع ػي ٚاىضسيؼخ إٍب ٍِ ٍفقغبد داخييخ ثبىَضسػخ مَب ف ٚاىَضاسع B,C ,أٗزصيذ ػييٖب ٍِ ٍفقغبد ثنفش اىشيخ ٗ اإلعنْذسيخ مَب ثبىَضاسع . A,D,E ثبًيب:الخصبئص الفيضيبئيخ و النيويبئيخ لويبٍ الجشك التشاثيخ :رٌ إخشاء ٕزٓ اإلخزجبساد ػي ٚػذد ( )160ػيْخ ٍيبٓ .فيَب يخص خصبئص مو ثشمخ ٍْفشدح إرعر أُ اىجشمخ (سقٌ )1رَيضد ثؤدٍّ ٚز٘عطبد ىقيٌ األمغديِ اىَزاة ٗ اىف٘عفبد.مّٖ٘ب ف ٚإردبٓ اىشير ٗزصيذ ػي ٚصسيؼزٖب ٍِ ٍفقغبد خبسخيخ ٗ .ىٌ رغزخذً اىَخصجبد غ٘اه دٗسح اىزشثيخ .عبػذد ظشٗف سػبيخ ٕزٓ اىجشمخ ػي ٚاإلقاله ٍِ اىَسز٘ ٙاىؼعٍ٘ ٙغ غيبة اىَخصجبد ,مزىل مُ٘ إردبٕٖب ٍز٘اصيب ٍغ اىشير ٗاىز ٙيغَر ثبىخيػ ثيِ اىَيبٓ اىغطسيخ ٗدسخخ زشاسح اىٖ٘اء ٍٗسز٘آ ٍِ االمغديِ ثبىشغٌ ٍِ غيبة اىجذاالد اىٖ٘ائيخ .مَب إزز٘د ٍيبٕٖب ػي ٚأػيٍ ٚسز٘ ٍِ ٙاألٍّ٘يب ٗأقو ٍز٘عػ ٍِ اه.pH اىجشمخ (سقٌ :)3إزز٘د ػي ٚأػي ٚقيٌ ىيْيزشيزبد ,دسخخ زشاسحٗ,األٍّ٘يب ثبىشثيغ ٗأػيٚ قيٌ ىؼذد اىَغزؼَشاد اىفطشيخ ثبىشثيغ ٗ.صيذ ٍؼذالد األٍّ٘يب ثبىشثيغ ٗ اىخشيف ىيسذٗد اىغبٍخ. اىجشمخ (سقٌ :)4إزز٘د ػي ٚأػي ٚقيٌ ٍِ األمغديِ اىَزاة.اىجشمخ ( سقٌ :)5إزز٘د ػي ٚأػي ٚقيٌ ٍِ اىدغيَبد اىصيجخ اىنييخ ,اىدغيَبد اىصيجخ اىَؼيقخ اىنييخ خاله ٍ٘عَ ٚاىصيف ٗاىخشيف .مزىل أػي ٚقيٌ ىذسخبد اىسشاسح ٗف٘عفبد ثَ٘عَ ٚاىشثيغ ٗاىصيف. اىجشمخ (سقٌ :)6إزز٘د ػي ٚأػي ٚقيٌ ىيَ٘صالد اىنٖشثبئيخ ,اىدغيَبد اىصيجخ اىَزاثخ اىنييخّ ,غت اىَي٘زخ ٗ ,اىني٘سيذاد خاله ٍ٘عَ ٚاىصيف ٗاىخشيف .مَب إزز٘د ػي ٚأػي ٚقيٌ 167
ىيني٘سيذاد ٍ ,نّ٘بد ُػغش اىَيبٓ ,اىَ٘صالد اىنٖشثبئيخ ,اىدغيَبد اىصيجخ اىَزاثخ اىنييخ ّٗغت اىَي٘زخ ػيٍ ٚذاس اىذساعخ ميٖب .اىجشمخ (سقٌ :)7إزز٘د ػي ٚأػي ٚقيٌ ىألط اىٖيذسٗخيْ .ٚاىجشمخ (سقٌ :)8إزز٘د ػي ٚأػي ٚقيٌ ىيقبػذيخ ٗأقو قيٌ اىدغيَبد اىصيجخ اىنييخ ,اىدغيَبد اىصيجخ اىَؼيقخ اىنييخ ,اىْيزشيزبد ٍٗنّ٘بد ُػغش اىَيبٓ ٗمبّذ اىقبػذيخ اىضائذح خاله ٍ٘عَ ٚاىصيف ٗ اىخشيف.اىجشمخ(سقٌ :)9إزز٘د ػي ٚأػي ٚقيٌ ىذسخخ اىسشاسح ,اىدغيَبد اىصيجخ اىَزاثخ اىنييخ,اىني٘سيذادّ ,غت اىَي٘زخ ,اىْيزشيزبد ٗاألٍّ٘يب ٗىنِ أػي ٚقيٌ ىيَزطيت اىنيَيبئ ٚىألمغديِ. ٗرَيضد ٕزٓ اىجشمخ ثزشثيخ اىجيط ٚفقػٗ .زص٘ىٖب ػي ٚاىضسيؼخ ٍِ ٍفقغبد خبسخيخ ٗ ٍ٘اصارٖب إلردبٓ اىشير ٗىٌ رغزخذً اىَخصجبد ٗىنِ إزز٘د ػي ٚثذاالد ٕ٘ائيخ .اىجشمخ (سقٌ :)10إزز٘د ػي ٚأقو قيٌ ىيقبػذيخ. ً°27,3ثبىجشمخ (سقٌ )5 ٗفيَب يخص مو ٍؼيبس فنبّذ أقص ٚدسخبد اىسشاسح ٕٚ 13,2خضء ثبىَييُ٘ ٗأقيٖب ً° 25,1ثبىجشمخ (سقٌ .)9أٍب أػي ٚقيٌ ىألمغديِ اىَزاة فنبّذ ثبىجشمزيِ( . )3,4أػي ٚقيٌ ىيني٘سيذاد مبّذ ٍ4617,2دٌ/ىزش ثبىجشمخ (سقٌ .)6ثيَْب أقو قيَخ مبّذ ٍ1436,4دٌ/ىزش ثبىجشمخ (سقٌ .)9أػي ٚقيٌ ىَنّ٘بد ُػغش اىَيبٓ مبّذ ٍ2737,61دٌ/ىزش ثبىجشمخ (سقٌٗ )6أقو اىقيٌ مبّذ ٍ 953,59دٌ/ىزش ثبىجشمخ (سقٌ .)8أػي ٚقيٌ اه pHمبّذ 8,37فٚ اىجشمخ (سقٌ ٗ )7أقيٖب 7,82ثبىجشمخ (سقٌ .)2أػي ٚقيٌ اىْيزشيزبد مبّذ ٍ 0,42دٌ/ىزش ثبىجشمخ (سقٌٗ )3أقيٖب ٍ0,2دٌ/ىزش ثبىجشمخ (سقٌ .)7,8,9أػي ٚقيٌ األٍّ٘يب مبّذ ٍ1,36دٌ/ىزش ثبىجشمخ (سقٌٗ )2أقيٖب ٍ0,5دٌ/ىزش ثبىجشمخ (سقٌ .)9أػي ٚقيٌ ىيف٘عفبد ٕ٘ ٍ27,1دٌ/ىزش ثبىجشمخ (سقٌ )5 ٗأقيٖب ٕ٘ ٍ12,1دٌ/ىزش ثبىجشمخ (سقٌ .)1أػي ٚقيٌ اىقبػذيخ ٕ٘ ٍ462,8دٌ/ىزش ثبىجشمخ (سقٌ .)8 ٗأقيٖب 332,5مٌ/ىزش ثبىجشمخ (سقٌ .)10أػي ٚقيٌ ىيَ٘صالد اىنٖشثبئيخ ٕ٘ ٍ 13,69ييي ٚعيَْض/عٌ ثبىجشمخ (سقٌ ٗ )6أقيٖب ٍ 4,46ييي ٚعيَْض/عٌ ثبىجشمخ (سقٌ .)9أػي ٚقيٌ ىيدغيَبد اىصيجخ اىنييخ ٕ٘ 13,6خٌ /ىزش ثبىجشمخ (سقٌ ٗ )5أقيٖب 3,4خٌ /ىزش ثبىجشمزيِ ( .)9,8أػي ٚقيٌ ىيدغيَبد اىصيجخ اىَؼيقخ اىنييخ ٕ٘ 7,2خٌ/ىزش ثبىجشمخ (سقٌ ٗ )5أقيٖب 0,8خٌ/ىزش 6,85ثبىجشمخ (سقٌ .)8أػي ٚقيٌ ىيدغيَبد اىصيجخ اىَزاثخ اىنييخ 6,85خٌ/ىزش ثبىجشمخ (سقٌ ٗ )6أقيٖب 2,24خٌ/ىزش ثبىجشمخ (سقٌ .)9 أػي ٚقيٌ ىْغجخ اىَي٘زخ ٕ ٪26,31 ٚثبىجشمخ (سقٌ )6ثيَْب أقيٖب ٪7,58ثبىجشمخ (سقٌ .)9أػي ٚقيٌ ىيَزطيت اىنيَيبئ ٚىألمغديِ ٍٕ 80,93 ٚدٌ/ىزش ثبىجشمخ (سقٌ ٗ )9أقيٖب ٍ 56,33دٌ/ىزش ثبىجشمخ ( سقٌ.)3 فيَب يخص اإلخزالفبد اىَ٘عَيخ ىَؼبييش خ٘دح اىَيبٓ :ى٘زع أّٔ ثبىصيف صادد دسخبد اىسشاسح ثدَيغ اىجشك ٗخبصخ ٍِ اىجشك ( )5-2مَب رَيض ثضيبدح اىني٘سيذاد ثبىجشمخ (سقٌ .)6 رَيضاىخشيف ثضيبدح األمغديِ اىَزاة ٍ ,نّ٘بد ُػغش اىَيبٓ ,رشميض األط اىٖيذسٗخيْ ,ٚاىْيزشيزبد, األٍّ٘يب ,اىَزطيت اىنيَيبئ ٚىألمغديِ ,اىقبػذيخ ,اىف٘عفبد ,اىَ٘صالد اىنٖشثبئيخ ,اىدغيَبد اىصيجخ اىنييخ ,اىدغيَبد اىصيجخ اىَؼيقخ اىنييخ ,اىدغيَبد اىصيجخ اىَزاثخ اىنييخ ,اىَي٘زخ .رَيض اىشثيغ ثئخزالفبد ٍؼْ٘يخ ف ٚقيٌ اىَ٘اد اىصيجخ اىَزاثخ اىنييخ ,اىَ٘صالد اىنٖشثبئيخ ,اىقبػذيخ ,رشميض األط اىٖيذسٗخيْ ,ٚاىَي٘زخٍ,نّ٘بد ُػغش اىَيبٓ ,دسخبد اىسشاسح ,اىني٘سيذاد ٍقبسّخ ثبىخشيف ٗاىصيف .ثيَْب اخزيفذ ٍؼْ٘يب ف ٚقيٌ اىدغيَبد اىصيجخ اىنييخ ,اىدغيَبد اىصيجخ اىَؼيقخ اىنييخ, اىف٘عفبد ,األٍّ٘يب ,اىَزطيت اىنيَيبئ ٚىألمغديِ ,األٍّ٘يب ٍقبسّخ ثَ٘عٌ اىخشيف. أٗظسذ ٍؼبييش خ٘دح اىَيبٓ اىنيَيبئيخ ٗخ٘د ػالقخ ٍؼْ٘يخ ثيِ اىَ٘صالد اىنٖشثبئيخ ٗمو ٍِ اىَ٘اد اىصيجخ اىَزاثخ اىنييخّ,غت اىَي٘زخ,اىَ٘اد اىصيجخ اىنييخ,اىَ٘اد اىصيجخ اىَؼيقخ اىنييخٗ,اىني٘سيذاد .مَب إسرجطذ اىَ٘اد اىصيجخ اىَزاثخ اىنييخ إسرجبغب ٗثيقب ثنو ٍِ ّغت اىَي٘زخ, اىَ٘اد اىصيجخ اىنييخ ,اىني٘سيذاد ,اىَ٘اد اىصيجخ اىَؼيقخ اىنييخٍٗ,نّ٘بد ُػغش اىَيبٓ. 168
إسرجطذ اىَ٘اد اىصيجخ اىنييخ إسرجبغب ٍؼْ٘يب ثنو ٍِ اىَ٘اد اىصيجخ اىَؼيقخ اىنييخ, اىَ٘صالد اىنٖشثبئيخ ,اىَ٘اد اىصيجخ اىَزاثخ اىنييخّ ,غت اىَي٘زخ ٗ,اىني٘سيذاد .إسرجطذ اىَ٘اد اىصيجخ اىَؼيقخ اىنييخ إسرجبغب ٍؼْ٘يب ثنو ٍِ اىَ٘اد اىصيجخ اىنييخ ّ ,غت اىَي٘زخ ,اىَ٘صالد اىنٖشثبئيخ ٗ,اىَ٘اد اىصيجخ اىَزاثخ اىنييخ .إسرجطذ اىني٘سيذاد ٍؼْ٘يب ثبىَ٘صالد اىنٖشثبئيخ , اىَ٘اد اىصيجخ اىَزاثخ اىنييخٍ ,نّ٘بد ُػغش اىَيبّٓ ,غت اىَي٘زخ ,اىَ٘اد اىصيجخ اىنييخ .إسرجطذ ٍنّ٘بد ُػغش اىَيبٓ ٍؼْ٘يب ثبىني٘سيذاد ,اىَ٘صالد اىنٖشثبئيخ ,اىَ٘اد اىصيجخ اىَزاثخ اىنييخ ّ ,غت اىَي٘زخ .إسرجطذ ٍؼذالد اىف٘عفبد إسرجبغب ٍؼْ٘يب ثبىَ٘صالد اىنٖشثبئيخ ,اىَ٘اد اىصيجخ اىَزاثخ اىنييخّ ,غت اىَي٘زخ ,اىَ٘اد اىصيجخ اىنييخ ,اىَ٘اد اىصيجخ اىَؼيقخ اىنييخ .إسرجػ رشميض األط اىٖيذسٗخيْ ٚإسرجبغب أقو ٍؼْ٘يخ ثبىقبػذيخ ,اىف٘عفبد ,اىَ٘اد اىصيجخ اىَزاثخ اىنييخ,اىَ٘صالد اىنٖشثبئيخ ,اىَزطيت اىنيَيبئ ٚىألمغديِ ,اىَ٘اد اىصيجخ اىنييخ ,اىَ٘اد اىصيجخ اىَؼيقخ اىنييخ. إسرجطذ دسخخ اىسشاسح ػنغيب ٍٗؼْ٘يب ٍغ اىقبػذيخ. ثبلثب :الحول الوينشوثً لويبٍ الجشك التشاثيخ :أمذد اىْزبئح اىَ٘عَيخ ىيسَو اىَينشٗثٚ ٗخ٘د اخزالفبد ف ٚاىقيٌ اىَغديخ ,زيث رَيض اىشثيغ ثؤػي ٚقيٌ ىيؼذ اىني ٚىين٘ىيف٘سً اىز ٙػض ٙإىٚ صيبدح اىَسز٘ ٙاىؼع٘ ٙاىَ٘ظر ٍِ خاله صيبدح قيٌ األٍّ٘يب ,اىْيزشيزبد ,اىف٘عفبد ٍغ صيبدح األمغديِ اىَزاة ٗاىَزطيت اىنيَيبئ ٍْٔ ٚىيغزٖيل ٍِ قجو اىَسز٘ ٙاىَينشٗثٗ ٚمزىل ىألّشطخ اىنيَيبئيخ اىسي٘يخ ىألعَبك. فيَب يخص اىَسز٘ ٙاىَينشٗث ٚثبىجشك اىزشاثيخ.أٗظسذ اىجشمخ (سقٌ )2أػي ٚقيٌ ىيؼذ )10فئزز٘د ػي ٚأػي ٚقيٌ ىيؼذ اىفطش ٙاىنيٗ ٚأقو قيٌ ىيؼذ اىجنزيش ٙاىني .ٚأٍب اىجشمخ (سقٌ اىفطش ٙاىني ٚثبىشثيغ .اىجشمخ (سقٌ )4رَيضد ثؤػي ٚقيٌ ىيؼذ اىجنزيش ٙاىنيٗ ٚاىؼذ اىني ٚىين٘ىيف٘سً ٗىنِ أقو قيٌ ىيؼذ اىفطش ٙاىني.ٚ ٗػيٍ ٚذاساىثالثخ فص٘ه ثبىجشك خَيؼٖب ,رَيض اىصيف ثضيبدح اىؼذ اىجنزيش ٙاىني ٚفٍِ 4 ٚ اىجشك ٍغ أقص ٚقيَخ ٕٗ٘ ٗ 210 x11450زذح رن٘يِ ٍغزؼَشح ٍ/و ٍِ اىَيبٓ ثبىجشمخ (سقٌ ,)4 ٗأيعب أػي ٚػذ فطش ٙميٗ 210 x89,6 ٚزذح رن٘يِ ٍغزؼَشح ٍ/و ٍبء ثبىجشمخ (سقٌ ٗ )10أػيٚ ػذ ثنزيش ٙميٗ 210 x1755,69 ٚزذح رن٘يِ ٍغزؼَشح ٍ/و ٍبء ث٘خٔ ػبً. ٗ 210 x19,53زذح رن٘يِ ٍغزؼَشحٍ/و ٍبء رَيض اىخشيف ثؤقو قيٌ ىيؼذ اىفطش ٙاىنيٚ ٗأػي ٚػذ مي ٚىين٘ىيف٘سً ف ٍِ 10 /7 ٚاىجشك زيث مبُ أاػالٕب ثبىجشمخ (سقٌ )9مَب رَيض اىَ٘عٌ ثؤػي ٚػذ ثنزيش ٙمي ٚف ٍِ 10 /5 ٚاىجشك ٗاػالٕب ف ٚاىجشمخ (سقٌ.)7 ساثعب :هعبييش النفبءٍ اإلًتبخيخ للسول :رٌ رقذيشٕب ف ٚػذد ( )100عَنخ أخزيشد ػش٘ائيب فّٖ ٚبيخ فزشح اىذساعخ .رَيضد اىجشمخ (سقٌ )5ثؤصغش أزدبً ىيغَل ,اى٘صُ اىس ٚاىْٖبئٗ ,ٚصُ اىنجذٗ ,صُ اىطُسبه .ثيَْب رَيضد اىجشمخ (سقٌ )7ثؤػي ٚقيٌ ىسدٌ اىغَلٗ ,صُ اىنجذ مَب عديذ اىؼالقخ اىَؼْ٘يخ اىَجبششح ثيِ زدٌ اىغَل ٗٗصّٔ اىْٖبئٗ ٚمزىل ثيِ اىَؤشش اىدغذ ٙىينجذ ,اىَؤشش اىدغذ ٙىيطسبه .اسرجػ اىَؤشش اىدغذ ٙىينجذ ٍؼْ٘يب ثبىَؤشش اىدغذ ٙىيطسبه ٗاى٘صُ اىسٚ اىْٖبئ.ٚ خبهسب :الٌتبئح الٌسيديخ الوشضيخألعضبء اسوبك الجلطً الٌيلً الوختبسح هي الجشك التشاثيخ ثٌهبيخ دوسح التشثيخ :رؼذ اىزغيشاد اىْغيديخ اىَشظيخ مَؤششاد زي٘يخ ىزؤثيش اىزؼشض ىإلخٖبداد اىجيئيخ.زيث ر٘ظر اىزغيش قجو ٍالزظزٔ ثبى٘ظبئف اىؼع٘يخ أٗ اىنيَيبئيخ اىسي٘يخ أٗ ثشافقزٖب ع٘يب.
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-1اىخيبشيٌ :اىق٘ط اىخيشٍ٘ ٚيزَيض ثزدَؼبد ٍنثفخ ٍِ اهخاليب راد اىسجيجبد األي٘صيْيخ ٍغ إززقبُ األٗػيخ اىذٍ٘يخ ٗردَغ ريل اىخاليب ز٘ه ٕزٓ األٗػيخ ٗرىل ثؤعَبك اىجشمزيِ (سقٌ .)1,2مَب رَيضد اىشؼيشاد اىخيشٍ٘يخ ثزنبثش اىظٖبسح اىشقبئقيخ ٍغ فصو إسرشبز ٚىيخاليب اىطالئيخ اىشقبئقيخ, ٗر٘عغ اىشؼيشاد اىذٍ٘يخ اىشقبئقيخ ثبىجشك (سقٌ .)3,4مَب رٌ اىزؼشف ػي ٚآفبد ٍشظيخ أقو ظشاٗح ثؤعَبك اىجشك (سقٌ .)1,2 -2اىنجذ :رؤثش ثآفبد ٍشظيخ غفيفخ ثؤعَبك اىجشك (سقٌ )7,8,9,10ػيٕ ٚيئخ ردَغ ثؤسٙ صغيش ٍِ اىزذٍيش اىفد٘ ٙىيخاليب اىنجذيخ ٍغ ردَغ ثؤس ٙىيخاليب ٗزيذح اىْ٘اح ٗآفبد ٍشظيخ شذيذح ثؤعَبك اىجشك (سقٌ )5,6,9رذٍيش ٍْزشش ثبىخاليب اىنجذيخ ,إززقبُ ثبى٘ػبء اىنجذ ٙاىجبثٗ ٚرْنشص ثبىخاليب اىنجذيخ ٍصس٘ثب ثزدَغ ثؤس ٙىيخاليب زبٍيخ ف ٚزبالد فشديخ .رَيض اىنجذ ثؤعَبك اىجشمخ (سقٌٗ )9مزىل ثَْطقخ ر٘اصو اىنجذ ٗاىجْنشيبط رغيشاد ّغيديخ ٍشظيخ غفيفخ ٗػْيفخ. -3اىطسبه:أٗظسذ اىص٘س اىَدٖشيخ اىذقيقخ ىيطسبه إخزفبء اىخاليب اىيَفيخ ٍصس٘ثب ثئززقبُ اىدييجبد اىطسبىيخ ٗرْشيػ ٍشمض رن٘يِ اىخاليب اإلىزٖبٍيخ اىسبٍيخ ىيصجغ( اىَياليْيِ) ٍغ اىزْنشص اىَشَ٘ه ثبىَغشاليبد اىطسبىيخ .ف ٚزبالد فشديخ ى٘زع ٗخ٘د قطبع غفيو ٍزس٘صو ثْغيح اىطسبه ٗ.مبّذ ٕزٓ اآلفبد اىَشظيخ اىؼْيفخ ثؤعَبك اىجشك (سقٌ .)3,4مَب أٗظر اىطسبه ف ٚثؼط اىسبالد آفبد أقو ظشاٗح ٍثو :إخزفبء ىيَفٗ ٚرْنشص رٌ اىزؼشف ػييٖب ثؤعَبك اىجشك (سقٌ .)5,6,9 ٍَٗب عجق رمشٓ ٍِ آفبد ٍشظيخ ػْيفخ ثبىنجذ ٗاىطسبه ,يَنِ إفزشاض أُ ٕزٓ اىجشك رؼشظذ ىَي٘ثبد ميَيبئيخ ,ثنزشيب ,فطشيبد ٗ,غفيييبد. -4اىَخ :أٗظسذ اىص٘س اىَدٖشيخ ىْغيح اىَخ إسرشبذ اىغبئو ,إخزفبء اىَسز٘ ٙاىخيٍِ٘ ٙ األّ٘يخ ,إىزٖبة اىَخ ٗاىَ٘ظر ػجش إززقبُ اىشؼيشاد اىذٍ٘يخ اىذٍبغيخ ٍغ رْنشص شذيذ ٗإخزفبء اىغشبء اىَيالّ ٚىْغيح اىَخ ٍغ ّعر خاليب اىذً اىسَشاء اىسشٓ ٗردَغ خاليب اىذً اىسَشاء اىسبٍعيخ اىَسججخ ثْغيح اىَخ ٗاىز ٙرٌ اىزؼشف ػييٌٖ ٍِ اعَبك اىجشك (سقٌ .)5,6,9,10
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