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International Journal of Fisheries Science and Research

Mixture Toxicity of the Heavy Metals, Mercury and Cadmium to the Indian Major Carp, Labeo rohita

Abstract Citation Introduction Materials and Methods Results Discussion Conclusion Acknowledgement References
Details

Received: 08-Feb-2019

Accepted: 13-Mar-2019

Published: 18-Mar-2019

Ramesh1, Appasamy Surendran2 and Antony Joseph Thatheyus1*

1PG and Research Department of Zoology, The American College, India 2PG Department of Food Science & Nutrition, The American College, India

Corresponding Author:

Antony Joseph Thatheyus, PG and Research Department of Zoology, The American College, Madurai, India, Tel:+91 94874 24820

Keywords

Heavy metals; Mercury; Cadmium; Mixture toxicity; Labeo rohita

Abstract

Many industries discharge their effluents in to aquatic ecosystems without proper treatment. As they contain several heavy metals, they affect aquatic organisms. Acute toxicity tests provide rapid estimates of lethal concentrations of toxicants. Hence, the present work has been designed to test the acute toxicity of mercury, cadmium and their combinations to the fingerlings of the Indian major carp, Labeo rohita. Among these four types of toxicants, Hg was the most toxic followed by (Cd)+Hg, (Hg)+Cd and Cd.

Citation

Ramesh, Surendran A and Thatheyus AJ. Mixture Toxicity of the Heavy Metals, Mercury and Cadmium to the Indian Major Carp, Labeo rohita. Int J Fisheries Sci Res. 2019; 3(1): 1012.

Introduction

Water is an integral constituent of all living things and it is the universal biological solvent. Modern industrial and agricultural techniques require the use of many million tones of fertilizers, heavy metals and pesticides. These effluents find their way in to aquatic systems through surface run off from industries or as a result of discharge of these wastes into streams and rivers. They pose constant threat to non-target organisms such as fish and insects and tend to bioconcentrate the inorganic and industrial wastes [1,2]. The industrial complexes have become the focus of environmental pollution [3]. The main pollutant from these industrial complexes is effluent, which contains heavy metals such as Cu, Ni, Zn, Pb, Cr, Hg, Cd and various organic compounds such as phenols and formaldehyde [4]. The recovery of these heavy metals using conventional techniques is neither economical nor eco-friendly [5,6]. Once heavy metals are accumulated by aquatic organisms they can be transferred to higher trophic levels of food chain. Carnivores at the top of the food chain including humans, receive most of their heavy metal burden from aquatic ecosystems by way of their food, especially where fish are present [7].

Studies have shown that even after cessation of the contamination source, heavy metals from sediments can be cycled into natural aquatic systems [8]. The heavy metal concentration in the tissues of aquatic animals is occasionally monitored. The toxicity may be either acute or chronic to fishes in sublethal concentration. Among these two, later concentrations are slow poisons disturbing the biochemistry of the organisms and in fact more dangerous [9].

Chemical and metallurgical industries are the most important sources of heavy metals in the environment [10]. The contamination of aquatic system with heavy metals may have devastating effects on the ecological balance of the aquatic environment and diversity of aquatic organisms becomes limited with extent of contamination [11]. Most of the heavy metals released into the environment find their way into the aquatic phase as a result of direct input, atmospheric deposition and erosion due to rain water. Hence, aquatic organisms are exposed to elevated levels of heavy metals. Cadmium and lead have no known role in biological systems whereas copper and zinc are essential components of enzymes or metalloproteins in fish metabolism. These heavy metals accumulate in the tissues of aquatic animals and may become toxic when accumulation reaches a substantially high level. Accumulation levels vary considerably among metals and species [12].

Fish have numerous advantages as indicator organisms for biological monitoring programs. Fish communities represent a variety of trophic levels (carnivores, herbivores, insectivores, planktivores and piscivores) and include foods of both aquatic and terrestrial origin. Fishes are typically present even in the smallest streams and in all but the most polluted waters. Both acute toxicity and stress effects can be evaluated employing fish [13]. The target organs, such as liver, gonads, kidney and gills have a tendency to accumulate heavy metals in high levels as shown in many species of fish in different areas [14]. Studies have shown that fish are able to accumulate and retain heavy metals from their environment and it has been shown that accumulation of metals in tissue of fish is dependent upon exposure concentration and duration, as well as other factors such as salinity, temperature, hardness and metabolism of the animals [15,16]. The toxic effects occur when excretory, metabolic, storage and detoxification mechanisms are able to counter uptake. In recent years, several authors have investigated the heavy metal accumulation in fish and other organisms [17,18]. The excess copper impairs the survival, growth and reproduction of fish [19]. In this context, the present study has been carried out to estimate the acute toxicity of mercury, cadmium and their mixtures to Labeo rohita.

Materials and Methods

For the present study, the fingerlings of L.rohita were purchased from local aqua farm in Madurai, Tamil Nadu, India. The fish were acclimatized for more than ten days in large aquaculture tanks (75L). The fish were fed with commercially available feed daily. The excreta and excess food were siphoned out to avoid contamination and ammonia stress. Once in a day water was changed. From the laboratory acclimatized fishes, fishes with 5 ± 0.5 cm length and 5 ± 1g were selected and they were again acclimatized for one or two days in experimental tanks prior to commencement of the experiment. The capacity of experimental tank was twenty liters. The tank was closed by net to prevent the jumping of fish.

1.353g of HgCl2 was dissolved in one liter double distilled water to get 1000 ppm of mercury stock solution where as 2.031g of CdCl2 2 ½ H2 O was dissolved in one litre of double distilled water to get 1000 ppm of cadmium stock solution. The ground water was used in the present study. Each tank was filled with five litres of ground water with five fishes.

Determination of LC50

After preparing the stock solutions for mercury and cadmium, the wide range of these two metals were identified by using three fish in each concentration. The fish should not be fed for one day before starting the experiment to avoid the change in toxicity of metals due to excretory products [20]. Then narrow range was identified from wide range. Different concentrations of the metals were prepared and in each of them ten fish were exposed separately. The percent mortality of fish in different concentrations was noted after 24, 48, 72 and 96 hours of exposure. The LC50 value for different exposure periods were obtained after computing probit analysis. In this, the concentrations were converted into log concentrations and percent mortality values were converted into probit scale. Using regression analysis, straight lines were drawn in the graph to derive the LC50 values. Chi- square tests were carried out to test the goodness of fit for comparing the observed Y-values and expected Y- values [21].

Determination of LC50 value for metal mixtures

The combinations of metals were prepared, in which one metal concentration was kept constant (i.e. 1/10th of 96 hr LC50 value) and the other was varied. Different concentrations of metal mixtures were prepared and in each of them ten fishes were exposed separately. The percent mortality of fish in different metal mixture concentration was noted after 24, 48, 72 and 96 hours of exposure. The LC50 values for metal mixtures were obtained employing probit analysis.

Results

The percent mortality values of L.rohita exposed to different concentrations of metals and metal mixtures are given in Table 1 to 4. No mortality was noticed in 0.20 ppm of HgCl2 from 24 hours to 96 hours, while 100% mortality was observed in 0.50ppm of HgCl2 within 24 hours. The LC50 values for 24, 48, 72 and 96 hours were 0.71, 0.65, 0.64 and 0.64 ppm respectively (Table 1). The LC50 values observed decreased with the increase in the duration of exposure to HgCl2 . In Cadmium, no mortality was observed in 40 ppm of CdCl2 in 24 hours of exposure. 100% mortality was noticed in 120ppm of CdCl2 in 24 hours of exposure. The LC50 values for 24, 48, 72 and 96 hours were 141, 88, 81 and 81 ppm respectively (Table 2).

Table 1: Acute toxicity test results of Mercury to L.rohita.

    95% Fiducial limits of LC50 (ppm) Probit regression equation Slope  
  Lethal concentration (ppm) Chi-square values
    Function  
Hours LC5                         Level of significance at
            Lower Upper Y = a+b x “S” Observed Table 0.05 level
LC10 LC16 LC50 LC84 LC90 LC99              
                    Y=6.388031 +        
24 0.48 0.52 0.56 0.71 0.91 0.98 1.26 0.63 0.82 9.411891 X 1.2732 20 7.81 S
                    Y=6.65433 +        
48 0.4 0.45 0.5 0.65 0.85 0.93 1.25 0.58 0.72 8.577419 X 1.3231 24.2 9.49 S
                    Y=6.734322 +        
72 0.41 0.45 0.49 0.64 0.83 0.91 1.21 0.52 0.73 8.761884 X 1.3103 17.6 9.49 S
                    Y=6.734322 +        
96 0.41 0.45 0.49 0.64 0.83 0.91 1.21 0.59 0.7 8.761884 X 1.3103 17.6 9.49 S

S = Significant; NS = Not Significant.

Table 2: Acute toxicity test results of Cadmium to L.rohita.

    95% Fiducial limits of LC50 (ppm) Probit regression equation Slope  
  Lethal concentration (ppm) Chi-square values
    Function  
Hours                           Level of
  LC5             Lower Upper Y = a+b x “S” Observed Table significance at
    LC10 LC16 LC50 LC84 LC90 LC99             0.05 level
                    Y=-2.085658+        
24 45 57.9 70.7 141 282 344 712 114 174 3.291838x 1.9972 4.0809 9.49 NS
                    Y=-1.27823 +        
48 28.4 36.6 44.5 88 174 212 435 67 115 3.224158x 1.9796 19.066 9.49 S
                    Y=-8.973124 +        
72 48.6 54.4 59.4 81 110 121 167 77 85 7.325261x 1.3616 5.7321 5.99 NS
                    Y=-8.973124 +        
96 48.5 54.4 59.4 81 110 121 167 77 85 7.325261x 1.3616 5.7321 5.99 NS

S = Significant; NS = Not Significant.

Table 3: Acute toxicity test results of (Mercury) + Cadmium to L.rohita.

    95% Fiducial limits of LC50 (ppm) Probit regression equation    
  Lethal concentration (ppm) Slope Chi-square values
       
Hours                           Level of
  LC5             Lower Upper Y = a+b x “S” Observed Table significance at
    LC10 LC16 LC50 LC84 LC90 LC99             0.05 level
                    Y=-26.35913 +        
24 49.2 51.5 53.4 60.4 68.3 70.8 80.6 57.5 63.5 17.57739X 1.13128 12.5379 11.07 S
                    Y=-20.51776 +        
48 43.3 48.9 48 56.1 65.6 68.6 80.8 55.2 57 14.59043X 1.1688 7.18575 12.59 NS
                    Y=-13.66395 +        
72 37 40.1 42.8 53.2 66.2 70.6 88.8 50.6 56 10.81501X 1.2447 24.4533 12.39 S
                    Y=-20.16803 +        
96 38.5 40.9 42.8 50.2 58.9 61.6 72.9 49.1 51.2 14.79845X 1.17294 9.50832 12.59 NS

S = Significant; NS = Not Significant.

Table 4: Acute toxicity test results of (Cadmium) + Mercury to L.rohita.

    95% Fiducial limit of Probit regression equation Slope  
  Lethal concentration (ppm) LC50 (ppm) Chi-square values
      Function  
Hours                           Level of
  LC5             Lower Upper Y = a+b x “S” Observed Table significance at
    LC10 LC16 LC50 LC84 LC90 LC99             0.05 level
                    Y=11.4719 +        
24 0.21 0.22 0.24 0.28 0.34 0.36 0.43 0.27 0.3 11.81938X 1.19956 21.9616 11.07 S
                    Y=10.0244 +        
48 0.18 0.2 0.21 0.27 0.34 0.37 0.47 0.25 0.29 8.907909X 1.26542 18.2988 11.07 S
                    Y=8.112757 +        
72 0.13 0.16 0.18 0.27 0.4 0.45 0.7 0.25 0.28 5.406702X 1.51346 11.9673 12.59 NS
                    Y=7.387148 +        
96 0.11 0.12 0.14 0.25 0.45 0.53 0.96 0.24 0.26 3.962734X 1.78123 6.52691 12.59 NS

S = Significant; NS = Not Significant.

In the metal mixture (HgCl2) + CdCl2 , no mortality was observed in (0.064 ppm of HgCl2) + 48 ppm CdCl2 within 24 hours (Table 3) while 100% mortality was noticed in (0.064 ppm of HgCl2) + 64 ppm of CdCl2 after 24 hours. The LC50 values for 24, 48, 72 and 96 hours were 60.4, 56.1, 53.2 and 50.2 ppm respectively (Table 3). In the second metal mixture (CdCl2) + HgCl2 , no mortality was observed in (8.096 ppm of CdCl2) + 0.18 ppm of HgCl2 after 24 hours (Table 4). But 100% mortality was noticed in (8.096 ppm of CdCl2) + 0.32 ppm of HgCl2 after 24 hours. The LC50 values for 24, 48, 72 and 96 hours were 0.28, 0.27, 0.27 and 0.25 ppm (Table 4). In the above four experiments, the LC50 values observed decreased with the increase in the duration of exposure (Figure 1).

Figure 1: LC50 values of Labeo rohita exposed to mercury, cadmium and their combinations.

Discussion

The present study reveals that mercury, cadmium and their mixtures are toxic to the fish, L. rohita and mortality rate increased with increasing concentrations of metals. The mortality rate depends upon the duration of exposure. The LC50 values for mercury, cadmium and two types of mixtures (in one type mercury was kept constant and cadmium concentrations varied and in the second type, cadmium was kept constant and mercury concentrations varied) for 96 hours were 0.64, 81, 50.2 and 0.25 ppm respectively.

The LC50 value of mercury for 96 hours is about three times lesser than that of Ophiocephalus (Channa) punctatus [22]. The LC50 value of cadmium for 96 hours is about six times higher than that of Oreochromis niloticus [23], about three times higher than that of Poecilia reticulata and for Catla catla it was very low [24].

LC50 value of zinc for 96 hours to L. rohita was found to be 156ppm [25]. The toxicity of hexavalent chromium has been studied in L. rohita [26] and its 96 hours LC50 value was 111.45 mg/l. The 96 hours LC50 values of copper to Tilapia guineensis and Tympanotonus fuscatus were 0.16 and 8.84 mg/l respectively [27]. The above findings indicate that the range of toxicity varied for different species and for different toxicants. Furthermore, several factors like pH, hardness, alkalinity, equilibration and kinetics involved in the chemical reactions are detrimental in the toxic efficacy.

One of the recent areas of research in toxicology is concerned with the fate of toxicants inside the organisms. The toxicant uptake by aquatic organisms is a two phased process, which involves initial rapid adsorption or binding to surface, followed by a slower transport into the cell interior. The transport of metal into the intracellular compartment may be facilitated by either diffusion of the metal across the cell membrane or by active transport by carrier protein [28]. The metal enters the blood circulation of fish and finds its way into different tissues of the body where it affects normal metabolism. Generally, liver is the centre of metabolism and detoxification in piscine body [29]. The kidney plays a major role in the accumulation, detoxification and excretion of metals and is considered to be a target organ for metal toxicity [30,31].

Exposure to toxic heavy metals is associated with many chronic diseases. Recent research found that low levels of lead, mercury, cadmium, aluminium and arsenic can cause a variety of health problems like decreased intelligence in children, nervous symptoms, immune dysfunctions, depression, fatigue, anemia, skin rashes, high BP, memory loss, diarrhea, nausea, irritability, tremors, cancer, hyperactivity, autism, behavioural disorders and head-ache [32,33].

The toxicity of mercuric chloride, cadmium chloride and their mixture to N.notopterus was determined by 96 hours LC50 concentration which indicated that CdCl2 was less toxic, while HgCl2 was most highly toxic and their mixture were in between them [34]. Consequently, in terms of ecological significance, fish are irreplaceable bio-indicators of the degree of damage to the water environment. Moreover, it is also important to monitor the contamination of fish with heavy metals, because frequent consumption of the contaminated fish presents a very serious health risk [35].

Conclusion

Among the two metals tested mercury exhibited higher toxicity than that of cadmium. Both the mixtures exhibited their LC50 values in between the LC50 values of cadmium and mercury to the Indian major carp, L.rohita.

Acknowledgement

The authors thank the authorities of the American College, Madurai, Tamil Nadu, India for the facilities and encouragement.

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Empirical Assessment of Fish Diversity of Uttar Pradesh, India: Current Status, Implications and Strategies for Management

About 60-70% of world’s biological resourcesis contributed by India, of which fish represents 80% of the global fishes. Uttar Pradesh blessed with vivid aquatic bioresources in innumerable forms contributes about 14.68% of Indian fish biodiversity with substantial scope of inland fisheries development and aquaculture. Ganga, the mighty river of this state reportsabout 265 freshwater species from its river system [1]. Besides, other rivers viz. Ramganga, Gomti, Ghaghara, Yamuna, Gandak, Kosi and Damodaract as reservoir of different f ish stocks. In past, no study highlights the assessment of the fish biodiversity of this state in holistic way except by Khan (2000) who justreported a compilation of 129 fishes under 27 families [2]. To substantiate and revise the assessment, the fish diversity of this state was assessed by investigating these rivers, analyzing and documenting the information on different fisheries measurements including biology, distribution and conservation status. About 10,000 individuals were collected and the analysis of individuals revealed 126 fish species under 28 families and 74 genera nearly mitigating the earlier reports. The highest species diversity was recorded in the river Ganga (90) followed by Gerua (87) and then Gomati (68). 37 species were found common in Gomati, Ghaghara, Ganges, Son, Tons and Yamuna. Out of 90 species, 6 species were recorded from the river Ganga. In addition, the new distribution of a threatened torrent catfish Amblyceps mango is was recorded from the rivers Gomati, Ganga and Ramganga. The economical assessment unravels nearly 33% as ornamental, 87% as food and 10% as sport fishes.

Pathak AK*


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Stranding of Small Cetaceans with Missing Fins Raises Concerns on Cetacean Conservation in Ecuador: Bycatch or Targeted Fisheries?

Among anthropogenic threats to marine mammals, bycatch is one of the major and increasing concerns. This report describes three species of small cetaceans, including a short-beaked common dolphin (Delphinus delphis), a bottlenose dolphin (Tursiops truncatus), and two dwarf sperm whales (Kogia sima), which were found stranded with pectoral fins, dorsal fins and caudal fin removed. The dolphins were found at the beaches of San José de Las Nuñez and San Pablo, respectively (Santa Elena Peninsula Province on 14 August 2017), while the dwarf sperm whales were found in Puerto Lopéz and Crucita (Manabí Province) in July 2014 and August 2015, respectively. Possible explanation for the dolphins and dwarf sperm whales missing fins support the event as a possible case of fishery interaction or bycatch with systematic removal of their fins. Although remnants of artisanal gillnets were not found near the two dolphin species, one of the dwarf sperm whales showed marks of artisanal gillnets on the body as evidence of bycatch. Trade of dolphin carcasses and their parts for bait by fishers cannot be ruled out as there is some evidence of this practice in the past. Both dolphins species are vulnerable species at the national level and commonly involved in incidental captures with gillnets of artisanal fisheries in Coastal Ecuador. Cetacean bycatch is a grave conservation problem affecting several cetacean species in Ecuador’s waters. Fisheries and environmental authorities must be vigilant and enforce actions to proactively mitigate possible anthropogenic impacts and promote environmental education activities in fishing communities to conserve vulnerable dolphin species in Ecuador’s waters. Further, to comply with new rules and regulations of the US Marine Mammal Protection Act (MMPA) intended to reduce the bycatch of marine mammals in foreign commercial fishing operations that export fish and fish products to the United States, a regulatory program is urgently needed to mitigate and reduce fisheries interactions with marine mammals in Ecuador.

Pedro J Jiménez1, Juan José Alava1,2*, Cristina Castro3, Jorge Samaniego4 and Patricia Fair5


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Sodium Arsenite-induced Morphological, Behavioral, Hematological and Histopathological abnormalities in Labeo Rohita

Toxic metals have contaminated the aquatic ecosystems to a large scale, and they eventually enter human systems by contaminated air, food, water and soil. Recently, arsenic toxicity has become an alarming concern around the globe. Major areas of North-Eastern states of India have been demarcated with an arsenic content of 50-1000 µg/l in drinking water sources and aquatic ecosystems. Arsenic range in Barak Valley is many folds higher than the permissible limit of WHO and BIS as 10µg/l and 50µg/l respectively, which is present in the form of Sodium Arsenite in water. Fishes are the major dwellers of aquatic ecosystem and serves as good bio-indicators for determination of health status of an aquatic ecosystem. They also form the staple diet of North Eastern people. Labeo rohita is one of the most commonly available and consumed in large scale. The present study was carried out in Labeo rohita in vivo. Labeo rohita (n=10) of similar size and weight were exposed to sodium aresnite at concentrations 100 µg/l and 250 µg/l along with controlled set up for 10 days. The morphological, behavioral, hematological and histopathological changes were evaluated. Fishes exposed to Sodium arsenite showed irregular ocular movement, fin movement, swimming pattern and loss in scales with higher prominence in 250 µg/l of arsenic group than those at 100 µg/l. The hematological indices revealed decrease in RBC count and increase in WBC count in both sodium arsenite exposed groups. The histopathological study of liver revealed parenchymal disorganization and atypical residual body in both sodium arsenite treated groups. Results obtained showed major damages to fishes due to contamination with sodium arsenite. These fishes, when consumed by humans, leads to increase in several thousand folds of sodium arsenite by means of biomagnification. High exposure of arsenic in human through fishes leads to several disorders. The possible way of eradicating sodium arsenite entry into humans is banning fishing activities in highly contaminated aquatic ecosystems. Community education and local participation are also essential to get a fruitful outcome.

Rajib Biswas1* and Soumitra Nath2


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Reconstruction of Historical Fisheries Profile of Cameroon

This work attempts to reconstruct historical fisheries profile by filling in the missed underestimated catch information for some reasons of industrial fishing, artisanal fishing, inland fishing, illegal fishing, discards and aquaculture production of Cameroon from 1950 to 2016.This reconstruction was carried out based on data published by various authors, the Ministry of Fisheries and Livestock (MINEPIA), the Limbe Research Center on Fisheries and Oceans and FAO reports. The dataset allowed us to reconstruct the fishing profile of Cameroon by completing the missing data by interpolation. Then we compare the data obtained with those of FAO. Reconstructed catches were estimated at 13,834 tons and aquaculture production was estimated at 19 tons in 1950 compared to 12,000 tons and 14 tons published by FAO, With the agricultural reforms and development of projects focused on the primary industry, catches increased around 94,122 tons in 1977(compared to 70,167 tons reported by the FAO) to 102,975 tons in 1981(compared to 79,761 tons reported by the FAO), declined to 78,790 tons in 1986 because of the reduction of the Exclusive Economic Zone of Cameroon (EEZ) by the geographical presence of the insular part of Equatorial Guinea (Malabo Island), then increased to 186,204 tons in 2005(compared to 142,345 tons reported by the FAO), declined to 154,800 tons in 2008(compared to 129,000 tons reported by the FAO). Since 2011 it became stable and reached around 240,000 tons against 220,000 tons published by FAO. Overall, there are discrepancies between the reconstructed data and the data provided to FAO: the reconstructed data is 30% higher than the FAO data. This information about fisheries production in Cameroonian waters shows that many locals, fisheries managers and stakeholders depends on fish products for either incomes or food safety; therefore, the recent decline of fish production in Cameroon is of no good sign to the abovementioned persons. These observed fish production decline indirectly threatens the food security of the people of Cameroon and low financial income to the state coffers.

Nyatchouba Nsangue Bruno Thierry, Richard Kindong and Liuxiong Xu*


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Effect of Fishmeal Substitution by Lima Bean Meal on the Zoo Technical Performances of African Catfish (Clarias gariepinus) in the Bati

A study on the effect of the substitution of fishmeal by Lima bean flour was conducted between March and May 2018 within the AIO ICG of the Batié District, with the global objective of contributing to the development of alternative sources of animal protein. Specifically, the aim of the study was to evaluate the effect of the substitution of fishmeal by Lima bean flour on the growth performance, survival and feed cost of Clarias gariepinus. For this purpose, 300 fry of Clarias gariepinus with an average weight of 3 ± 1.41g were divided into five batches and fed three times a day with rations corresponding to 5% of their ichthyo biomass. The rations R0, R25 R50, R75 and R100 respectively corresponded to the substitution rates of 0, 25, 50, 75 and 100% of fish meal by that of Lima bean. The physic-chemical characteristics of the water (pH, temperature, dissolved oxygen, nitrites and nitrates) were measured daily. The following results were obtained: The highest weight gains were obtained with the rations R25 (20.56 ± 0.40 g), R50 (20.64 ± 0.32 g), R75 (20.98 ± 0.46 g) and the lowest with the ration R100 (16.21 ± 0.28 g). For this average daily gain, the highest values were 0.36 ± 0.02 g; 0.37 ± 0.01 g, 0.38 ± 0.01 g respectively for the R0, R50 and R75 rations and the lowest with R100 (0.29 ± 0.01 g). The highest value of the specific growth rate (2.47 ± 0.07%) was obtained with the ration R0 and the lowest (1.61%) with the ration R100. The consumption index reached its highest and lowest values with the rations R100 (4.74 ± 0.42) and R50 (3.57 ± 0.43) respectively, compared to the value of the ration R0 (3.31 ± 0.37) for this parameter. Concerning the condition factor K, the highest value was recorded with the R50 diet (1.11 ± 0.49) while the lowest value was obtained with the R75 diet (0.95 ± 0.45). The cost of producing one kilogram of food was higher with the R25 ration (504.59 FCFA) and lower with the R100 ration (443.20 FCFA). This study found that incorporating 75% Lima bean flour into the feed increases the growth performance of Clarias gariepinus fry and reduces the cost of food production.

Emile Miégoué1*, Pégis Davy Tagning Zebaze2, Fernand Tendonkeng1, Lemoufouet Jules1, Nadège Elvire Njoh2, Ronald Komguep Nganyo2 and Etienne Tedonkeng Pamo1


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Comparative Effect of Monoculture and Polyculture in Two Species of Clariidae: Heterobranchus longifilis and Clarias gariepinus in Post Fingerlings Growth

In order to improve the production of Clariidae, a study on the type of cultivation of Heterobranchus longifilis and Clarias gariepinus in post fingerlings growth phase was carried out in tanks. It took place from March to May 2018 at the IRAD fish station in Koupa-Matapi (LN: 5º 21 ‘to 5º 58’ and LE: 10º 17 ‘to 11º 02’) west region Cameroon. For this fact 180 fry therefore 90 Heterobranchus longifilis and 90 Clarias gariepinus with an average weight 3.55 ± 0.68 g; 8.46 ± 0.41cm of total length and 7.37 ± 0.30 cm of standard length were used. The 180 fry were divided into three treatments of 60 individuals (T1 treatment: Clarias gariepinus, T2 treatment Heterobranchus longifilis and T3 treatment: Clarias gariepinus + Heterobranchus longifilis). Each treatment was repeated twice. The fish were fed twice per day at a rate of 10% of the ichthyobiomass readjusted each month after control fishing with a feed at 42% crude protein. From the results of this trial, it appears that unlike the higher mortality rates (11.66 ± 2.36%) recorded in monoculture Clarias gariepinus, the highest cannibalism rates were obtained in monoculture of Heterobranchus longifilis (13.33 ± 4.71%). The survival rate was not influenced by the type of culture. Nevertheless, the highest rate (94.44 ± 0.00%) was observed in Heterobranchus longifilis in polyculture. The highest growth values were recorded for C. gariepinus in polyculture and the weakest for H. longifilis in polyculture. For linear growth, the highest values were recorded in C. gariepinus in monoculture. In order to reduce the rate of cannibalism and mortalities in Clarias gariepinus and Heterobranchus longifilis in post f ingerlings growth phase, it is preferable to combine these two species.

Nana Towa Algrient¹, Nanmegni Rostand Romeo¹, Tonfackachille Peguy², Efole Ewoukem Thomas¹ and Jouokou Salifou²