International Journal of Recirculating Aquaculture
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Carrie Cross
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Template for submissions to the International Journal of Recirculating Aquaculture.
Template for submissions to the International Journal of Recirculating Aquaculture.
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\pubyear{2017}
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\begin{document}
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\title[Two Organic Carbon Application Rates]{Two Organic Carbon Application Rates to Control Inorganic Nitrogen in Minimal Water Exchange, Biofloc, Shallow Water, Shrimp Nursery Systems}
\author[1]{Jack Crockett\thanks{smpjkc@yahoo.com}}
\author[1, 2, 3]{Addison Lawrence}
\affil[1]{Texas A\&M University AgriLife Research Mariculture Laboratory at Port Aransas, 1300 Port St., Port Aransas, TX 78373 USA}
\affil[2]{Department of Wildlife and Fisheries Science,
210 E Nagle Hall, 2258 TAMU, Texas A\&M University
College Station, TX 77843-2258 USA}
\affil[3]{Department of Biological Sciences, Texas A\&M University-Corpus Christi, 6300 Ocean Drive, Corpus Christi, TX 78412-5843 USA}
\maketitle
\begin{abstract}
The objectives of this study were to develop and test a quantitative method for reactive carbon application to control inorganic nitrogen, and to compare the effect of carbon application using 40\% and 60\% microbial conversion efficiency (MCE) while leaving a residual 11.3 mg/l nitrate nitrogen ($\text{NO}_3$-N) level. The organic carbon requirement was based on the carbon to nitrogen ratio of the elemental composition of microbial cells. The source of supplemental organic carbon was short-chained fructooligosaccharide (scFOS). Correction for moisture was duplicated on the first 2 days of scFOS application, so the actual efficiency rates were 35.1\% and 58.3\%. The proposed carbon quantitative method was effective in predicting the amount of carbon required to control inorganic nitrogen. Both 35.1\% MCE and 58.3\% MCE maintained total ammonia nitrogen (TAN) and nitrite nitrogen ($\text{NO}_2$-N) at desired levels of equal to or less than 2.3 mg/l and 3.1 mg/l, respectively. The amount of carbon applied using 35.1\% MCE was higher than with 58.3\% MCE. The 58.3\% MCE treatment resulted in slightly higher $\text{NO}_3$-N levels than 35.1 \% MCE. The most toxic species of inorganic nitrogen, TAN and $\text{NO}_2$-N, are assimilated by heterotrophic bacteria before $\text{NO}_3$-N, permitting decreased reactive carbon input and water quality improvement. The benefits of 58.3\% MCE vs. 35.1\% MCE were lower organic loading, reduced water replacement, and decreased costs. The total water replacement associated with biofloc control was 0.24\% using 35.1\% MCE and 0\% using 58.3\% MCE. After a culture period of 14 days the mean weight was 65.5 mg and 61.9 mg for 31.5\% MCE and 58.1\% MCE, respectively, and a survival of 79.5\% for both MCE's.
\end{abstract}
\begin{keywords}
Biofloc, minimal water exchange, shallow water systems, inorganic nitrogen control, Short Chained Fructooligosaccharide \end{keywords}
%%%%%%%%%%% Introduction %%%%%%%%%%%%
\section{Introduction}
\vspace*{-1pt}
\noindent For a number of years shallow water biofloc nurseries have been used to successfully produce juvenile \textit{Litopenaeus vannamei}, Pacific White-legged Shrimp, at Texas AgriLife Research Mariculture laboratory in Port Aransas, Texas. The focus of simulated production trials has been to develop a method for commercial production of juvenile shrimp at inland sites where seawater is not available. The reduction of salinity in water used within recirculating aquaculture systems can lead to production of shrimp at lower costs because of the need for less salt and easier management of wastewater \citep{sch+al2010}. Ammonia and nitrite toxicity increases as salinity decreases. \citep{linche2001, linche2003}. High nitrate nitrogen levels are detrimental to shrimp, especially at low salinity, as they can reduce growth, decrease survival, and cause negative effects on product marketability \citep{kuhn+al2010}. Initial simulated production trials were carried out in full strength seawater (28 ppt), however, the objective was to develop an acceptable minimal water exchange process, before testing it in low salinity water where the inorganic nitrogen level is more critical.
During initial biofloc trials, ammonia and nitrite levels were controlled throughout the entire production trial primarily through oxidation by nitrifying bacteria in autotrophic dominant biofloc \citep{cro+al2012}. Both ammonia and nitrite were kept at levels acceptable for shrimp culture in low salinity water, however, this technique resulted in nitrate nitrogen levels higher than optimal for low salinity shrimp culture. The end product of nitrification is nitrate nitrogen \citep{ritmcc2001}. Attempts were made to dilute nitrates, however, the result was a spike in nitrite nitrogen \citep{cro+al2012}. Water exchange rates above 30\% per day wash more nitrifying bacteria out of a system than the amount required to maintain steady nitrification \citep{avn2009}.
An option to reduce nitrate nitrogen levels was to provide enough organic carbon for heterotrophic bacteria to assimilate ammonia and nitrites rather than allowing nitrifying bacteria to oxidize these types of inorganic nitrogen to nitrates. A methodology was developed to control inorganic nitrogen by sequencing autotrophic and heterotrophic bacterial dominance \citep{cro+al2013}. In this process ammonia and nitrite nitrogen were initially controlled through oxidation, followed by inorganic nitrogen bacterial assimilation. When enough suspended particulate matter within the water column had been established to serve as media on which heterotrophic bacteria colonies could develop, heterotrophic dominance was promoted.
Organic carbon is required for heterotrophic bacteria to assimilate inorganic nitrogen for cell synthesis \citep{ritmcc2001}. Nitrogen input was reduced at the same time organic carbon input was increased by decreasing the feed protein level. Organic carbon input was also increased by applying a carbon source to reduce the concentration of inorganic nitrogen in the production system. A methodology was developed to keep inorganic nitrogen levels close to zero \citep{cro+al2013}.
However, it is desirable to have a residual level of nitrate nitrogen for proactive prevention of sulfates being reduced to hydrogen sulfide, should anaerobic pockets develop \citep{chuelm1999, usper2014}. Low levels of nitrates (up to 35 mg/l) are not detrimental to shrimp, even at greatly reduced salinities \citep{kuhn+al2010}. Less organic carbon application is required if low levels of nitrate nitrogen remain in the system. If less organic carbon is applied, there is less the organic loading and production costs.
One of the objectives of this trial was to develop a quantitative method to determine the amount of organic carbon required to assimilate total ammonia nitrogen, nitrite nitrogen, and a selected level of nitrate nitrogen. The targeted residual nitrate nitrogen concentration was approximately 11 mg/l.
Studies using stoichiometric analysis have reported that heterotrophic bacteria require 6.07 grams of organic carbon for each gram of total ammonia nitrogen (TAN) assimilated \citep{ebe+al2006}. In these studies it was assumed the system was pure heterotrophic bacteria, and no autotrophic bacteria were present. It was concluded that if enough organic carbon is present to assimilate TAN, there is no production of nitrite nitrogen ($\text{NO}_2$-N) or nitrate nitrogen ($\text{NO}_3$-N).
It has also been reported that there are no totally autotrophic and no totally heterotrophic systems, and there is always a mix between the two types of bacteria \citep{avn2009}. When sequencing autotrophic and heterotrophic dominance, autotrophic bacteria are initially inoculated, followed by promotion of heterotrophic bacterial dominance. In this study it was assumed both autotrophic and heterotrophic bacterial populations were present, and that both oxidation and assimilation of inorganic nitrogen was occurring simultaneously.
Ammonia nitrogen can be assimilated relatively easily by heterotrophic bacteria because it is more reduced than other forms of inorganic nitrogen. Nitrate and nitrite must be reduced by enzymes to ammonia before assimilation occurs, but all types of inorganic nitrogen can be incorporated into organic material by heterotrophic bacteria if organic carbon is available \citep{pre+al1990}. It was accepted the carbon requirement for nitrogen in TAN, ($\text{NO}_2$-N), and ($\text{NO}_3$-N) needed to be taken into consideration to determine the amount of organic carbon required.
It was assumed the amount of organic carbon required to assimilate inorganic nitrogen is proportional to the ratio of carbon and nitrogen in microbial cells. Bacteria have a large range of carbon and nitrogen levels. Mean values were selected to be the base for the calculations for the addition of organic carbon. Means of the percentage ranges give an average carbon to nitrogen ratio of 5.17:1. Table 1 provides information concerning the carbon, oxygen, hydrogen, and nitrogen values used in this study.
\begin{center}
\emph{\footnotesize Table 1. The chemical composition of prokaryotic cells resulting in mean carbon to nitrogen ratio of 5.17:1.}
\includegraphics[width=\linewidth]{Crockett_Eq_1.png}\par
\refstepcounter{figure}
\end{center}
The potential microbial biomass that can be generated from inorganic nitrogen was projected using 9.46\% nitrogen biomass content. The required amount of carbon to become bacterial tissue was estimated using 48.9\% carbon biomass content.
During metabolism some organic carbon is lost as carbon dioxide due to cellular respiration through catabolism and some carbon becomes microbial biomass through anabolism \citep{ritmcc2001}. The percentage of assimilated carbon with respect to metabolized feed carbon is defined as the microbial conversion efficiency and is in the range of 40-60\% \citep{avn2009}. The primary objective of this study was to compare two microbial conversion efficiency (MCE) rates (40\% and 60\%).
%%%%% Materials and Methods %%%%%%
\section{Materials and Methods}
\vspace*{-1pt}
\subsection{Aquaculture System}
\noindent Four 1.5 m square tanks were filled with filtered 28 ppt seawater to a depth of 20 cm. Each tank contained five aeration hoses, a submersible heater, an automatic belt feeder, and 8mm square netting suspended into the water column to increase surface area and to mitigate water circulation. The dissolved oxygen level was maintained above 5 mg/l, the temperature was kept at $28 \pm 1$\textdegree\ centigrade, and the feeders were loaded once every 24 hours in the morning.
Each tank was equipped with a settling tank used to remove excess biofloc. Water was moved into the settling tank by an airlift pump which had a 0.5 to 0.8 liter per minute capacity. Treated water returned to the culture tank by gravity.
Low light level (36 lumens per m\textsuperscript{2}), which is beneficial for nitrifying bacteria development, was maintained except for brief periods when system maintenance was being carried out.
\subsection{Stocking Procedure}
\noindent Post larvae were provided by Shrimp Improvement Systems, Islamorada, Florida. The tanks were stocked with PL\textsubscript{13} \textit{Litopenaeus vannamei} (mean size 3.7 mg) at an average density of 3,295/m\textsuperscript{2} (16,475/m\textsuperscript{3}). The number of animals stocked were counted at the hatchery, and upon arrival were counted again using an XpertSea Solutions, Inc. electronic counter.
The post larvae were acclimated to the salinity, pH, temperature, and overall tank water conditions over a 90 minute period. No mortality or stress were observed. As soon as the animals were released into the tank feed was proffered.
\subsection{Hydrological Parameters and Water Quality}
\noindent Dissolved oxygen, temperature, and salinity were measured once daily with an YSI 85 oxygen conductivity, salinity and temperature meter. Municipal fresh water, treated by reverse osmosis, was added as needed to replace water lost by evaporation.
Total ammonia nitrogen, nitrite nitrogen, nitrate nitrogen, pH, and alkalinity, were monitored every morning and afternoon. Tetra test strips were used to get rapid results on inorganic nitrogen levels. Standard inorganic nitrogen solutions were used to validate test strip readings. On a weekly basis test strip values for ammonia and nitrite were compared to Hach DR3900 analysis results. Samples were sent to an independent lab for comparison of nitrate nitrogen values.
Settleable solids were determined twice daily with Imhoff cones at 7:00 a.m. and 4:00 p.m. These values were used to define the biofloc level.
\subsection{Feeding Regime}
\noindent The daily estimated population was adjusted for expected mortality. Four samples from each tank averaging 90 animals each were taken during the culture period. The average weights were used to adjust the feeding curves which were based on known growth rates. The expected weight gain per animal was multiplied by the number of animals per tank times the FCR to quantify the daily feed ration. Tank bottoms were checked every morning after the feeding cycle was over to check for uneaten feed. The percentage of protein in the feed is described in the sections on bacterial dominance.
\subsection{Autotrophic Dominance}
Autotrophic dominance was promoted until biofloc levels reached a minimum of 3 ml/l. During this period 41.3\% protein (on an as-used basis) feed was given to provide complete nutritional requirements. The carbon to nitrogen ratio (C:N) of this feed is low (about 7.8:1 on an as-used basis), which limits the amount of carbon available for heterotrophic bacteria to assimilate inorganic nitrogen, restricting their competition with autotrophic bacteria.
To rapidly initiate a population of nitrifying bacteria, the tanks were inoculated with commercial inoculum (Fritz Turbostart 900) at a rate of 0.2 ml/l (90 ml/l per tank) immediately after the shrimp were stocked. Thereafter, every morning at 7:00 a.m. and every afternoon at 4:00 p.m. inorganic nitrogen was monitored with test strips. If the total ammonia level was 2 mg/l or higher, 90 ml of inoculum was applied. If the $\text{NO}_2^-$ level was 2 mg/l or greater an additional 90 ml of inoculum was applied. The nitrifying bacteria inoculum was applied as needed during the period autotrophic dominance was being promoted, and on the first day of transition from autotrophic to heterotrophic dominance.
\subsection{Alkalinity Management}
\noindent Sodium bicarbonate was added to the tank water to maintain alkalinity and pH at desired levels (160 mg/l to 200 mg/l and 7.5 to 8.6, respectively). Sodium bicarbonate was applied when the level dropped to 160 mg/l or lower using a formula defined by \citet{cro+al2012}. See Equation 1 for the equation used to determine sodium bicarbonate required.\par
\begin{center}
\emph{\footnotesize Equation 1. Formula to calculate sodium bicarbonate required to raise alkalinity to 200 mg/l.}
\includegraphics[width=\linewidth]{Crockett_Eq_1.png}\par
\refstepcounter{figure}
\end{center}
\subsection{Heterotrophic Dominance}
\noindent When Imhoff cone readings indicated the biofloc levels were greater than 3 ml/l heterotrophic dominance was promoted. The feed was changed to 21.5\% protein (on an as-used basis) which reduced the C:N ratio to about 15:1. To further increase the C:N ratio, scFOS was applied daily in proportion to existing inorganic nitrogen levels. In this manner, enough organic carbon was available for heterotrophic bacteria to be dominate.
It was assumed all inorganic nitrogen in the system was available to be assimilated by heterotrophic bacteria and become microbial biomass. The potential microbial biomass resulting from assimilation of inorganic nitrogen is directly proportional to the amount of inorganic nitrogen in the system. For each part of microbial biomass there are 0.0946 parts of nitrogen. Therefore, inorganic nitrogen divided by 0.0946 is equal to potential microbial biomass. Selected inorganic nitrogen was calculated using the sum of mg/l TAN, mg/l $\text{NO}_2$-N and $\text{NO}_3$-N above 11.3 mg/l. For each part of potential microbial biomass there are 0.489 parts of carbon, so this proportion was used to calculate the amount of carbon required to be assimilated by potential microbial biomass.
Equation 2 shows the hypothetical quantification of potential microbial biomass from a selected level of inorganic nitrogen, and determination of the amount of carbon required for inorganic nitrogen assimilation. The amount of carbon in mg/l was converted to grams of carbon required per tank.
\begin{center}
\emph{\footnotesize Equation 2. Hypothetical calculation of potential biomass from a selected level of inorganic nitrogen and the determination of the amount of carbon required to assimilate the inorganic nitrogen.}
\vspace{.1 cm}
\includegraphics[width=\linewidth]{Crockett_Eq_2.png}\par
\refstepcounter{figure}
\end{center}
The carbonaceous substance to apply (with 100\% efficiency) was determined by adjusting for moisture and percent carbon. See Equation 3 for the equations used to calculate the amount of carbon required, and the amount of carbonaceous substance to apply to each tank.
\begin{center}
\emph{\footnotesize Equation 3. Quantification of carbon needed per tank and the amount of carbonaceous substance required.}
\includegraphics[width=\linewidth]{Crockett_Eq_3.png}\par
\refstepcounter{figure}
\end{center}
The source of carbon used for reactive control of inorganic nitrogen was short-chained fructooligosaccharide (scFOS) which is a prebiotic having 40.98\% carbon on an as-used basis. ScFOS was applied to convert excess inorganic nitrogen to bacterial biomass in two tanks at 40\% MCE and two tanks at 60\% MCE. Equation 4 gives the equation used to determine the amount of scFOS to apply for both 40\% MCE and 60\% MCE.
\begin{center}
\emph{\footnotesize Equation 4. Quantification of scFOS applications for both microbial conversion efficiency rates.}
\vspace{.1 cm}
\includegraphics[width=\linewidth]{Crockett_Eq_4.png}\par
\refstepcounter{figure}
\end{center}
%%%%%%%%% Results and Discussion %%%%%%%%%
\section{Results and Discussion}
\noindent Correction for moisture was duplicated on the first two days of scFOS application, so the actual microbial conversion efficiency rates turned out to be 35.1\% and 58.3\% rather than 40\% and 60\%.
\begin{center}
\emph{\footnotesize Table 2. Mean daily hydrological parameters, and biofloc. Mean harvest weight, survival, water replacement, and FCR. The values are means of two replicates per treatment.}
\includegraphics[width=\linewidth]{Crockett_Table_2.png}\par
\refstepcounter{figure}
\end{center}
Table 2 details mean hydrological parameters, mean biofloc levels, mean harvest weights, mean survivals, mean water replacement, and mean FCR. Mean parameters were very similar and not significantly different for both treatments. However, mean biofloc levels were slightly higher in treatment 35.1\% MCE, and settling was required to keep levels within those specified by trial standards. Approximately 0.24\% water replacement was needed to make up for what was lost during biofloc removal. Treatment 58.3\% MCE did not require biofloc settling or water replacement. The harvest weight was slightly higher for the 35.1\% MCE treatment.\par
\begin{center}
\emph{\footnotesize Table 3. Mean TAN, $\text{NO}_2$-N and $\text{NO}_3$-N for 35.1\% and 58.3\% microbial conversion efficiency rates. The values are daily means of two replicates per treatment in mg/l nitrogen.}
\includegraphics[width=\linewidth]{Crockett_Table_3.png}\par
\refstepcounter{figure}
\end{center}
Table 3 details the mean levels of inorganic nitrogen for both treatments during heterotrophic dominance promotion. ScFOS was applied in all tanks on a daily basis during the heterotrophic phase (days 6 through 13). Mean TAN and $\text{NO}_2$-N were very similar for both treatments during this period. At the beginning of the heterotrophic phase (day 6), mean $\text{NO}_3$-N values were very similar for both treatments. Mean $\text{NO}_3$-N during the entire heterotrophic period (days 6 through 14) was slightly higher in the 58.3\% MCE treatment.
Details on daily and accumulated scFOS applications are shown in table 4. During the first 3 days heterotrophic dominance was stimulated, mean daily scFOS applications were greater for the 35.1\% MCE treatment. Thereafter, the amount of daily scFOS applied for both treatments were more similar. Accumulated scFOS applied was greater for the 35.1\% MCE treatment.
\begin{center}
\emph{\footnotesize Table 4. Daily and accumulated scFOS application for 35.1\% and 58.3\% microbial conversion efficiency rates. The values are means of two replicates per treatment in grams.}
\includegraphics[width=\linewidth]{Crockett_Table_4.png}\par
\refstepcounter{figure}
\end{center}
Figure 1 shows trends of accumulated scFOS for both application rates projected forward 3 periods (days). The difference between the amounts of accumulative scFOS for each treatment, progressively decreased with time. These trends intersect indicating the same amount of scFOS may have been estimated for both treatments in the future. If this is true, the sum of inorganic nitrogen would have to be higher for the 58.3\% MCE rate and lower for the 35.1\% MCE rate.
\begin{center}
\emph{\footnotesize Figure 1. Trends of accumulated scFOS application for both MCE rates projected forward 3 periods.}
\includegraphics[width=\linewidth]{Crockett_Fig_1.png}
\end{center}
TAN, $\text{NO}_2$-N, and $\text{NO}_3$-N levels as compared to daily carbon application for both treatments are given in Figure 2. In both treatments TAN and $\text{NO}_2$-N were assimilated before $\text{NO}_3$-N. Mean daily TAN and $\text{NO}_2$-N levels were very similar for both treatments even though more organic carbon was applied in the 35.1\% MCE treatment. TAN levels did not increase above 2 mg/l and $\text{NO}_2$-N did not increase above 3.1 mg/l during the experimental period.
\begin{figure*}
\begin{center}
\emph{\footnotesize Figure 2. Daily scFOS carbon applications compared to inorganic nitrogen levels.}
\includegraphics[width=.7\linewidth]{Crockett_Fig_2.png}
\end{center}
\end{figure*}
Figure 3 shows accumulated carbon as compared to inorganic nitrogen. Total accumulative scFOS applications were 0.6312 and 0.5327 g/l in treatments 35.1\% MCE and 58.3\% MCE, respectively. At trial termination 15.65\% less scFOS was applied in the 58.3\% MCE treatment. This occurred because the lower efficiency rate called for a greater application rate.
\begin{figure*}
\begin{center}
\emph{\footnotesize Figure 3. Accumulative scFOS carbon applications compared to inorganic nitrogen levels.}
\includegraphics[width=0.7\textwidth]{Crockett_Fig_3.png}\par
\end{center}
\end{figure*}
Figure 4 compares TAN, $\text{NO}_2$-N and $\text{NO}_3$-N for both treatments. 35.1\% MCE carbon application rate was more precise in maintaining nitrate nitrogen at the selected level (11.3 mg/l). Mean daily nitrate levels in treatment 58.3\% MCE were slightly higher resulting an average of 1.88 mg/l $\text{NO}_3$-N greater than selected. The differences were not significant.
There was not enough carbon in the 21.5\% protein feed to assimilate enough inorganic nitrogen to maintain the desired level of 11.3 mg/l $\text{NO}_3$-N residual nitrate. Daily scFOS applications were required to reduce inorganic nitrogen. Gradually decreasing the amount of protein in the feed will help determine what percentage protein in the feed will maintain 11.3 mg/l nitrate nitrogen with only minimal scFOS applications. Ongoing daily scFOS applications are beneficial because scFOS promotes proliferation of non-pathogenic beneficial bacteria.
\begin{center}
\emph{\footnotesize Figure 4. Inorganic nitrogen levels with 35.1\% and 58.3\% microbial conversion efficiency scFOS application rates.}
\includegraphics[width=\linewidth]{Crockett_Fig_4.png}\par
\refstepcounter{figure}
\end{center}
%%%%%%%%%%%% Conclusions %%%%%%%%%%%%%
\section{Conclusions}
\noindent The hypothetical carbon quantification methodology was effective in predicting the amount of carbon required to control inorganic nitrogen. Both 35.1\% MCE and 58.3\% MCE maintained TAN and $\text{NO}_2$-N at desired levels. The amount of carbon used in the 35.1\% MCR treatment resulted in greater biofloc levels. This required settling to remove excess biofloc, and water to replace what was lost during biofloc removal. Ammonia and nitrites were assimilated before nitrates. This permits flexible carbon application management to maintain good water quality. Accumulated scFOS trends projected forward indicated that ultimately, the MCE rate may not affect the amount of carbon being applied. The 58.3\% MCE treatment had the benefits of reduced organic loading, reduced water replacement, and decreased costs. The 58.3\% MCE treatment produced slightly higher benign $\text{NO}_3$-N levels.
%%%%%%%%%%%% Acknowledgments %%%%%%%%%%%%%
\section{Acknowledgments}
\noindent We would like to thank graduate students Jolly Morgan and Ivy McClellan for their help in stocking and harvest of the production trial. We would like to thank technician Wendy Baxter for help in preparing experimental diets, technician Woodie Lawson for assistance in system preparation, and technician Roger Anderson for help in system maintenance.
We would like to acknowledge Colorite Plastics for donating air diffuser hoses, Fritz Industries for providing nitrifying bacteria, Ingredion for providing scFOS, Shrimp Improvement Systems for quantifying small batches of PL's to be stocked, Ziegler Brothers for providing feed and feeders, and XperSea Solution, Inc. for providing training and use of the electronic post larvae counter.
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\end{document}