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# An alternative kernel-based method for estimating copepod growth rates from multimodal biomass distributions in artificial cohort experiments

*Zoological Studies*
**volume 52**, Article number: 14 (2013)

## Abstract

### Background

Elucidating copepod growth and production rates is important in understanding the trophic role of copepods in marine systems. One of the most commonly used field methods for measuring copepod growth rates is the artificial cohort method.

### Results

An ‘artificial cohort’ is established by limiting the incubated animals to relatively narrow size ranges or developmental stages. Thus, one can measure the change in body weight (BW; attributed to body growth) between the start and conclusion of incubation by following the shift in the biomass distribution. The critical issue here is determining how to describe the biomass distribution before and after incubation in a mathematically concise manner. Traditionally, the mean value of the biomass distribution is used as the representative BW, which assumes that the biomass distribution follows a unimodal distribution. However, in practice, the complex composition of copepod communities can commonly yield observations of multimodal distributions. To overcome this difficulty, we suggest that the representative BW of copepod communities be estimated by multiple-peak consideration instead of using the average value. Specifically, we used a kernel-based approach to determine peak values; as such, only BW values associated with a high frequency were used to determine the representative BW.

### Conclusions

Through a comparison of different methods, we show that the multiple-peak consideration yielded a higher proportion of realistic growth rate values. In addition, we noted that growth rates estimated with the multiple-peak method were more closely aligned with predictions based on the metabolic theory of ecology.

## Background

Copepods represent the main component of the marine mesozooplankton, contributing about 80% to the total abundance (Verity and Smetacek 1996). This group also plays important roles in linking primary production to higher trophic levels in pelagic food webs (Cushing 1989). Importantly, small species (as well as early developmental stages of larger species) represent a key component in marine ecosystems due to their high abundance, wide distribution (Turner 2004), high weight-specific ingestion rate (Levinsen et al. 2000), and year-round presence and reproduction (Lischka and Hagen 2005; Madsen et al. 2008). Therefore, empirical studies of specific properties of these small copepods such as variations in productivity may help clarify their contributions to marine ecosystem functioning.

Estimates of growth rates are one of the most important processes (Kiørboe 1997) used to investigate the trophodynamics of copepods in marine ecosystems. Several methods were developed to measure copepod growth rates (see Runge and Roff (2000) for a review). One of the best studied and applied field techniques is the artificial cohort (AC) method, which was developed by Kimmerer and McKinnon (1987). In practice, the approach relies on the creation and incubation of ACs consisting of selected developmental stages or size fractions (e.g., McKinnon and Duggan 2003). The AC method is often applied in empirical studies (e.g., Hopcroft et al. 1998; McKinnon and Duggan 2003; Kobari et al. 2007) because it relies on fewer assumptions than other approaches (e.g., the molt rate method; Peterson et al. 1991; Hirst et al. 2005). Basically, one only has to assume exponential growth and no artificial interference during incubation; also, the estimation is relatively free from the bias of mortality (Kimmerer et al. 2007).

The key issue in the AC method as discussed here is the ability to obtain a correct biomass distribution of the AC. Under ideal conditions, the AC method should create cohorts with a unimodal distribution of biomass, and thus, the average value can be used as a representative body weight (BW) value for the ‘cohort.’ However, there are several technical issues in field sampling which can make estimates based on average values inappropriate. For example, most studies only analyzed cohorts of a single developmental stage (nauplius or copepodite); as such, those copepods undergoing a stage transition (e.g., NVI to CI or CV to adult) will be missed in the biomass distribution at the end of incubation (Calbet et al. 2000; Kimmerer et al. 2007). The disappearance of these individuals in transitional stages after incubation can lead to underestimates of growth rates. More importantly, the biomass distribution of copepod assemblages may consist of multiple peaks, despite efforts to create a single peak by the AC technique. This often occurs when the AC method is applied to estimate community growth rates because different species within the community may have different biomass distributions and growth rates. Such an issue is particularly problematic in subtropical and tropical environments where copepod communities are complex and diverse (e.g., Hsieh et al. 2005; Tseng et al. 2008). Furthermore, contamination from imperfect sieving or clogging by algae (Kimmerer et al. 2007; Kobari et al. 2010) can further exacerbate this situation, especially in tropical and subtropical environments where surface waters are often overgrown by microalgae (McKinnon 1996). Under such circumstances, growth rates calculated with simple average biomass values may be biased by the frequency difference between assemblages before and after incubation. For example, if an assemblage before incubation has two peaks and the larger peak is associated with a high BW (i.e., it is highly skewed) and the corresponding assemblage after incubation also has two peaks but the larger peak is now associated with a low BW (as illustrated in Figure 1), the estimated growth rate will be underestimated (and vice versa). One may argue that a way to resolve this issue is to incubate one species at a time; however, this is not practical in tropical and subtropical environments where copepod diversity is high and sorting live animals to species level at sea is difficult.

To overcome these technical issues in the AC method for growth rate estimates, we developed a new procedure that accounts for multiple BW peaks in AC experiments. Herein, we measured *in situ* copepod weight-specific growth rates in the East China Sea by employing the AC method. We demonstrate the efficacy of our new technique of multiple-peak consideration by comparing growth rates estimated with different enumeration methods. First, we compare the number of realistic growth values. Second, we investigate whether growth estimates more closely follow predictions arising from the metabolic theory of ecology (MTE) (Brown et al. 2004) which incorporates both the effects of temperature (*T*) and body mass (*M*) on the weight-specific growth rate (*g*):

where *E* is the enzyme-catalyzed activation energy for biochemical reactions of metabolism and *k* is Boltzmann's constant (eV/K). Such an evaluation is based on the observation that the MTE has been widely tested empirically in rate measurements (e.g., Gillooly et al. 2001; Lek et al. 2012; Price et al. 2012) and has theoretical support (Brown et al. 2004).

## Methods

### Sampling

All sampling and incubations were carried out aboard the *R/V Ocean Researcher I* (OR1) and *R/V Ocean Researcher II* (OR2) from March 2009 to November 2011. We carried out AC experiments at 31 stations located in the East China Sea and western Pacific area near Taiwan (Figure 2). Environmental data (e.g., depth-specific temperature) were obtained using a Sea-Bird CTD-General Oceanic Rosette (Sea-Bird Electronics, Inc., Bellevue, WA, USA) equipped with 20-L Go-Flo bottles (General Oceanics, Miami, FL, USA). Incubation temperatures were measured periodically during incubation or from CTD measurements of surface seawater temperatures if the former measurement was lacking.

### AC method

Copepod weight-specific growth rates were measured using the AC method (Kimmerer and McKinnon 1987). We restricted the body size range of animals by selective filtration in order to create ACs as illustrated in Figure 3. Similar to McKinnon and Duggan (2003), we used 50- to 80-μm and 100- to 150-μm size fractions to respectively isolate nauplii and copepodites. Shipboard incubations for each size fraction were carried out using three replicates in 20-L collapsible polyethylene cubitainers. Incubation seawater (and the food contained therein) was collected from 10 m using 20-L Go-Flo bottles. This water was screened through a 50-μm mesh (in order to exclude mesozooplankton), and the cubitainers were filled to approximately 90% capacity. Seawater accompanying the size-fractionated zooplankton made up the remaining volume of each 20-L cubitainer.

Live zooplankton (mainly copepods) were collected using two separate Norpac zooplankton nets (50- and 100-μm mesh, respectively, and each with a ring diameter of 45 cm; General Oceanics, Miami, FL, USA). At each station, nets were set to 10 m in depth and allowed to drift with the ship for 5 to 10 min. The contents of each net were carefully resuspended in buckets filled with prescreened incubation seawater. After gentle mixing, the contents of the 50-μm net were reverse filtered through an 80-μm mesh and siphoned (approximately 2 L) into cubitainers for the 50- to 80-μm AC incubations. Another subsample from the 80-μm-mesh reverse filtrate, representing the biomass distribution at the start of the incubation (i.e., time 0), was preserved with 5% formalin-buffered seawater. The process was repeated using the contents of the 100-μm-mesh net and reverse filtered with a 150-μm mesh to establish a 100- to 150-μm AC. All cubitainers were incubated in dark black tanks (of about 200 L in volume) filled with circulating seawater pumped constantly from the surface during each cruise. Incubation periods were 24 h for the 50- to 80-μm size fraction and 48 h for the 100- to 150-μm size fraction in order to allow sufficient time for measurable growth to occur. The lengths of the incubation periods were also carefully considered; therefore, we assumed no container effects (e.g., food limitation) for the organisms in the cubitainers during these periods. After incubation, the contents of each cubitainer were concentrated onto a 50-μm mesh and preserved with 5% formalin-buffered seawater.

### Classification and growth rate estimation

Preserved samples were identified and counted using a dissecting microscope, and images of 8 × 10 magnification were taken using a CCD camera (Olympus DP71 with the software analySIS LS Starter 2.6; Olympus America Inc., Center Valley, PA, USA) mounted on the microscope. We followed the protocol of McKinnon and Duggan (2003) and limited our analysis to copepod morphotypes rather than individual species (e.g., Kimmerer and McKinnon 1987; Liu and Hopcroft 2006a, b; Kobari et al. 2007). In the 50- to 80-μm size fraction, our morphotypes were calanoid (Calanoida) and cyclopoid (Cyclopoida) nauplii. We occasionally found harpacticoid (Harpacticoida) nauplii in our incubations, and these animals were measured and enumerated when sufficiently abundant. In the 100- to 150-μm size fraction, we identified, counted, and measured calanoid, oithonid (Cyclopoida: Oithonidae), harpacticoid, oncaeid (Poecilostomatoida: Oncaeidae), and corycaeid (Poecilostomatoida: Corycaeidae) copepodites in addition to calanoid and cyclopoid nauplii. The taxonomic resolution of identification was determined under consideration of the trade-off with sample sizes. Each morphotype contributed to one growth rate value (if available) from a single incubation.

The prosome length and width of each individual were measured from digital images of the copepods. Body mass metrics for morphotypes of different shapes were calculated according to Svetlichny (1983):

where *K*
_{
c
} is a constant (0.6 for calanoids and 0.705 for cyclopoids; McKinnon and Duggan 2003) and has an average value of 0.65 for groups where conversion factors were not available. A conversion factor of 0.135 × 0.42 was used to convert the wet weight to carbon weight, i.e.,

(Postel et al. 2000) and

(Beers 1966).

Assuming exponential growth (e.g., Kimmerer et al. 2007), the weight-specific growth rate (*g*) was calculated as

where *W*
_{0} is the carbon weight of copepods at the beginning of incubation, *W*
_{
T
} is the carbon weight at the end of incubation, and *T* represents the respective incubation times of 24 and 48 h for the 50- to 80-μm and 100- to 150-μm size fractions.

### Calculation and comparison of three estimates of the representative BW

The representative BW value (in units of carbon) for each copepod assemblage (i.e., *W*
_{0} and *W*
_{
T
}) was estimated by three methods for comparison: (1) the average value, (2) mode value, and (3) multiple-peak consideration. Only assemblages with ≥30 individual copepods were used here (the average number for each morphotype was approximately 160 and ranged from 30 to 1,182). The first method using the average value was the same as the traditional method for BW estimation: without prior examination of the biomass distribution, the representative BW value was calculated as the geometric mean value of the BW of all copepod individuals for each assemblage of each morphotype (e.g., *W*
_{0} = exp(-2.31), the dashed line in Figure 1A; *W*
_{24} = exp(-2.02), the dashed line in Figure 1B).

The procedures for the methods considering the mode value and multiple peaks were as follows. In the first step, we calculated the probability density estimate (PDE) using ln(BW) values of all copepod individuals by a kernel-smoothing technique (see Figure 1 for an illustration) for each assemblage of each morphotype. First, a discrete distribution of biomass was approximated by a continuous distribution based on a normal kernel function (Bowman and Azzalini 1997), with a bandwidth of the kernel-smoothing window of 0.1. Second, local maximal values (peaks) of the PDE were located and singled out. To avoid any bias caused by outliers, we excluded minor peaks that had a probability density (peak height) of <1/3 the height of the largest peak (e.g., the peaks where BWs were exp(-1.00) and exp(-0.32) in Figure 1B were accordingly excluded). Third, unreasonable values (which might arise from contamination, experimental failure, or different growth rates of organisms within cohorts) were removed. The criteria for removal were as follows: for any peak BW at *T* = 0 that was higher than all peak BWs at *T* = 24/48, that peak at *T* = 0 was eliminated. Similarly, for any peak BW at *T* = 24/48 that was lower than all peak BWs at *T* = 0, that peak at *T* = 24/48 was also eliminated. If there was no remaining peak at *T* = 0 or all *T* = 24/48, the growth rate was not calculated. Following this criterion, only one or two (rarely three) peaks ever remained for each assemblage. The elimination of unreasonable values based on our criteria also meant that there were fewer values remaining for calculation based on the mode value and multiple-peak consideration than with the average value approach. Unbalanced numbers of peaks between *T* = 0 and *T* = 24/48 were permitted in growth rate calculations because copepod growth patterns can vary as a consequence of the complex composition of a diverse assemblage (as described above).

For the method based on the mode value, only the BW value associated with the largest peak was chosen to represent the BW value for the assemblage (e.g., *W*
_{0} = exp(-1.98) in Figure 1A; *W*
_{24} = exp(-2.41) in Figure 1B). The mode value method is a preliminary consideration of peaks, and it can be regarded as an intermediate method between the traditional average value method and multiple-peak consideration. For the multiple-peak consideration, the average value (or single value if only one peak was identified) of the peak BWs was the representative BW value for the assemblage (e.g., *W*
_{0} = exp(-2.44) according to the two peaks of -2.90 and -1.98 in Figure 1A). Note that we have only one *T* = 0 sample and three *T* = 24/48 replicates. Thus, three pairs of [*W*
_{0}-*W*
_{
T
}] for one incubation for each morphotype were respectively calculated by each enumeration method. Each pair of [*W*
_{0}-*W*
_{
T
}] was used to calculate growth rate values by Equation 5. Finally, the growth rate estimates represent the average of the three values from the replicates.

To help illustrate differences in performance among the three methods, it is useful to show an example. According to the example shown in Figure 1, the weight-specific growth rate calculated by the average value method was -2.02 - (-2.31) = 0.29. However, an obvious underestimation can be observed in Figure 1 due to the negative-skewed biomass distribution in *T* = 0 and the positive-skewed form in *T* = 24. This problem was resolved by the multiple-peak consideration. Two peaks were extracted in both *T* = 0 (-2.90 and -1.98, average -2.44) and *T* = 24 (-2.41 and -1.61, average -2.01) assemblages, and a more appropriate estimate of the weight-specific growth rate was calculated as -2.01 - (-2.44) = 0.37. The mode value method yielded an unrealistic negative growth rate estimate of -0.43.

### Testing the efficacy of each method for growth rate estimation

In order to test the efficacy of the three methods, we performed two types of comparison. First, we simply compared the calculated growth rate values among the three methods (the pooled data included all morphotypes as representative). Specifically, the number of realistic growth rate values (weight-specific growth rate from 0 to 2) was compared. If the proportion of realistic growth rate estimates was higher for any given method, then that method was considered a better approach. Second, we fitted growth rate estimates to the relationship predicted by the MTE (Brown et al. 2004). We evaluated the goodness of fit and whether the estimated coefficient of temperature and body mass followed the prediction of the MTE for each of the three methods. The generalized linear model (GLM) is described as

where the coefficient *a*
_{0} is the intercept, *a*
_{1} is the factor of activation energy associated with temperature, and *a*
_{2} is the allometric coefficient for body mass. Here, the body mass (*M*) was measured as the carbon BW at the beginning of incubation (i.e., *W*
_{0}, which could differ due to different methods in use) for each copepod assemblage.

In addition to the analysis of pooled data, we also performed the same GLM analysis on selected abundant morphotypes, ‘calanoid’ and ‘cyclopoid’ (which combined oithonids, oncaeids, and corycaeids), in the 100- to 150-μm size fraction as representative groups. Moreover, a 10-fold cross-validation (Cudeck and Browne 1983) was performed to compare the GLM results. That is, we randomly divided the dataset into 10 subsamples and used 9 subsamples to construct the GLM model and the remaining subsample to evaluate the model performance (based on a prediction error). The same procedure was repeated 10 times to exhaust the 10 combinations, and the average error was calculated. A small prediction error was considered good performance.

### Statistical analysis

The growth rate values calculated with each of the three calculation methods were compared using a one-way analysis of variance (ANOVA). We used a GLM (Equation 6) to evaluate (1) the goodness of fit of our three types of growth rate estimates to MTE predictions and (2) the correspondence of our estimated coefficients for temperature and body size to the MTE coefficients. All of the statistical analyses used in this study were carried out with MATLAB (The Mattworks, Inc., Concord, MA, USA).

## Results

### Efficacy test 1: the number of realistic growth estimates

In total, 196 growth rate values (including all morphotypes in both size fractions) were obtained with the average value method (Table 1). However, due to elimination of unreasonable values using the criteria for removal (see “Methods” above), there were only 181 and 189 values for the methods of mode value and multiple-peak consideration, respectively (Table 1). No significant differences among the three methods in weight-specific growth rates were found (one-way ANOVA, *F* = 0.51, *p* = 0.60). When testing the efficacy of each approach using the number of realistic growth rate values, we found that there were 168, 181, and 189 growth values within the range of 0 and 2 for enumeration by the average value, mode value, and multiple-peak consideration, respectively (Table 1). The traditional average value method yielded the lowest percentage of realistic growth rate estimates (Table 1).

### Efficacy test 2: regression with temperature and body mass

Weight-specific growth rates were positively related to temperature and negatively related to body mass, regardless of which method was applied (Table 2). The coefficient of determination (*r*
^{2}) was lowest when the average value method was applied. The range of temperature coefficients overlapped with values predicted by the MTE (*E*; Gillooly et al. 2001) for all three methods. However, the coefficient for body mass did not approach the predicted value (-0.25) for rates estimated by any of the three methods (Table 2). Only the method of multiple-peak consideration yielded a less negative body size coefficient estimation, which more closely approached the predicted MTE value of -0.25 (Table 2). In addition, the method of multiple-peak consideration yielded the lowest mean squared error (MSE) for the 10-fold cross-validation (Table 2). An observation of this type was also qualitatively similar when we respectively analyzed data for the calanoid (Table 3) and cyclopoid (Table 4) subgroups.

## Discussion

In the current study, we introduced a new method of representative BW determination by multiple-peak consideration for copepod growth rate estimations. We also compared the new method with the traditional average value method by evaluating the number of realistic growth rate values and their accordance with the MTE, in order to demonstrate the performance of the multiple-peak consideration method.

We found that the method of multiple-peak consideration provided better estimates of growth rate values by yielding a higher proportion of realistic growth values (Table 1). The reason is that enumeration by the multiple-peak consideration was able to resolve problems that the traditional average value method faces. First, multiple-peak consideration avoids underestimating the representative BW when stage transitions occur during incubation. If there were no possible corresponding BW peaks after incubation (i.e., the inevitability of missed individuals after a stage transition), that BW peak before incubation would not be considered in the calculation. Second, samples must be discarded in traditional enumeration if sieving problems (leakage or clogging, e.g., Kobari et al. 2010) lead to contamination; otherwise, an abnormal distribution of biomass will result in a potential bias or higher variability in growth rate values (Kimmerer et al. 2007). By applying the multiple-peak consideration, the contamination effect was minimized because BW values of a low frequency are not considered when calculating the growth rate. Third, due to the complexity of copepod communities, one apparent cohort may consist of organisms with different growth rates. Enumeration with the multiple-peak consideration can take such a condition into account, and even the occasional unreasonable condition (e.g., negative growth) can also be handled according to the criteria for removal.

We also investigated how well the growth rates estimated with multiple-peak consideration followed predictions using the MTE (Brown et al. 2004) which incorporates the effects of both temperature (*T*) and body mass (*M*) on weight-specific growth rates. Results from all three enumeration methods were qualitatively consistent with the prediction of the MTE: growth rates were positively related to temperature and negatively related to body mass (Table 2), which were also consistent with most studies of copepod growth rates (e.g., Campbell et al. 2001; Hirst and Bunker 2003). However, the coefficient of determination (*r*
^{2}) showed that the two methods that considered mode (peak) values performed better than the traditional method that considered average values. Additionally, in spite of similar estimates of temperature coefficients among the three methods, the multiple-peak consideration method yielded a coefficient of body mass that was closer to the predicted value of the MTE (Table 2). In order to carefully examine the efficacy of MTE fitting, we also carried out 10-fold cross-validation of the regression between growth rate estimates and variables described by the MTE (i.e., temperature and body mass). The results were qualitatively similar to those of the GLM regression analysis; the MSE was lowest when applying the multiple-peak consideration (0.43, compared to 0.71 and 0.72 for the average value and mode value methods, respectively). The better performance of the multiple-peak consideration was further revealed when we focused only on representative morphotypes (calanoids and cyclopoids): only the method of multiple-peak consideration yielded coefficients of body mass and temperature which overlapped predicted MTE values (Tables 3 and 4). In addition, results from the method of multiple-peak consideration yielded the greatest coefficient of determination (*r*
^{2}) and the lowest MSE in the analysis that focused on calanoids (Table 3) and cyclopoids (Table 4). However, due to a relatively low number of data points for regression, the coefficient of determination was even lower (compared to results of the pooled data in Table 2). Certainly, a higher consistency with MTE cannot be sufficient proof of a better prediction of growth rate variation. Nevertheless, our new method indeed helped resolve some technical difficulties, such as the multimodal distribution of biomass that cannot be resolved with the traditional method.

In addition to the issue of enumeration methods, we also noted some caveats associated with sampling. Samples from different seasons or locations may be affected by different thermal or food conditions. Food resources available during incubation are indeed crucial for the growth of copepods (Lin et al. 2013), and this was also one of the reasons we chose the incubation time with an intermediate duration (the incubation time can be even longer when conducted in temperate areas). In order to completely understand the dynamics of copepod communities, further examination of seasonality and/or stage/species-specific information is required. However, there is always a trade-off between time and taxonomic resolution. This is particularly a challenge in tropical and subtropical environments. Nevertheless, this study focused on improving the data analysis of estimating growth rates and demonstrated the applicability of our method.

In this study, we sought to remove unreasonable growth rates from our analyses. However, we note here that some of those unreasonable growth rates may signal biological information. For example, some of them may be related to food-limited growth for large animals or mortality. In addition, an apparent widening of the cohorts during the course of the experiment may occur when applying the AC experiment as a result of differences in ages within stages in the initial cohort. Depending on the research question, one may want to treat these data separately in order to develop a comprehensive understanding of environmental effects.

## Conclusions

In conclusion, our results suggest that the new method of multiple-peak consideration offers a better estimation of weight-specific growth rates when resolving rates at the community level. The improvement might be most applicable in tropical/subtropical systems where problems with traditional methods can be quite significant. Further application and examination of this new method are encouraged. Through better estimates of copepod community growth rates, we hope to improve our knowledge of the ecology of copepods and further refine our understanding of the functional roles of this group in marine ecosystems.

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## Acknowledgements

We acknowledge the assistance provided by the crews of the *R/V ORI* and *R/V ORII* during sampling and Y.C. Lee and W.H. Teng with the experiments. Comments from C.W. Chang, T.S. Chiu, C. García-Comas, T. Miki, and C.t. Shih greatly improved this work. This study was supported by National Taiwan University and the National Science Council (NSC) of Taiwan.

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### Competing interests

The authors declare that they have no competing interests.

### Authors' contributions

KY carried out the sampling, collected data from microscopic work, performed the statistical analysis, and drafted the manuscript. AR participated in the design of the study, sampling, and data collection. CH conceived the study and participated in its design and coordination. All authors read and approved the final manuscript.

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### Cite this article

Lin, KY., Sastri, A.R. & Hsieh, Ch. An alternative kernel-based method for estimating copepod growth rates from multimodal biomass distributions in artificial cohort experiments.
*Zool. Stud.* **52, **14 (2013). https://doi.org/10.1186/1810-522X-52-14

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DOI: https://doi.org/10.1186/1810-522X-52-14

### Keywords

- Copepod community
- Artificial cohort method
- Metabolic theory of ecology
- Multimodal distribution