Tanja Schweers¹, Matthias Wolff², Volker Koch³ & Francisco Sinsel Duarte⁴

1 Wiesenweg 187, 27257 Sudwalde, Germany; taschweers@web.de

2 Center for Tropical Marine Ecology (ZMT), University of Bremen, Fahrenheitstrasse 6, 28359 Bremen, Germany; matthias.wolff@zmt-bremen.de

3 Universidad Autónoma de Baja California Sur (UABCS), Depto. Biol. Marina, Apdo. 19-B, Carretera al Sur, km 5.5, La Paz, B.C.S., C.P. 23080, Mexico; vokoch@uabcs.mx

4 Campo 13, Estero San Buto, Bahía Magdalena, domicilio conocido, B.C.S., Mexico

Received 30-V-2005. Corrected 12-I-2006. Accepted 23-V-2006.

Abstract: The population dynamics of an intertidal population of Megapitaria squalida was studied from September 2002 to February 2003 in Bahía Magdalena, Mexico. To obtain information about the artisanal and recreational fishery of M. squalida, local fishermen at different parts of the bay were interviewed. Clam densities were determined at one unexploited and two exploited sites along perpendicular transects from the shore line. Average clam density was 2.01±1.41 ind/m², densities did not differ significantly between the three sampling sites. The length-total mass relation was M_tot = 0.0001*SL^3.1644 (r2 = 0.9804, n = 92) and the length-tissue mass relation was Mtis = 0.0002*SL^2.7144 (r² = 0.945, n = 92). Von Bertalanffy-growth parameters were determined using marked individuals. Strong interindividual and also seasonal differences in growth were observed. Average annual values were: K = 0.655, L∞ = 83 mm. Since M. squalida can reach a shell length of more than 135 mm in deeper waters, it is necessary to consider intertidal and subtidal populations separately. Average total mortality (Z) was 1.61 y^-1. No fishing mortality was calculated because total mortality Z at the unexploited control site was higher than Z at the exploited sites. It appears that M. squalida migrates into deeper water with increasing shell length, as average shell length increased at lower tidal levels and marked specimens showed a clear migration towards deeper waters. As yet no overexploitation could be found in the study area. Rev. Biol. Trop. 54 (3): 1003-1017. Epub 2006 Sept. 29.

Key words: Megapitaria squalida, Veneridae, population dynamics, intertidal, Bahía Magdalena, México.

Chocolate clams are an important component of the benthic community in Bahía Magdalena, a shallow and highly productive coastal lagoon (Cruz-Agüero et al. 1994) located on the west coast of Baja California Sur (Fig. 1). The black chocolate clam is supporting an artisanal and recreational fishery in the region. It is harvested by divers in depths of 2-10 m using Hooka equipment and is also hand collected during spring low tides on exposed intertidal sand flats. Clams are either gathered for personal consumption or sold on the local and regional market. The shell is sometimes used for crafts and jewellery (Castro-Ortiz et al. 1992). However, there is no quantitative data on zonation, size distribution, biomass, growth and mortality available for this species and nothing is known about the present state of the fishery. The overall objective of this study was thus to study the population dynamics of M. squalida in Bahía Magdalena. Specifically, the following research questions were addressed:

- What is the population density and biomass of M. squalida at one unexploited and two exploited areas?

- What is the population size structure in the area and how does it change with water depth?

- What are the growth and mortality rates of M. squalida and how is growth influenced by environmental conditions?

- What is the local fishermens knowledge about the past and present level of the fishery?

The study is based on a six months field work conducted in the mangrove channel Estero San Buto near Puerto San Carlos, Baja California Sur. Sampling was done at the intertidal zone, which is also the main fishing area for the recreational fishery. Sampling circles were searched for specimens of M. squalida to obtain data on the population size structure, density and biomass. Growth parameters were determined from tagging data. The length-converted catch curve was used to estimate total mortality Z. Transects were sampled perpendicular to the shoreline to test the hypothesis, that clam size increases with the water depth. Migration was observed with tagged specimens. Oxygen content, temperature and turbidity of the water was recorded over the study period. Local fishermen were interviewed to obtain qualitative data about the chocolate clam fishery.

Materials and methods

Study area and sampling sites: Bahía Magdalena (Fig. 1), is located between 24º15’ N and 25º20’ N, and 111º30’ W and 112º15’ W on the Pacific coast of Baja California Sur, Mexico. This coastal lagoon system can be divided into three different areas: the north-western zone has an irregular form and is mainly composed of intertidal and shallow areas and relatively narrow mangrove channels with an average water depth of 3.5 m; the central zone, that is actually called Bahía Magdalena, is connected with the open ocean through a wide mouth (40 m deep, 4 km wide), whereas the connection to the ocean of the southern part, called Bahía Almejas, is narrow and shallow. Bahía Magdalena and Bahía Almejas are connected trough a channel of 2.5 km width and a maximum depth of 10 m (Alvarez-Borrego et al. 1975). Tides are mixed-semidiurnal with a range of about 2 m. At low tides, wide stretches of mud and sand flats are exposed.

Density and size distribution: The sampling at the sites was done in the mid- and low-intertidal during spring tide days from September 2002 to February 2003. SBnorth and Sbsouth were sampled at the time of new moon and Sbcontrol to the time of full moon resulting in monthly sampling for each site. 8-16 randomly allocated circles (6 m²) were searched monthly for chocolate clams >30 mm at each site. Specimens <30 mm could not be reliably detected with this method and were thus not considered. To find the clams, the circles were searched for the typically shaped holes made by their siphons and by stepping next to them. Usually, M. squalida would squirt out water when closing the shell, and the clams where then dug out by hand. The number of individuals of M. squalida per circle were counted and the shell length of each clam was determined with callipers from the anterior to the posterior end of their shells to the nearest mm. The average density±standard deviation of M. squalida at each site was calculated by averaging over all replicate samples.

These values were corrected for sampling efficiency that was determined as follows: Six circles were dug out completely with a shovel after the ‘normal’ sampling was completed. The percentage of additional clams found in a circle was calculated as:

P = (100 / (N₁ + N₂)) * N₂

with P = percentage of additional individuals; N₁ = number of individuals per circle, found with ‘normal’ sampling; N₂ = number of additional individuals per circle.

Using the average value (P_av) from the six replicates, the sampling efficiency (SE) was calculated as follows:

SE = 100% - P_av

with SE = sampling efficiency; P_av = average percentage.

Size frequency histograms using length classes of 5 mm were constructed from the length measurements for each site at each sampling date. The average densities of the three sampling sites were compared using an one way ANOVA.

Length-mass relations: A total of 92 specimens were collected during regular sampling at the three different sites and frozen alive at -20 °C. Later, the total weight of the whole organism, weight of the soft parts and the shell separately were determined with an accuracy of 0.01 g. Shell length was measured with callipers with an accuracy of 0.1 mm. Length-total mass relation and length-tissue mass relation were calculated:

with M = mass and L = shell length

Biomass in each sample was calculated by calculating the mass of each individual using the length-mass relations.

Growth: 159 chocolate clams were marked with a scratch code made with an hacksaw. The scratches were coloured with red nail-polish and coated with super glue. The clams were kept in fenced areas (corrals with 2 cm mesh buried about 10-15 cm) of 0.25, 1 and 4 m2 size at the intertidal zone at an unexploited area to prevent escape of the marked clams. Densities in the corrals were higher than natural densities of M. squalida. However, the abundant burrowing clam Chione californensis was excluded from the corrals, thus the total clam density was similar to that found in the field. The shell length was measured monthly using callipers with an accuracy of 0.1 mm. The von Bertalanffy growth equation (VBGE) was used to describe the growth of the clams (Gulland 1988):

L_t = L_∞ (1 – ^{e – (K (t – t0)})

with Lt = length at time t; L_∞ = asymptotic length; K = growth constant; t₀ = age at length 0 (considered as zero).

To calculate the parameters of the VBGE, the Munro plot was used (Munro 1982):

K = ln(L_∞ – L₁) ln(L_∞ – L₂) / (t₂ – t₁).

with K = growth constant; L_∞ = asymptotic length; L₁ = length at tagging; L₂ = length at recapture; t₂ – t₁ = time interval between tagging and recapture.

This plot requires a fixed input-value for ‘L_∞’. It leads to individual daily ‘K’-values for each specimen. The ‘L_∞’ was selected which minimized the variance around the mean ‘K’-value. The values obtained were multiplied with 365 to obtain the annual growth constants ‘K’. To compare the growth constants of different length classes at different months, the average ‘K’-values of length class-groups of 10 mm (beginning with the class 0-9.9 mm) at every month were calculated. In addition, the average ‘K’-value of all measurements was determined and a growth curve was calculated. All calculations were done using the computer program FISAT II (Gayanilo et al. 1994).

φ = log10 K + 2 * log10 L_∞

with K = growth constant and L∞ = asymptotic length.

Mortality: To calculate the instantaneous annual mortality rate ‘Z’ the length converted catch curve was applied to the pooled length frequency data using the estimated growth parameters from the tagging experiment. The calculation was done with the program FISAT II. ‘Z’ corresponds to the negative slope of the linear regression of the descending arm of the catch curve (Gayanilo et al. 1994):

ln(N_i/ ∆t_i) = a + b * t_i

with N = number of specimens in length class i; ∆t = time needed for the clam to grow trough length class i; T = relative age (computed with t₀ = 0) corresponding to the midlength of class i; b = estimate of Z. ‘Z’ was calculated for each site and for the complete data set.

Vertical zonation: At each sampling site, transects were sampled perpendicular to the shoreline. The seaward mangrove edge was chosen as a starting point. Beginning at this point, every 20 m three sampling circles (6 m2) were searched for specimen of M. squalida (see above) down to the water line at low tide. The mean lengths of the clams at the different transects (20, 40, 60 and 80 m) were compared using one way ANOVA.

Migration: 25 clams were tagged as described above and released close to a marked starting point in the mid-low intertidal. After 69 and 143 days, the area around the release point was searched for marked clams and their distance and direction from the release mark was measured.

Monitoring environmental conditions: Throughout the study period, oxygen, temperature and turbidity were measured. Dissolved oxygen content of the water was measured twice every week using Winkler-titration at the time of sunrise and sunset. The samples were taken at the water line near SBcontrol. Morning and evening values were averaged to a mean daily value. For longterm observation of the sediment temperature in °C, a data-logger (Tidbittm) was dug into the sediment near the corrals. The temperature of the bottom water was measured in the subtidal with a second data-logger. The data were analysed with the program Boxcar 6.0. The turbidity of the water (using a Secchi disc) was measured monthly in the subtidal.

Qualitative assessment of fisheries by interviews: To obtain information about the fishery of M. squalida, some randomly selected fishing grounds near the town of Puerto San Carlos (Fig. 1) were observed and people operating here were interviewed about their capture methods, the size and amounts of their catch and market issues (Table 1).

Results

Densities and size distribution: The sampling efficiency obtained during regular sampling was about 68 % and densities were corrected accordingly using a factor of 1.47. Average density at the exploited site SBnorth (2.45±1.18 ind/m²) was significantly higher (one way ANOVA, p = 0.009) than at SBcontrol (1.84±1.35 ind/m²) while SBsouth (1.81±1.61 ind/m²) did not differ from the control site (p = 0.923). SBnorth and SBsouth differed significantly (p = 0.017). Total average density from all sites was 2.01±1.41 ind/m². Individual samples varied between 0 and 6.13 ind/m² (Table 2). The length frequency histograms (Fig. 2) show two cohorts at each sampling site with a modal progression of the small cohort over the sampling period.

Length-mass relations: The length-total mass and length-tissue mass relations are shown in Fig. 3. Biomass of clams with different shell lengths calculated with these equations are given in Table 3 and refer to the population biomass.

Growth: Clams larger than 60 mm showed very little or no growth at all. The parameters K and L_∞ derived from the tagging data of clams smaller or equal 60 mm were 0.655±0.367 and 83 mm respectively. The growth performance index derived from these values was φ = 3.654. As seen in Fig. 4, K-values varied for different length groups and also temporally, between 0 and 1.741. Since the capacity of the Munro-routine of FISAT II was limited, 178 tagging data were chosen randomly and a semi-quantative growth curve was calculated (Fig. 5).

Mortality: Using K = 0.655 and L_∞ = 83 mm obtained from tagging data the mortality rate ‘Z’ at the unexploited site SBcontrol was 2.18 y^-1 (confidence interval CI = 1.53-2.82). The exploited sites SBnorth and SBsouth show lower mortality rates (SBnorth Z = 1.38 y^-1 (0.30-2.46), SBsouth Z = 1.71 y^-1 (-0.54-3.96)). The value for ‘Z’ of the pooled data for all sampling sites is 1.61 y^-1 (CI = 1.37-1.85).

Vertical zonation: The box plots (Fig. 6) show an increase of mean length with increasing distance to the starting point. An ANOVA shows significant differences between the 40 and 60 m transects at SBcontrol (p = 0.002), at SBnorth between 40 and 80 m (p = 0.003) and 60 and 80 m (p = 0.0006) and at Sbsouth between 40 and 60 m (p = 0.016) and 60 and 80 m (p = 0.009).

Environmental conditions: The dissolved oxygen ranged between 3.95 mg/ml in August 2002 and 7.50 mg/ml in December 2002 (Fig. 4A). The temperature of the sediment and the bottom water were almost identical. As there was more data available on the bottom water temperature, this data was considered. A maximum was reached at the end of September (30.3 °C) and a minimum at the end of December (17.7 °C). Average temperature of the sampling period was 24.3 °C. Secchi depth increased over the study period from 2 m to more than 5 m.

Qualitative assessment of fisheries by interviews: 11 fishermen were interviewed. Two of them were professional chocolate clam fishermen who depend exclusively on the M. squalida fishery. Their fishing grounds are located in the channel in front of Puerto San Carlos. The size limit for chocolate clams is 60 mm shell length. The clams are collected by Hooka diving with the help of a co-worker in shallow water depths, bigger clams (up to 135 mm) are generally found in deeper waters (up to 10 m). There they find six clams per m² on average. Observations of the fishermen show that bigger clams appear in coarse sediments whereas smaller ones seem to prefer fine sand. One of the fishermen was fishing six days of the week for chocolate clams. Up to 900 individuals with an average size of 99 mm were caught per day and sold directly in Puerto San Carlos or on the regional or national market.

The recreational fishery of M. squalida is common in Puerto San Carlos. Seven of nine interviewed people search chocolate clams; five of them every two weeks at the time of spring low tides. In total, four different collecting sites were named: Estero San Buto, La Curva near San Carlos, Banderitas (another mangrove channel) and the sandflat in front of the boating ramp of San Carlos. They collect 50-200 clams per catch of an average length of 60 mm, which are used exclusively for private consumption. Just one of the fishermen claimed to find less clams than before, the other persons did not observe a decline of the of the M. squalida population.

The average densities of M. squalida at the three sampling sites with 1.81-2.45 ind/m² were similar to densities found in Bahía Loreto by Gutiérres-Barreras et al. (1998) with 1-3 ind/m². The distribution of M. squalida in San Buto was patchy, with 0-6.13 ind/m². High patchiness was also found in other studies (Baqueiro-Cárdenas and Stuardo 1977, Baqueiro-Cárdenas et al. 1982) who recorded chocolate clam densities from 0.04-10 ind/m² at different sites in Baja California and seems to be the rule in M. squalida. Several factors might explain this high patchiness:

1. Baqueiro-Cárdenas (1979) studied the distribution of M. squalida, M. aurantiaca and Dosinia ponderosa in relation to the grain size of the sediment. M. squalida was found in coarse to fine sand and its relative abundance decreased in coarse sand. García-Domínguez (1991) observed that the distribution of Chione californiensis, which is often found in assemblage with M. squalida, is also determined by the type of substrate. The grain size could influence the burrowing rate of the chocolate clam which has been observed for other bivalves (Alexander et al. 1993, Nel et al. 2001) and could thereby influence the ability of M. squalida to evade its predators or to reach the sediment surface after burial by storm deposits or by tidal sedimentation. In addition, the substrate selectivity off settling larvae could play a role (Alexander et al. 1993). It was shown by Norkko et al. (2001) that several juvenile bivalves (0.5-4 mm length) dispersed over scales of meters within one tidal cycle. Nothing is known about dispersal of juvenile specimens of M. squalida but adult chocolate clams are able to move several decimeters in a few months as was observed in the migration experiment of this study.

2. Intraspecific competition could also be influencing the distribution of M. squalida and may explain the high patchiness. Adults could filter passively settling larvae and therefore inhibit settlement and subsequent recruitment (Defeo 1996, Brazeiro and Defeo 1999). The density of adults could also limit the survival of settled juveniles as they are not able to compete for food with the same efficiency as the adults (Searcy-Bernal and Juárez-Romero 1991).

3. Patchy occurrence of predators could lead to patchy distributions of M. squalida on a very small scale.

The length-total mass relation of M. squalida was different from that found by Singh-Cabanillas et al. (1991) in the bay of La Paz whereas length-tissue mass relation was similar. As seen in Table 3, total weight of a chocolate clam of 50 mm length would be 23.78 g (tissue mass 8.18 g) in this study. After the length-mass relation found by Singh-Cabanillas et al. (1991), it would be 39.42 g (tissue mass 9.55 g). These differences might be explained by different methods. Singh-Cabanillas et al. (1991), did not freeze specimens of M. squalida before weighing. This might have led to a higher proportion of water in the clams resulting in higher total mass than found in clams of the recent study. In addition, high variation of individual length-mass ratio could have an influence. In this study, variations in mass of more than 30 % were found in clams of the same length.

Sampling of transects showed a general trend to larger chocolate clams in deeper water (Fig. 6). Though no transects were sampled in the subtidal area, observation of the commercial fishery lead to the conclusion, that average size of M. squalida specimens increases with increasing water depths. Individuals of more than 135 mm could be found in water depths of more than 10 m. It was observed that average size of 163 clams of a commercial catch in deeper water was 107 mm. This phenomenon was also described by Donn (1990) for Donax serra, a sediment-burrowing bivalve inhabiting southern African coasts who observed small individuals high on the shore and larger ones progressively further down. This author suggests that the different zonation patterns were due to a change of behavior/response of clams with increasing size. It could be possible that small individuals prefer the upper intertidal to be better protected against aquatic predators. Larger clams might move to lower tidal levels because they are less vulnerable to predation and conditions for feeding and spawning are better (Bally 1983). The migration experiment of this study confirmed the ability of M. squalida to move and its preference to move in direction of the subtidal zone.

The relatively low L_∞ found in this study at the intertidal and the high L_∞ of chocolate clams at the subtidal area strongly suggest that intertidal and subtidal populations should be considered separately. After small clams of the intertidal zone reach L_∞ of about 83 mm their growth ceases and the clams migrate to the subtidal area, where growth continues due to better food availability and more constant environmental conditions (Fig. 5). Another possible explanation could be settlement of larvae in deeper waters, where specimens reach up to 135 mm due to better conditions. In conclusion, clam size seems to be highly dependent on the habitat and water depth.

The two distinct cohorts in the length frequency histograms may represent two consecutive year classes. According two the growth parameters determined in the tagging experiment, M. squalida is a moderately slow growing species and large individuals (~ 82 mm) may be up to seven years old. Using the average growth parameters L_∞ = 83 mm and K = 0.655, a 50 mm clam would be approximately 1.4 years old, a 70 mm shell 2.8 years. The two distinct peaks shown at the histograms could refer to these age groups. This might be a sign for one main spawning pulse per year. Although M. squalida reproduces throughout the year, one or two periods of increased spawning were usually mentioned in most previous studies. However, reproduction patterns varied between populations at different sites (Baqueiro-Cárdenas and Stuardo 1977, Singh-Cabanillas et al. 1991, Villalejo-Fuerte et al. 1996, Villalejo-Fuerte et al. 2000).

The average K-value = 0.655 and L_∞ = 83 mm (φ = 3.654) obtained with tagging data of this study are similar to the average K = 0.551 and L_∞ = 81 mm (φ = 3.558) found by Castro-Ortiz et al. (1992) in El Remate, Bahía Concepción. These growth parameters differ considerably from K = 0.152 and L_∞ = 86 mm (φ = 3.051) found at a different site in the same study of Castro-Ortiz et al. (1992). The two sampling sites in Bahía Concepción showed different sediment properties and different current velocities. Other studies reported faster growth of M. squalida. While juveniles of 25 mm with K = 0.655 and L_∞ = 83 mm would increase approximately 3 mm per month in Estero San Buto, Baqueiro-Cárdenas and Stuardo (1977) found growth rates of 4.5 mm in these size classes, and Singh-Cabanillas et al. (1991) even 5 mm per month. These studies were conducted in the Bay of La Paz (Gulf of California) and in the south of Mexico (Guerrero), sites with higher annual mean temperatures than San Buto. The growth of M. squalida seems to be highly dependent on geographical differences of parameters such as temperature, sediment properties and currents. It has to be taken into account that densities of M. squalida in the fenced in areas were high (4-20 ind/m², juveniles < 20 mm: 92 ind/m²) which might have negatively influenced the growth of the clams. Still, clam biomass in the corrals was similar to clam biomass in the field as most of other abundant bivalves such as Chione californiensis (densities of about 48 ind/m² found by Castro-Ortiz and García-Domínguez 1993) were removed from the corrals.

Growth of M. squalida was strictly seasonal (Fig. 4b). K-values decreased with decreasing temperature, increasing oxygen content and increasing secchi depth of the water (Fig. 4). The decreasing turbidity observed during the study is a sign for decreasing food availability and might be a limiting factor for filter-feeders such as M. squalida. Since it is a tropical species and found on its northernmost distribution limit, temperature plays an more important role in its development. In conclusion the growth seems to be positively correlated with food availability and temperature. Castro-Ortiz et al. (1992) and Baqueiro-Cárdenas and Stuardo (1977) observed a seasonal growth of M. squalida with highest growth rates in June in Bahía Concepción and Bahía Zihuatanejo. Seasonality could also be observed for other venerid clams like Chione californiensis which can be found associated with M. squalida (Castro-Ortiz and García-Domínguez 1993). Another venerid clam that can be found at the coast of Baja California is Tivela stultorum. This species showed seasonal growth in California populations (Coe and Fitch 1950) but slower winter growth was not observed in T. stultorum inhabiting beaches in Baja California, its southernmost limit of distribution (Searcy-Bernal and Saavreda-Rosas 1988).

A strong individual variation of K-values (Fig. 4) within one population at the same site under the same environmental conditions was observed. K-values varied between 0 and 1.741. Standard deviation of K was very high (K = 0.655±0.367). This phenomenon makes it difficult to predict individual growth and it is necessary to sample a high number of clams throughout the year to obtain more reliable growth parameters.

Total mortality Z was high at all sampling sites (pooled data: 1.61 y^-1). Contrary to our expectations, mortality rate at the exploited sites was lower than at the control site.

Consequently, exploitation must have been too small to be recognizable and the calculated total mortality should equal the natural mortality rate M at the sampling sites in San Buto. The natural mortality M of M. squalida is high in comparison to other bivalves. Venus antiqua showed natural mortality of M = 0.33 y^-1 ((φ = 3.07) in Southern Chile (Clasing et al. 1994)). Similar mortality and growth parameters could be found for Mesodesma mactroides M = 1.64 y^-1 (φ = 3.67) on Uruguayan beaches (Defeo et al. 1992).

Although the recreational fishery at San Buto takes place mostly in summer (May-July) (pers. obs.), its impact on density and size distribution should have been observable in the following months, which was not the case. The exploitation of the sampling sites at San Buto might have been lower in comparison to more heavily exploited areas at other parts of the bay and therefore the impact might have been too small to be recognizable. Another possible explanation could be the early maturity of clams which was observed in individuals of 42 mm length (Villalejo-Fuerte et al. 1996) and the limitation of the fishery to specimens larger than 60 mm, which was also the average shell length of specimens harvested by recreational fishermen. Early maturity and reproduction throughout the year may enable M. squalida to compensate the fishing pressure. Furthermore, sampling efficiency at the intertidal, which is presumably higher than fishing efficiency, was about 68% of clam stock. The remaining clams might be sufficient to keep the intertidal population stable. However, the absence of clear indications of overfishing should not be taken as a proof that the population is in a healthy state, as data was only gathered over a period of six months and the spatial scale was not extensive enough to be able to draw conclusions. Therefore, further studies with a strong emphasis on the fishery of M. squalida in the subtidal should be conducted, as the large specimens play an important role in the commercial fishery.

The authors gratefully acknowledge the financial and logistic support provided by the School for Fieldstudies, Center for Coastal Studies, Puerto San Carlos and the Center for Tropical Marine Ecology (ZMT), Bremen. Special thanks go to Marc H. Taylor for his help and advice in fieldwork.

Se estudió la dinámica poblacional de la almeja Megapitaria squalida de setiembre 2002 a febrero 2003 en Bahía Magdalena, México. La densidad se determinó en un sitio no explotado y dos sitios explotados utilizando transectos perpendiculares desde la línea costera. También se entrevistó a pescadores locales de diferentes partes de la bahía para obtener información acerca de la pesquería artesanal y recreacional de M. Squalida. La densidad promedio estimada fue de 2.01±1.41 ind/m², sin diferencias significativas entre sitios. La relación de masa y longitud total fue de M_tot = 0.0001*SL^3.1644 (r² = 0.9804, n = 92) y la relación de masa y longitud de tejido fue de M_tis = 0.0002*SL^2.7144 (r² = 0.945, n = 92). Los parámetros de crecimiento Von Bertalanffy se determinaron utilizando marcadores individuales. Hay grandes diferencias en crecimiento tanto interindividuales como estacionales. Los valores anuales promedio fueron: K = 0.655, L_∞ = 83 mm. Debido a que la longitud de la concha puede superar los 135 mm en aguas profundas, es necesario considerar las poblaciones intermareal e inframareal de manera separada. La mortalidad promedio total (Z) fue de 1.61 y^-1. No se calculó la mortalidad de pesca porque la mortalidad total (Z) del sitio no explotado fue mayor que la de sitios explotados. Aparentemente M. squalida migra hacia aguas más profundas al crecer. No se encontró evidencia de que estas poblaciones estén sobreexplotadas.

Palabras clave: Megapitaria squalida, Veneridae, dinámica poblacional, intermareal, Bahía Magdalena, México.

Alexander, R.R., R.J. Stanton & J.R. Dodd. 1993. Influence of sediment grain size on the burrowing of bivalves: correlations with distribution and stratographic persistence of selected neogene clams. Palaios 8: 289-303.        [ Links ]

Alvarez-Borrego, S., L.A. Galindo-Bect & A. Chee-Barragan. 1975. Características Hidroquímicas de Bahía Magdalena, B.C.S. Cien. Mar. 2: 94-109.        [ Links ]

Bally, R. 1983. Intertidal zonation on sandy beaches of the west coast of South Africa. Cah. Biol. Mar. 24: 85-103.        [ Links ]

Baqueiro-Cárdenas, E. 1979. Sobre la distribución de Megapitaria aurantiaca (Sowerby), M. squalida (Sowerby) y Dosinia ponderosa (Gray) en relación a la granulometría del sedimento (Bivalvia: Veneridae): Nota científica. An. Centro Cien. Mar Limnol. UNAM 6: 25-32.        [ Links ]

Baqueiro-Cárdenas, E. & J. Stuardo. 1977. Observaciones sobre la Biología, Ecología y Explotación de Megapitaria aurantiaca (Sowerby, 1831), M. squalida (Sowerby, 1835) y Dosinia ponderosa (Gray, 1838) (Bivalvia: Veneridae) de la Bahiá de Zihuatanejo e Isla Ixtapa, Gro., México. An. Centro Cien. del Mar y Limnol. UNAM 4: 161-208.        [ Links ]

Baqueiro-Cárdenas, E., J.A. Masso R. & H. Guajardo B. 1982. Distribución y abundancia de moluscos de importancia comercial en Baja California Sur. Instituto Nacional de la Pesca, México. Serie de divulgación 11. 32 p.        [ Links ]

Baqueiro-Cárdenas, E. & D. Aldana-Aranda. 2000. A review of reproductive patterns of bivalve mollusks from Mexico. Bull. Mar. Sci. 66: 13-27.        [ Links ]

Brazeiro, A. & O. Defeo. 1999. Effects of harvesting and density dependence on the demography of sandy beach populations: the yellow clam Mesodesma mactroides of Uruguay. Mar. Ecol. Prog. Ser. 182: 127-135.        [ Links ]

Castro-Ortiz, J.L., A. Tripp-Quezada & B. Anguas-Vélez. 1992. Crecimiento de la almeja chocolata Megapitaria squalida (Sowerby, 1835) en Bahía Concepción, Baja California Sur, México. Inv. Mar. CICIMAR 7: 1-7.        [ Links ]

Castro-Ortiz, J.L. & F. García-Domínguez. 1993. Creci-miento de Chione californiensis (Broderip, 1835) (Veneridae) en la Ensenada de La Paz, Baja California Sur, México. Inv. Mar. CICIMAR 8: 45-52.        [ Links ]

Clasing, E., T. Brey, R. Stead, J. Navarro & G. Asencio. 1994. Population dynamics of Venus antiqua (Bivalvia: Veneridae) in the Bahía de Yaldad, Isla de Chiloé, Southern Chile. J. Exp. Mar. Biol. Ecol. 177: 171-186.        [ Links ]

Coe, W.R. & J.E. Fitch. 1950. Population studies, local growth rates and reproduction of the Pismo clam (Tivela stultorum). J. Mar. Res. 9: 188-210.        [ Links ]

Cruz-Agüero, J. de la, F. Galván-Magaña, L.A. Abitia-Cárdenas, J. Rodriguez-Romero & F.J. Gutiérrez-Sánchez. 1994. Systematic List of Marine Fishes from Bahía Magdalena, Baja California Sur (Mexico). Cien. Mar. 20: 17-31.        [ Links ]

Defeo, O. 1996. Recruitment variability in sandy beach macroinfauna: much to learn yet. Rev. Chil. Hist. Nat. 96: 615-613.         [ Links ]

Defeo, O., E. Ortiz & J.C. Castilla. 1992. Growth, mortality and recruitment of the yellow clam Mesodesma mactroides on Uruguayan beaches. Mar. Biol. 114: 429-437.        [ Links ]

Donn, T.E. 1990. Zonation Patterns of Donax serra Röding (Bivalvia: Donacidae) in Southern Africa. J. Coast. Res. 6: 903-911.        [ Links ]

García-Domínguez, F. 1991. Distribución, abundancia, reproducción y fauna asociada de la almeja roñosa, Chione californiensis, en la Ensenada de La Paz, B.C.S., México. Tesis de Maestría, Universidad de Colima, La Paz, Baja California Sur, México. 136 p.        [ Links ]

Gayanilo, F.C., P. Sparre & D. Pauly. 1994. The FAO-ICLARM Stock Assessment Tools (FISAT) user’s guide. Final Draft, FAO, Rome. ICLARM Contr. 1084 p.        [ Links ]

Gulland, J.A. 1988. Fish population dynamics. Wiley & Sons, Chichester, 2. ed., 422 p.        [ Links ]

Keen, A.M. 1971. Sea Shells of Tropical West America. Marine Mollusks from Baja California to Peru. Stanford University, Stanford, California, USA, 1064 p.        [ Links ]

Munro, J.L. 1982. Estimation of the parameters of the von Bertalanffy growth equation from recapture data at variable time intervals. J. Cons. CIEM 40: 199-200.        [ Links ]

Nel, R., A. McLachlan & D.P.E. Winter. 2001. The effect of grain size on the burrowing of two Donax species. J. Exp. Mar. Biol. Ecol. 265: 219-238.        [ Links ]

Norkko, A., V.J. Cummings, S.F. Thrush, J.E. Hewitt & T. Hume. 2001. Local dispersal of juvenile bivalves: implications for sandflat ecology. Mar. Ecol. Prog. Ser. 212: 131-144.        [ Links ]

Pauly, D. & J.L. Munro. 1984. Once more on the comparison of growth in fish and invertebrates. Fishbyte 2: 21.        [ Links ]

Searcy-Bernal, R. & A. Saavreda-Rosas. 1988. Population studies of the pismo clam Tivela stultorum in a beach of Baja California, Mexico. Cien. Mar. 14: 1-14.        [ Links ]

Searcy-Bernal, R. & R. Juárez-Romero. 1991. Length and age structure in commercial catch samples of the pismo clam clam Tivela stultorum (Mawe, 1823), from Playa San Ramon, B.C., Mexico. Cien. Mar. 17: 71-82.        [ Links ]

Singh-Cabanillas, J., J.A. Vélez-Barajas & Ma. del C. Fajardo-Léon. 1991. Estudio poblacional de la almeja chocolata Megapitaria squalida (Sowerby, 1835) en Punta Coyote, Bahía de La Paz, B.C.S., México. Ciencia Pesquera, Inst. Nal. de la Pesca. Serie de Pesca. México 8: 7-22.        [ Links ]

Villalejo-Fuerte, M., G. García-Melgar, R.I. Ochoa-Báez & A. García-Gasca. 1996. Ciclo reproductivo de Megapitaria squalida (Sowerby, 1835) (Bivalvia: Veneridae) en Bahía Concepción, Baja California Sur, México. INPA Boletín Científico 4: 29-39        [ Links ]

Villalejo-Fuerte, M., M. Arellano-Martínez, B.P. Ceballos-Vázquez & F. García-Domínguez. 2000. Ciclo reproduvtivo de la almeja chocolata Megapitaria squalida (Sowerby, 1835) (Bivalvia: Veneridae) en Bahía Juncalito, Golfo de California, México. Hidrobiológica 10: 165-168.        [ Links ]

Internet references

Gutiérrez-Barreras, J.A., M. Maldonado-Diaz, M. Villalejo-Fuerte, M. Mandujano-Herrera & B. Bermúdez-Almada. 1998. Evaluación de la almeja chocolata Megapitaria squalida (Sowerby, 1835) (Bivalvia: Veneridae) en el Parque Nacional Bahía de Loreto, Golfo de California. (Abstract). (Downloaded: September 14, 2002, http://aimac.ens.uabc.mx/aim/conferencias/Biol-Ecol/formatoHTML/lr-041.htm).        [ Links ] ]]> 1993 8 289-303 1975 2 94-109 1983 24 85-103 1979 6 25-32 1977 4 161-208 1982 32 2000 66 13-27 1999 182 127-135 1992 7 1-7 1993 8 45-52 1994 177 171-186 1950 9 188-210 1994 20 17-31 1996 96 615-613 1992 114 429-437 1990 6 903-911 1991 136 1994 1084 1988 2 422 1971 1064 1982 40 199-200 2001 265 219-238 2001 212 131-144 1984 2 21 1988 14 1-14 1991 17 71-82 1991 8 7-22 1996 4 29-39 2000 10 165-168 1998