Although iron is the fourth most abundant element in the Earth's crust, bioavailable iron limits marine primary production in about one third of the ocean. This lack of iron availability has implications in climate change because the removal of carbon dioxide from the atmosphere by phytoplankton requires iron. Using literature values for global fish biomass estimates, and elemental composition data we estimate that fish biota store between 0.7–7×1011 g of iron. Additionally, the global fish population recycles through excretion between 0.4–1.5×1012 g of iron per year, which is of a similar magnitude as major recognized sources of iron (e.g. dust, sediments, ice sheet melting). In terms of biological impact this iron could be superior to dust inputs due to the distributed deposition and to the greater solubility of fecal pellets compared to inorganic minerals. To estimate a loss term due to anthropogenic activity the total commercial catch for 1950 to 2010 was obtained from the Food and Agriculture Organization of the United Nations. Marine catch data were separated by taxa. High and low end values for elemental composition were obtained for each taxonomic category from the literature and used to calculate iron per mass of total harvest over time. The marine commercial catch is estimated to have removed 1–6×109 g of iron in 1950, the lowest values on record. There is an annual increase to 0.7–3×1010 g in 1996, which declines to 0.6–2×1010 g in 2010. While small compared to the total iron terms in the cycle, these could have compounding effects on distribution and concentration patterns globally over time. These storage, recycling, and export terms of biotic iron are not currently included in ocean iron mass balance calculations. These data suggest that fish and anthropogenic activity should be included in global oceanic iron cycles.
Citation: Moreno AR, Haffa ALM (2014) The Impact of Fish and the Commercial Marine Harvest on the Ocean Iron Cycle. PLoS ONE 9(9): e107690. doi:10.1371/journal.pone.0107690
Editor: Erik Sotka, College of Charleston, United States of America
Received: April 9, 2014; Accepted: August 20, 2014; Published: September 24, 2014
Copyright: © 2014 Moreno, Haffa. This is an open-access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited.
Data Availability: The authors confirm that all data underlying the findings are fully available without restriction. All relevant data are within the paper and its Supporting Information files.
Funding: AM was provided a stipend through a Lewis Stokes Alliances for Minority Participation obtained by the California State University, Monterey Bay Undergraduate Research Opportunity Center. This project was supported in part by the National Science Foundation under the California State University-Louis Stokes Alliance for Minority Participation Senior Alliance project (http://uroc.csumb.edu/lsamp National Science Foundation Grant Number: HRD-0802628). Any opinions, findings, and conclusions or recommendations expressed in this material are those of the authors and do not necessarily reflect the views of the National Science Foundation. AH was unfunded. The funders had no role in study design, data collection and analysis, decision to publish, or preparation of the manuscript.
Competing interests: The authors have declared that no competing interests exist.
The oceans provide ecosystem services that may be at risk due to human activity . One service is the sequestration of atmospheric CO2 through photosynthesis, which mitigates climate change. Photosynthesis requires a sufficient supply of iron for the electron transfer mechanisms to proceed; however, in much of the ocean the concentration of iron in the oceans limits primary production –. While iron is abundant on earth, iron concentrations are limited in natural waters by its low solubility .
A biological need for iron is not limited to photosynthetic organisms. It is also required for respiration and nitrogen fixation; thus, most marine organisms concentrate iron in their bodies and cells. Many marine animals including fish, whales, turtles, and sharks have long distance migration patterns to support their mating, feeding, and spawning  that could help to transport iron and other nutrients to high nutrient-low chlorophyll regions of the ocean. It is estimated that the historical killing of baleen whales has removed ∼650 tonnes of iron from the Southern Ocean . There may be compounding effects beyond the immediate removal of the elements contained in heterotrophic organisms from an ecosystem because these species excrete nutrient-containing waste. The feces of the baleen whales was found to have iron concentrations 6 orders of magnitude greater than the surrounding sea water . Some current ocean iron cycles include internal cycling by phytoplankton, but higher trophic levels are not included , , , . The purpose of this study is to estimate the amount of iron stored and recycled by fish, and to determine the amount of iron removed from the ocean due to the commercial marine harvest.
Global estimates of fish total biomass have recently been reported as between 8.99×1011–2.05×1012 kg . Using elemental analysis data for whole fish we estimate that the global marine fish population stores between 0.7–7×1011 g of iron. The fertilizer effect by these organisms is even greater. We estimate that annual iron excretion by living fish ranges from 0.4–1.5×1012 g. Iron recycling by marine mammals and other animals is not included because we found it to be insignificant in comparison to the magnitude of that by bony fishes over the time range in this study. As noted above, historical whaling could be significant over longer time scales, or in some regions of the ocean .
The translocation of iron from the ocean to land due to the commercial marine harvest, which includes species other than fish, is on the order of 1–30×109 g per year (Database S1). Between 1950 and 2010 iron removal was lowest in 1950, reached a peak in 1996 and has declined since (Figure 1). While the marine harvest of iron is small on an annual basis, the export of stored iron integrated over this time range is ∼1×1012 g. The Actinopterygii (ray-finned fish) account for 62–82% of the total high and low estimates respectively (Table 1). Because the true catch data could be even higher our estimates are potentially more conservative than overstated. There have been concerns of under-reporting of fishing data to the UN for all countries except China . Additionally, recreational fishing has estimates as high as 12% of the total commercial catch –, and has increased over the past few decades , yet we do not take it into account due to lack of concrete data. The absolute loss term is compounded by the loss of nutrient cycling by these animals. The potential fecal fertilizer effect lost due to fishing is from 3–6×1010 g/yr.
The chemistry of iron in the ocean is complicated and a detailed analysis of the global ocean iron cycle is beyond the scope of this paper. However, in order to assess the relative magnitude of iron stored in fish biomass and recycled in feces, as well as the marine harvest data it must be compared to estimates for bioavailable iron sinks and sources in the ocean. Currently recognized input, export, and assimilated storage terms include Aeolian dust, ice sheet melting, sediment deposition and upwelling, and plankton assimilation , , –. Bioavailable iron has been calculated as the total aqueous iron and between 1–10% of the colloidal and nanoparticulate iron. Using this calculation Aeolian dust inputs 0.6–2 Tg yr−1, iceberg melting inputs 0.09–0.1 Tg yr−1, and rivers input 0.08–0.09 Tg yr−1.  Recently a report that ice sheet melting provides 0.46–2.71 Tg yr−1 of nanoparticulate iron, of which 1–10% would be considered bioavailable using this calculation. An estimate for loss of iron from the cycle due to particulate iron sinking in the deep sea is 16 +/− 8 Tg yr−1 . Particulate iron has very low solubility (<1–2%) which would limit its bioavailability . The assimilation, and potential recycling into higher trophic levels by phytoplankton is estimated at 0.02–0.7 Tg yr−1. The phytoplankton associated iron and the iron stored in fish (0.07–0.7 Tg) and excreted by them (0.4–1.5 Tg yr−1) is 1.5–2.4 times more bioavailable than FeII, the most bioavailable inorganic form . Furthermore, the solubility and residence time of iron that is complexed with organic ligands is enhanced . Iron from inorganic sources also has low solubility (≤2%) ; thus, transport and fertilization by fish could be a primary driver of marine primary productivity, especially in the high nutrient-low chlorophyll regions of the world. Fecal recycling of iron is roughly the same magnitude as the currently accepted greatest inputs due to sediment recycling and Aeolian dust. The annual loss of iron due to the marine harvest is only about 1% of the total available from inorganic inputs (0.006–.02 Tg yr−1); however, the cumulative removal of iron between 1950–2010 is 1.2×1012 g. A global median reduction of phytoplankton primary production at a similar rate of 1% annually has been observed over the past century.  The authors hypothesized that the reduced primary production was due to increases in sea surface temperature. This is supported by comprehensive studies of the effects of temperature on phytoplankton growth, but there is large variation between and within species.  Given the thermocline within the photic zone and the cooler temperatures within it, the increases in sea surface temperature may not account completely for this reduction in primary production, and it may be useful to include loss of iron due to fishing in future models. The removal of iron due to the commercial marine harvest is either essentially permanent on biological time scales or already included with fluvial or coastal input data as offal or wastewater. The majority of the fish are captured in upwelling zones and coastal areas. However, as fisheries have collapsed the industry has greatly expanded into off-shore  and deeper waters . Thus if a portion of the iron removed via fishing is returned via sewage in riverine inputs, then this may represent a redistribution of iron even if the removal is mitigated by near shore replacement processes.
Most of the iron removed from the ocean is in the form of a complex higher life form at the top of food webs . If iron-enrichment to reduce atmospheric CO2 is effected, or if global climate change causes physical processes to enhance the cycling of iron in regions of the ocean that are currently limited  the iron input will result in increases in primary production, or simple life forms at the bottom of food webs. How long the ocean will take to change from this trophic unsettling is not clear, however, if the longevity of many of the fish being removed is indicative, then it is on the order of decades. We conclude that the addition of marine animals as a biological reservoir and resource of organically-complexed iron, and marine harvest activities to ocean iron cycle models is warranted, and may ultimately lead to a better understanding of changes in biogeochemical processes over time.
Materials and Methods
Estimates for the amount of iron stored in fish tissue as a biological reservoir and recycled in the ocean due to feces
Global estimates of fish abundance have recently been reported as between 8.99×1011–2.05×1012 kg . Elemental analysis data for whole fish was obtained from the literature and used to estimate the amount of iron stored in the global marine fish population (See literature sources in Table 1). Food consumption (Q) by body weight (B) of fish on an annual basis was obtained for all of the species in our list for which it was available (n = 54, Database S1) . The average Q/B was 7.3, which is identical to a previously published estimate of 2% intake per body weight per day . This was multiplied by global estimates of fish biomass  and then by the assimilation efficiency of iron in fish (0.7–1.2%, ). To obtain the most liberal range the low end biomass for both living and harvested fish was multiplied by the highest assimilation efficiency, and the greater biomass estimate with the lowest assimilation efficiency. Next we used these same estimates, but the loss term instead of the assimilation term to consider the fertilizer effect by these organisms. We estimate that annual iron excretion outputs of living fish range from 0.4–1.5×1012 g.
Estimates of the loss term of iron due to the commercial marine harvest
The total commercial marine catch data for 1950 to 2010 was obtained from the Food and Agriculture Organization (FAO) of the United Nations, using FishStat software . Freshwater organisms were excluded, and the data were then separated into the taxonomic categories: Actinopterygii, Algae, Chondrichthyes, Cnidaria, Crustacea, Echinodermata, Invertebrate, Mammalia, Mollusca, Monocot, Myxini, Nemertea, Porifera, Reptilia, and Tunicata (Table 1, Database S1). The database includes 1567 marine species in which the data were reported as mass landed, or brought to shore. For 83 species of mammals the data were reported as quantity caught, not tonnage. For these species high and low end estimates of male and female adult body weight  was used to obtain an estimate of the tonnage. High and low end values for elemental composition were obtained for each taxonomic category from the literature, and used to determine estimates of iron removal due to harvesting of that category (Summary in Table 1, full calculated dataset at Database S1). If the iron content was reported as a percentage of dry matter, then moisture content was used to determine percent iron for wet weights. The highest and lowest estimates for the fish in our database were also used to estimate the stored iron range in the living fish. Applying the same excretion calculations to the bony fish in this database we estimated the amount of recycled iron lost due to commercial fishing activities.
Marine Harvest Calculations and Food Consumption by Teleosts. Commercial marine harvest data from 1950–2010 in tonnes for 1567 non-mammal species (tab 1), low Fe elemental composition for these species and an estimated low end value of Fe in this biomass (tab 2), high Fe elemental composition for these species and an estimated high end value of Fe in this biomass (tab 3), raw data of commercially harvested mammals 1950–2010 (tab 4), mammal harvest data in tonnes for 2 species and in number of animals caught for 83 species, and high and low estimates of Fe in their biomass (tab 5), food consumption data for 54 teleost species (tab 6). Source of raw data was the FAO Fisheries and Aquaculture of the United Nations . Elemental analysis data sources provided in Table 1. Body mass estimates for mammalian species may be found in reference  and food consumption of teleosts in .
Conceived and designed the experiments: AH. Performed the experiments: AH AM. Analyzed the data: AH AM. Contributed reagents/materials/analysis tools: AH AM. Wrote the paper: AH AM.
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