The worldwide effects of ocean acidification (OA) on coral reefs are of growing concern (Doney et al., 2009). Carbon dioxide released into the atmosphere as a result of burning of fossil fuels has not only an effect on “global warming” (Oreskens, 2004). But, also on OA which is called the “other CO2 problem” (Barker & Ridgwell, 2012). OA in combination with high ocean temperatures resulted the last decade in a massive bleaching of coral reefs in the Indian Ocean and throughout Southeast Asia, which is finally lethal (Normille, 2010). Here we discuss the option if we can via innovative seaweed biotechnology—“the Ulva lactuca bioreactor” option (Figure 1) with its H+ ion absorbing capacity (van Ginneken, 2017) and its tremendous green biomass production of around 50 MT/ha/year (Bruhn et al., 2011, van Ginneken & de Vries, 2016)—stabilize our “World Ocean” and protect our coral reefs.
Carbon dioxide (CO2) is an important heat-trapping (greenhouse) gas, which is released through human activities such as deforestation and burning fossil fuels, as well as natural processes such as respiration and causes “global warming” (Oreskens, 2004). Around the millennium time-series measurements of atmospheric O2 and δ13 C showed that the world oceans annually sequestered 2.0 ± 0.6 gigatons (GT) of Carbon between mid-1991 and mid-1997 (Battle et al., 2000). Dissolving CO2 in seawater increases the hydrogen ion (H+) concentration in the ocean, and thus decreases ocean pH, as follows (Raven et al., 2005):
CO2(aq) + H2O ó HCO3− + H+ ó + 2H+ (see Figure 2).
Consequently, an ongoing decrease in the pH of the Earth’s oceans took place until the first decade of the 21st century with an estimated oceanic “acidity” to be around 30% (Hall-Spencer et al., 2008).
So, after the millennium it became clear that the oceans had been during the industrial era acting as a massive sink for anthropogenic CO2 from the atmosphere which is called “the other CO2 problem” (Doney et al., 2009; Barker & Ridgwell, 2012) or “Ocean Acidification” (OA) (Hall-Spencer et al., 2008; Caldeira & Wickett, 2003).
Coral reefs and other marine organisms whose skeletons or shells contain calcium carbonate may be particularly affected, as calcification rates of the Australia’s Great Barrier Reef over the past twenty years indicated (Pennisi, 2009). OA in combination with high ocean temperatures resulted the last decade in a massive bleaching (disturbance of symbiotic balance between the corals and photosynthetic algae) of Coral reefs in the Indian Ocean and throughout Southeast Asia, which is finally lethal (Normille, 2010).
Caldeira & Wickett (2003) placed the rate and magnitude of modern OA changes in the context of probable historical changes during the last 300 million years. Since the industrial revolution began, it is estimated that surface ocean pH has dropped by slightly more than 0.1 units on the logarithmic scale of pH, representing about a 29% increase in H+ (Figure 2). It is expected to drop by a further 0.3 to 0.5 pH units (Mora et al., 2013) (an additional doubling to tripling of today’s post-industrial acid concentrations). By 2100 as the oceans absorb more anthropogenic CO2, the impacts being most severe for coral reefs and the
Figure 1. “Ulva lactuca bioreactor” model which gave annual Ulva lactuca biomass production data of around 50 Mt (metric tonnes) dry weight/ha/year (≈ 365 days) (Source modified: van Ginneken & de Vries, 2016).
Figure 2. The Biophysical process of Ocean Acidification (OA). In theory Seaweed biomass production is severely hampered by a 10,000-fold slower diffusion rate of a Carbon source or Dissolved Inorganic Carbon (DIC) in the biophysical medium water in comparison to terrestrial C3 crops. Despite this detrimental property pelagic seaweeds outcompetes C3 crops for annual green biomass production which is called “the seaweed-paradox” (van Ginneken, 2017). Here we have reported our findings and hypothesized that for four seaweed species that due to an internal acidification the abundant oceanic bicarbonate ion ( ) is introduced into the cell which will in the inner acidic mitochondrial environment (matrix) rapidly be converted to CO2 which is the only C-form photosynthetic enzyme ribulose-1,5-bisphosphate carboxylase/oxygenase (Rubisco) can react with to produce with solar energy and water green biomass. We hypothesize this intracellular acidification is performed by reversal of the fifth pump of the chemi-osmotic model of Mitchell (van Ginneken, 2017). It can be expected that in nearby future seaweeds may play a prominent role in providing the unfettered growth of the world population—estimated at around 10 billion people at the midst of the 21st century: food, fuel and other bioactive ingredients (van Ginneken & de Vries, 2016; Hurd et al., 2014).
Southern Ocean (Raven et al., 2005; Caldeira & Wickett, 2003; Orr et al., 2005). These changes are predicted to accelerate as more anthropogenic CO2 is released to the atmosphere and taken up by the oceans.
In temperate coastal seas, seaweeds are dominant primary producers that create complex habitats and supply energy to higher trophic levels (Hurd et al., 2014). These seaweed communities or seaweed plantations (van Ginneken et al., 2016), can also stabilize the pH of the seawater, thus preventing a further OA.
We hypothesize that due to the sequestering capacity of H+ ions or seaweeds this oceanic crop in theory must be able to prevent ocean acidification (OA) due to H+ ions and that this should be theoretically possible for our “World Ocean”.
Here we will present—based on the H+ ions sequestering ability of seaweeds, which is characteristic for their photosynthetic system (van Ginneken, 2017)— our calculations for land-based systems like the seaweed “Ulva lactuca-bioreactor” (Figure 1), with an annual biomass production of ≈ 50 metric ton/ha/year (Bruhn et al., 2011; van Ginneken & de Vries, 2016).
2. Material & Methods
2.1. Experimental Set Up
The following materials were used in the experiments:
Ulva lactuca (Chlorophyta): ≥ origin: Katse Heule, Easters-Scheldt, The Netherlands; approximate coordinates: 51˚32'30''N and 3˚52'E.
Caulerpa sertularioides (Chlorophyta): ≥ origin: Denpassar, Bali, Indonesia; approximate coordinates: 8˚41'S and 115˚1
Caulerpa cf. brachypus (Chlorophyta): ≥ origin: Cuba): approximate coordinates: 23˚50'S and 82˚50'W.
Undaria pinnatifidia, (Wakame) (Phaeocophycea): ≥ origin, Kilcar, West-Donegal, Ireland, approximate coordinates: 54˚37'N and 8˚37'W.
2.3. Sampling and Purchasing Seaweeds and Identification Procedures
Ulva lactuca was collected ourselves and brought directly to the laboratory— together with surrounding water—for species determination with a binocular and microscope. The other three seaweed species (Caulerpa sertulariodes, Caulerpa cf. brachypus, Undaria pinnatifida) were fresh provided by an aquarium wholesaler for seaweed species “De Jong Marinelife”, Spijk, (The Netherlands) a purchaser for marine aquariums, with a network of international worldwide contacts. This “aquarium-shop” delivers oceanic sea fishes, corals and seaweeds which are flown together with native surrounding water asp to the shop. Here species were identified by name and with a binocular and microscope.
Earlier (van Ginneken, 2017; van Ginneken, 2018; van Ginneken & de Vries, 2018) we determined for four seaweed species under mechanical pressure until 10 bar pressed moisture weight out of the seaweed fronds for further biochemical analysis. All investigated four seaweeds species gave moisture and Oceanic water and seaweed moisture were measured for salinity, pH and by Inductively Coupled Plasma Spectroscopy (ICP)-techniques concentrations for macro-elements: (Ca, Fe, K, Mg, Mn, Na, P, & S), micro-elements ≈ [HM]: (Al, As, Cd, Co, Cr, Cu, Mo, Ni, Pb & Zn) and nutrients (N-total & P-total). With ICP-techniques we investigated it among else for macro- and micro-elements. The [seawater compound X]/[oceanic compound X] ration is a reflection of an inward (uptake) or excretion mechanism over the seaweed cellular membrane which is operative (van Ginneken, 2017; van Ginneken, 2018; van Ginneken & de Vries, 2018).
2.4. Mechanical Pressure Procedure
To be able to press seaweed moisture out of the seaweed biomass the materials were first pulped using a laboratory homogenizer (manufacturer: Foss Tecator, type: Tecator 1094 homogenizer). For seaweed biomass a smooth knife was used, for others a serrated knife was used. For most materials the lower speed of 1500 rpm was sufficient, for other the higher speed of 3000 rpm was needed. Juice was pressed out of the pulp, approximately 100 grams of pulp was used, using a LLOYD INSTRUMENTS (type: LR30K) testing machine that was fitted with a specially constructed unit for pressing pulps at a maximum pressure of 60 bar (Figure 3: Panel 1, 2). Pulps were first pressed for 5 minutes at a pressure of 2 bars, after that for another 5 minutes at a pressure of 10 bars (Figure 3: Panel 3). Applied pressure, thickness of the press cake and cumulative juice production (Figure 3: Panel 4), were continuously monitored. Total weight of press cake and press juice were determined. Afterwards press cake and samples of the obtained seaweed moisture of the four different seaweed species (n = 4 per seaweed species) were immediately stored at −80˚C pending analyses. This procedure was earlier described in (van Ginneken, 2017; van Ginneken, 2018; van Ginneken & de Vries, 2018).
Theoretical data for our Calculations: Our “World Ocean”—with its tremendous amount of 1.37 billion cubic kilometer of saltwater—has since start of the Industrial Revolution act as a sink by sequestering massively per annum 9 Gt CO2 produced by our fossil driven economic (Raven et al., 2005).
Calculations: Of the ≈ 10,000 seaweed species in our oceans (Hurd et al., 2014) ≈ 98% of the worlds cultivated seaweed production consist of the following leading five genera Saccharina, Undaria, Porphyra, Eucheuma/Kappaphycus and Gracilaria which cover 3% of our oceans (Buschmann et al., 2017). So, we allowed us, for these fast-growing pelagic seaweed-species to select two of them, “Sea lettuce” Ulva lactuca and “Asian Kelp” (Undaria pinnatifidia), to make a calculation about the neutralizing capacity of our “World Ocean”.
If we calculate based on the present amount of global seaweed production the H+ sequestering in seaweed biomass we can further calculate how much more seaweed biomass needs to be produced in our oceans to neutralize our “World Ocean”. Recent data indicated seaweeds produce only a small fraction of the global supply of global green biomass below ≈ 30 × 106 fresh weight (FW) ton of
Figure 3. Example of a pressure experiment in the LR30K laboratory press with the seaweed Ulva lactuca.
seaweed, in comparison to ≈ 16 × 1011 ton of terrestrial crops, grasses and forests (Buschmann et al., 2017). In addition, the present global natural seaweed production amounts 30 million tonnes of seaweed (FW) which corresponds to already ≈ 3% surface area of our “World Ocean” (Buschmann et al., 2017), and gives an annual global moisture content of 3.2 × 1011 tonnes seaweed moisture.
In our calculations we used the pre-industrial oceanic pH environmental value of 8.25 (De’ath et al., 2009). Furthermore, we used in our calculations an average Dry Matter (DM) percentage of ≈ 20% for seaweed green biomass (De’ath et al., 2009).
Methods to obtain data for Table 1: we can calculate for these two species the sequestering ability of seaweeds for H+ ions based on the measured pH of seaweed moisture. The measured pH in the seaweed moisture of both seaweed species corresponds to 6.51 (see Table 1).
Following our “calculation-model”, the concentration of H+ ions 10−6.51 = 3.09 × 10−7 mol per litre. The ΔpH due to the H+ ions sequestering photosynthetic mechanism and the pre-industrial oceanic pH environmental value of 8.25 corresponds to ∆pH(8.25 − 6.51) = ∆pH 1.74.
Next, we can calculate the amount of H+ ions in ppm or mmol per liter: ΔpH(8.25 − 6.51) = ΔpH.74 ≥ pH= −log10H+ ó [concentration] ocean/[concentration] seaweed = 10–delta pH [mol/l] ≈ 0.018.
Based on Table 1 we can calculate for both “Sea lettuce” (Ulva lactuca) and “Asian Kelp” how much H+ ions presently with the standing stock of seaweeds
Table 1. Some characteristics for the at 10 bar mechanical pressed seaweed moisture for four seaweed species, Ulva lactuca, Caulerpa sertlatiodes and Caulerpa cf. brachypus and the brown seaweed Undaria pinnatifidia found at different locations like: salinity, nutrients like N & P, and pH value and from this value calculated according to 10pH the amount of H+ ions in (mol/l) was calculated (Raven et al., 2005). While humanity has to shift the 21st century gradually towards a “green” bio-based economy in order to survive. With around 10,000 seaweed species in our oceans we can select the most appropriate species to sequester H+ ions, heavy metals (HM) and nutrients (N & P). B.D.L. = Below detection limit.
are removed. So, the H+ concentration of the seaweed moisture is 50 times higher than that of the ocean.
Based on a realistic model we continue the calculation the amount of hydrogen ions which needs to be removed from our “World Ocean”.
In contrast, the present global natural seaweed production amounts 30 million tonnes of seaweed (FW) which corresponds to already ≈ 3% surface area of our “World Ocean” and gives an annual global moisture content of 3.2 × 1011 tonnes seaweed moisture.
A standing crop of seaweeds on a global scale needs to be removed at once in order to eliminate 50 × 3.2 × 1011 = 16 × 1012 tonnes H+ ions from our “World Ocean”.
So, calculating for our “World Ocean”: according to Equation (1) per mole CO2 two moles H+ are produced so per annum 18 Gt = 1.8 × 1016 mol H+ = 1.084 × 1016 mol H+ ions per volume “World Ocean” needs to be sequestered in order to prevent a further oceanic pH decline.
Briefly, in our “World Ocean” we are aiming to remove around 1.8 × 1016 mol of H+ ions out of 1.37 billion cubic kilometers of saltwater ≥ 1800 × 1014/50 = 36 × 1014 mol H+ in 1.37 billion cubic kilometer of seaweed moisture.
This corresponds to 26.3 × 1014 mol H+ in one billion cubic kilometer of seaweed moisture (giving: 1 km3 = 1,000,000,000 m3), results in 1.0 × 1018 cubic meter.
So, based on an average Dry Matter (DM) percentage of ≈ 20% (see M & M) 1.0 × 1018/40 = in an area covered with “Ulva lactuca bioreactors” of 250 × 1016 ha seaweed production capacity per year needs to be produced and managed in order to eliminate at once all H+ ions which cause OA in our “World Ocean” since the start of the “Industrial Revolution” ≈ 250 years around AD 1870.
From our calculations we concluded an area covered with “Ulva lactuca bioreactors” (Figure 1) of 250 × 1016 ha seaweed production capacity per year is needed in order to eliminate at once all H+ ions which cause OA in our “World Ocean” since the start of the “Industrial Revolution” ≈ 250 years around AD 1870 (Raven et al., 2005).
So, we can conclude this is an unfeasible case and we are aware our calculation may have been too optimistic to immediately aspire to neutralize our “World Ocean” by sequestering all H+ ions at once and removing as waste in a suddenly arising amount of seaweed. It had only the purpose to give the reader a practical look at the sustainability of our “World Ocean” and about the enormous amounts of seaweed and hydrogen ions which are involved. By elucidating the complexity of the causes of OA and the current global state of our “World Ocean” we need to consider:
a) There are estimates that there are still some 10,000 unknown seaweed species in the ocean whose physiological & biochemical properties are unknown with regard to photosynthesis (Hurd et al., 2014), so there might be seaweed species found that grow faster and sequester more H+-ions than Ulva lactuca which also appears from Table 1 where both Caulerpa sp. have a pH of the seaweed juice of ≈ 4.0;
b) Nutrient enrichment negatively affects coral physiology including phytoplankton blooms impose nutrient stress on coral reefs; seaweeds can trap these nutrients (Table 1) avoiding eutrophication (D’Angelo & Wiedenmann, 2014);
d) Heavy metals are toxic to corals—even at very low concentrations—and small amounts of heavy metal pollution even can kill corals. We demonstrated via ICP-techniques in seaweed moisture that seaweeds are champions in sequestering these toxic heavy metals in this way protecting coral reefs (van Ginneken & de Vries, 2018);
e) In addition, it is not exactly known how much actual biomass of seaweeds are in the oceans. A 2008 report suggested that the Island of Orkney (UK) has a Kelp forest of one million tons covering 22,000 hectares along 800 km of coastline (Christiansen, 2008). This equates to 44.5 t of Kelp per hectare. It further suggested that there are approximately 100,000 hectares of Kelp forests in UK waters which could be commercially harvested. Kelp (or Laminaria) is typically found at depths of 8 to 30m in the north Atlantic. Kelps are considered optimal for bioconversion to energy (Milledge et al., 2014). In a study with stable carbon isotopes, (Duggins et al., 1989) demonstrated that Kelp seaweed communities are important CO2 sinks and thus help to prevent global warming.
It appears from all these examples that seaweeds and coral reefs work on the two extremes of an ecosystem. This may also be apparent from a natural coral ecosystem that is naturally volcanic erupted and subsequently overgrown by seaweeds (Enochs et al., 2015).
There are many examples mentioned in this manuscript that indicate that a diligent search is being made for solutions to save our global coral reefs. Perhaps not one direct global solution should be sought, but the sum of all those individual components which can work synergistically is greater than the total sum of the individual parts.
That there is still hope for the recovery of our coral reefs is evident from all these individual initiatives to combat OA. People are increasingly thinking and operating more greener and ecosystems are more protected.
This recovery in the practice of our coral reefs has been proven based on the results from the experiment of (Albright et al., 2016) where it has been demonstrated that if OA is stopped, coral reef calcification is accelerated.
Furthermore, seaweed plantations can act as a natural oceanic sink for anthropogenic CO2 to combat “Global Warming” (Duggins et al., 1989; Barker & Ridgwell, 2012) through giant seaweed farms across the world’s oceans (Figure 4), which would meet the Kyoto Protocol (Laffoley & Grimsditch, 2009).
It seems like a daunting or even an impossible task to build ocean seaweed plantations for the “World Ocean” to prevent OA. But we must remind that since the beginning of the “Industrial Revolution” around AD 1870 over an extremely long period of ≈ 250 years these OA processes are under way. The wry thing about this story is that humanity, through the “laissez-faire” policy of
Figure 4. Futuristic giant seaweed farm in our “World Ocean”.
mainly the baby-tree generation of the previous century, now has to find a solution in barely 30 years (van Ginneken & de Vries, 2015).
This will also require huge economic investments estimated at around 8 trillion US$ (Bishop & Hill, 2014).
But two comments have to be made:
a) The shift towards a bio-based economy does not take place on land but in the eutrophic oceans where the seaweed industry can grow into a truly green biomass creating industry.
b) We should not invest money in rehabilitation projects of dying reefs but tackle the problem at the base. That is a recently observed biological mechanism or H+ sequestering by growing seaweeds.
A major advantage of this crop is that it is itself not affected in its growth by OA but is rather stimulated as indicated by recent studies of (Britton et al., 2016). In assessing the environmental sustainability and combat ocean acidification there is scope to consider the role of seaweed plantations in removing H+ ions from our “World Ocean”. In this way the presently massive and collective “bleaching” of coral reefs can be prevented (Figure 5).
5. Conclusion & Perspectives
This research manuscript gives a reflection of a problem which accumulated in our World Ocean over a time-frame of 250 years but clearly reflects no “natural” solutions are presently available to neutralize our World Ocean at once. But the clear description of this problem in this manuscript itself could be very useful for future studies and techniques for the International Scientific Community to handle this problem and find a new innovative technique/solution to neutralize our “World Ocean”.
The requested area covered with “Ulva lactuca bioreactors” of 250 × 1016 ha seaweed production capacity per year is needed in order to eliminate at once all H+ ions which cause OA in our “World Ocean” is a daunting task. Perhaps finding a solution to the OA problem in this proposed natural way via seaweeds can be accelerated by using improved seaweed species with a larger absorption spectrum of H+ ions. Another solution could be by positioning these
Figure 5. Changes in Aragonite Saturation of the World’s Oceans, 1880-2012. The underlying architecture of the reef is a biogenic carbonate structure responsible for years of active biomineralization by calcifying organisms including corals and algea2. Ocean acidification is a chronic threat to coral reefs by reducing the saturation state of the aragonite mineral, or which coral skeletons are concentrated and reducing the concentration of carbonate ions needed to maintain the carbonate reef. Reduced calcification, combined with increased bioerosion and dissolution, can bring reefs into a state of net loss this century.For more information, visit US EPA’s “Climate Change Indicators in the United States” at www.epa.gov/climatechange/indicators (Source modified: Feeley et al., 2009).
Presently, to preserve our current coral reefs, the OA process needs to be halted. In doing so, we will have to deal temporarily with a range of the under a) up to and including e) mentioned variables (see Discussion) which would justify the protection and rehabilitation of our coral reefs—hopefully supported by synergy—which would strengthen the net effect.
Finally, the power and originality of this manuscript lies in the original, robust and reliable calculations performed by “Biometris”-Institute, Wageningen University, Netherlands (see acknowledgments), by which the problem of OA since the start of the Industrial Revolution starting around 250 years ago clearly has been elucidated for the International Scientific Community.
Dr. GA (Guus) ten Broeke and Prof. Dr. Jaap (J) Molenaar, Department of Plant Sciences, Biometris, Wageningen University, Netherlands, are kindly acknowledged for performing the calculations in this manuscript. The management team of Blue Green Technologies, Jaap van Meerveld, Albert Frans Welmers, Jan Rochard and Hans Lammers is kindly acknowledged for supportive action and kind support.
 Albright, R., Caldeira, L., Hosfelt, J., Kwiatkowski, L., Maclaren, J. K., Caldeira, K. et al. (2016). Reversal of Ocean Acidification Enhances Net Coral Reef Calcification. Nature, 531, 362-365.
 Battle, M., Bender, M. L., Tans, P. P., White, J. W., Ellis, J. T., Conway, T., & Francey, R. J. (2000). Global Carbon Sinks and Their Variability Inferred from Atmospheric O2 and δ13C. Science, 287, 2467-2470.
 Britton, D., Cornwall, C. E., Revill, A. T., Hurd, C. L., & Johnson, C. R. (2016). Ocean Acidification Reverses the Positive Effects of Seawater pH Fluctuations on Growth and Photosynthesis of the Habitat-Forming Kelp, Ecklonia radiata. Scientific Reports, 6, Article No. 26036.
 Bruhn, A., Dahl, J., Nielsen, H. B., Nikolaisen, L., Rasmussen, M. B., Markager, S., Olesen, B., Arias, C., & Jensen, P. D. (2011). Bioenergy Potential of Ulva lactuca: Biomass Yield, Methane Production and Combustion. Bioresource Technology, 102, 2595-2604.
 Buschmann, A. H., Camus, C., Infante, J., Neori, A., Israel, á., Hernández-González, M. C., Pereda, S. V., Gomez-Pinchetti, J. L., Golberg, A., Tadmor-Shalev, N., & Critchley, A. T. (2017). Seaweed Production: Overview of the Global State of Exploitation, Farming and Emerging Research Activity. European Journal of Phycology, 52, 391-406.
 D’Angelo, C., & Wiedenmann, J. (2014). Impact of Nutrient Enrichment on Coral Reef: A New Perspectives and Implications for Coastal Management and Reef Survival. Current Opinion in Environmental Sustainability, 7, 82-93.
 Doney, S. C., Fabry, V. J., Feely, R. A., & Kleypas, J. A. (2009). Ocean Acidification: The Other CO2 Problem. Annual Review of Marine Science, 1, 169-192.
 Duggins, D. O., Simenstad, C. A., & Estes, J. A. (1989). Magnification of Secondary Production by Kelp Detritus in Coastal Marine Ecosystems. Science, 245, 170-173.
 Enochs, I. C., Manzello, D. P., Doham, E. M., Kolodziej, G., Okano, R., Johnston, L., Price, N. N. et al. (2015). Shift from Coral to Macroalgae Dominance on a Volcanically Acidified Reef. Nature Climate Change, 5, 1083-1088.
 Feeley, R. A., Doney, F. S., & Cooley, S. R. (2009). Ocean Acidification: Present Conditions and Future Changes in a High-CO2 World. Oceanography, 22, 36-47.
 Hall-Spencer, J. M., Rodolfo-Metalpa, R., Martin, S., Ransome, E., Fine, M., Turner, S. M., Rowley, S. J., Tedesco, D., & Buia, M. C. (2008). Volcanic Carbon Dioxide Vents Show Ecosystem Effects of Ocean Acidification. Nature, 454, 96-99.
 Hurd, C. L., Harrison, P. J., Bischof, K., & Lobban, C. S. (2014). Seaweed Ecology and Physiology (2nd ed., 551 p.). Cambridge: Cambridge University Press.
 Milledge, J. J., Smith, B., Dyer, P. W., & Harvey, P. (2014). Macroalgae-Derived Biofuel: A Review of Methods of Energy Extraction from Seaweed Biomass. Energies, 7, 7194-7222.
 Mora, C., Wei, C. L., Rollo, A., Amaro, T., Baco, A. R. et al. (2013). Biotic and Human Vulnerability to Projected Changes in Ocean Biogeochemistry over the 21st Centu-ry. PLoS Biology, 11, e1001682.
 Orr, J. C., Fabry, V. J., Amount, O., Yool, A. et al. (2005). Anthropogenic Ocean Acidification over the Twenty-First Century and Its Impact on Calcifying Organisms. Nature, 479, 681-686.
 Raven, J., Caldeira, K., Elderfield, H., Hoegh-Guldberg, O., Liss, P. S., Riebesell, U., Sheperd, J., Turley, C., & Watson, A. (2005). Ocean Acidification Due to Increasing Atmospheric Carbon Dioxide (57 p.). Royal Society Policy Document.
 van Ginneken, V. (2018). Some Mechanisms Seaweeds Employ to Cope with Salinity Stress in the Harsh Euhaline Oceanic Environment. American Journal Plant Sciences, 9, 1191-1211.
 van Ginneken, V., & de Vries, E. (2018). Seaweeds as Biomonitoring System for Heavy Metal (HM) Accumulation and Contamination of Our Oceans. American Journal of Plant Sciences, 9, 1514-1530.
 van Ginneken, V., de Vries, E., & Wijgerde, T. (2016). A Suggested “Seaweed-Plantation Model” to Tackle the Looming Phosphorus Crises in the 21st Century at the Rhine/ North Sea System. Journal of Fisheries Sciences, 9, 105-114.