The ocean is the largest sink of atmospheric CO2 (about 7 petagrams (Pg) per year) (1 Pg = 1 gigaton = 1015 g). Dissolved CO2 (passively entering the ocean via diffusion from the atmosphere) has already acidified the surface ocean, the most productive region of the ocean. Ocean carbon sequestration (OCS) is a method to distribute CO2 more evenly throughout ocean depth and minimize surface ocean impacts. There are two major methods of OCS – direct injection and ocean fertilization (promoting photosynthetic fixation of CO2 by ocean organisms). This chapter focuses only on the direct injection as a method of OCS. This chapter will first describe the physical mechanism by which CO2 can be stored in the ocean water column at depth. It will summarize past ocean direct injection studies, and outline the effects of increased dissolved CO2 and locally increased CO2 partial pressure on marine organisms. It will also include a discussion of the engineering challenges of delivering CO2 to the water column, including the selection of injection sites to minimize CO2 outgassing to the atmosphere as well as minimizing marine life impacts. Finally, this chapter will address the legal, policy and public outreach issues that have ultimately precluded implementation of OCS using direct injection.
1.1. Motivation of Ocean Carbon Sequestration (OCS)
The ocean is presently the largest sink of atmospheric CO2 (about 7 Pg per year) . The Earth’s oceans cover over 70% of the Earth’s surface, and have an average depth of 3,800 m. However, dissolved CO2 is already causing surface ocean acidification (most productive region of ocean) as it equilibrates with the atmospheric CO2. By 1994, the total atmospheric release of anthropogenic (i.e., man-made) carbon was about 244 Pg of carbon (PgC) from fossil fuel combustion, and about 140 PgC from land use change (e.g., deforestation) . The oceans have absorbed about one-third of anthropogenic CO2 (the atmosphere retained about 43%, while the oceans absorbed about 30%), leading to a decrease of surface-ocean total pH by about 0.1 units from about 8.2 to 8.1. If CO2 emissions continue unabated the subsurface ocean total could decline by 0.7 units by 2300. To place in a geological perspective, the surface ocean pH (on a total scale) has not been below 8.1 during the past 2.1 million years. The total addition of carbon into the atmosphere is expected to be about 5000 PgC – the estimated fossil fuel reserves excluding hydrates -- in the next 500 years. This is a higher rate of carbon addition than ever experienced by the earth over a short geological time scale .
At the same time the ocean pH in the deep ocean has been decreasing at a relatively slower rate compared with the surface ocean [1, 4]. Rising concentrations of greenhouse gases in the atmosphere are implicated in adverse climate changes and two-thirds of the change is attributed to CO2 . Ocean carbon sequestration was conceived as a method to distribute CO2 more evenly throughout the ocean column, especially into deep ocean waters, and minimize surface ocean impacts while the ocean CO2 levels equilibrate with the atmosphere.
There are two major methods of OCS – direct injection and ocean fertilization (promoting photosynthetic fixation of CO2 by ocean organisms). This chapter focuses only on the direct injection of CO2.
2. Physical description of direct injection
2.1. Physical properties of ocean/CO2 system
The conditions under which CO2 can exist in a gas, liquid, solid or hydrate, and aqueous phases are depicted in the phase diagram (see Figure 1)  At typical ocean temperatures and pressures, CO2 exists as a gas above 500 m depth, and a liquid below this depth. Between 500 and 2700 m depth, liquid CO2 is less dense than seawater and would float, while below 2700 m CO2 is denser than seawater and would sink. A solid CO2 hydrate phase is thermodynamically stable in the ocean at low temperatures; CO2 hydrates are discussed in Section 2.3.
2.1.1. Solubility of CO2 in the ocean
CO2 dissolves in ambient seawater that is not saturated with CO2. Once dissolved, aqueous CO2 exists in various charged forms in water according to these main reactions, known as the carbonate system :
The total dissolved inorganic carbon (CT) is defined as:
The result of this is that increasing dissolved CO2 will shift the equilibria (1) and (2) above to the right, and lower the local pH of the ambient seawater. . At a typical surface seawater water pH of 8.2, the equilibrium (3) is shifted to the left with the addition of CO2. The net result of an increase in dissolved CO2 is the decrease of pH, an increase in HCO3- and a decrease of CO32- (Figure 2).
In turn, the dissolved CO2 causes an increase of the density of the seawater via the solute density effect  that has implications for the physical design of a direct injection of CO2 into the ocean.
2.1.2. CO2 partial pressure (pCO2)
The partial pressure of CO2 of a sample of water, denoted by pCO2, is the pressure of gaseous CO2 which, if allowed to equilibrate with water, will result in the same amount of dissolved CO2 as observed in the sample. It is related to the solubility of CO2, Cs, and the concentration of H2CO3(aq) by the following:
where Cs(T,S) (usually expressed in μatm) is dependent on the local temperature T and salinity  provide empirical relations to obtain Cs.
As the atmospheric CO2 concentration increases, pCO2 levels increase in the surface ocean as it equilibrates with the atmosphere. The ratio of the relative change in pCO2 to the relative change in CT is known as the Revelle factor, and is inversely proportional to [CO32-]. The inverse of the Revelle factor is also often termed as the buffering capacity of the ocean. According to this relation, a doubling in atmospheric CO2 would only increase the total dissolved CO2 by about 10%. 
While sea-air equilibria for most gases like oxygen occur over a time scale of days, it can take ~8 months for CO2 to reach equilibrium at the surface, because the dissolved CO2 in the carbonate system does not remain a dissolved gas but instead causes an increase in HCO3-. .
2.1.3. Calcium carbonate saturation state of seawater
The CaCO3 saturation state of seawater is defined as Ω:
where [Ca2+] and [CO32-] are the seawater concentrations of Ca2+ and CO32-, and Ksp is the solubility product of either calcite or aragonite (the two major forms of CaCO3). If Ω for aragonite (Ωa) for instance is greater than 1, then aragonite is supersaturated and solid aragonite would begin to precipitate; if Ωa drops to below 1 then aragonite is undersaturated with respect to the ambient ocean and solid aragonite would begin to dissolve. Because Ksp increases with pressure, for both aragonite and calcite there is a transition of the saturation state from Ω > 1 to Ω < 1 sediments with depth . The depth at which Ω = 1 for a mineral is known as its saturation horizon.
2.2. Methods of direct injection
CO2 sequestration first involves capture from their sources, of which one major type of the coal-fired power plant. The CO2 emissions are relatively pure from coal-fired power plants and could be isolated and injected into the ocean. A typical 500 MW power plant produces about 130 kg/s of CO2. . After CO2 capture, the CO2 would be transported to the ocean via a pipe or ship to the ocean for direct injection. Technologies for CO2 direct injection include: Liquid CO2 droplets ; CO2 laden seawater [9,14,15]; Solid CO2 (dry ice) [16,17]; and CO2 lake formation (See Figure 3)
2.3. CO2 hydrates
As shown in Figure 1, at lower temperatures (below about 5 - 10 degrees C) and at high pressure (corresponding to an ocean depth of about 400 m or greater) solid CO2 hydrates are thermodynamically stable. CO2 hydrates consist of molecules of CO2 inside a cage-like structure of hydrogen-bonded water molecules . They are of interest as a possible vehicle for deeper ocean carbon sequestration, because they are denser than seawater, and will sink unaided while dissolving to promote dispersion in the ocean. Pure hydrate particles are difficult to produce, but the Oak Ridge National Laboratory (ORNL) has designed a continuous CO2-seawater co-flowing injector to create cylindrical composite particles comprised of CO2 hydrate (negatively buoyant), liquid CO2 (slightly positively buoyant at 1000-1500 m depths) and seawater .
Although CO2 hydrates are thermodynamically stable, they will dissolve in ambient seawater upon release, because CO2 is under-saturated in the ambient water. Field and laboratory observations confirmed that both pure hydrates and partially reacted cylindrical composite particles dissolved in the ambient seawater [20,21,23].
2.4. CO2 droplet and hydrate studies
Numerical efforts to simulate the behaviour of CO2 droplet plumes have included solving the full three dimensional Navier-Stokes equations in quiescent ambient sea conditions [7,22,24]. Bubble plume models calibrated using laboratory observations have also been applied to CO2 droplet releases [25-27].
Field tests were conducted using CO2 hydrate composite injectors [23,28]. The latest survey, with a hydrate reactor located at an ocean depth of ~1500 m, produced curved negatively buoyant cylindrical particles with diameters ~2.2 cm and lengths up to ~1 m. Applying a drag coefficient model to observed initial settling velocities and dissolution rates during the most recent survey [29,30], the hydrate conversion efficiency (percentage of liquid CO2 converted to hydrate) in the field was ~ 15-20% resulting in particles with specific gravity 1-2% greater than seawater, which lead them to sink to a depth below discharge of roughly 100 m. Greater sinking could be achieved using larger particles. Discharging particles with a range of sizes and densities (reflecting different conversion rates) would cause differential settling resulting in spreading in the down-current and vertical directions. Furthermore, towing the source from a moving ship would contribute additional dispersion .
An alternative approach to enhancing mixing and vertical descent is to release a continuous stream of particles, forming a dense plume which would sink both due to the density of the particles as well as the increased density of seawater containing dissolved CO2. An integral double plume model [25,29,31] was used to simulate the behavior of continuous streams of composite particles released to a quiescent ocean, with typical ambient stratification, at CO2 loadings of 0.01 to 1000 kg/s. Results showed that, for a CO2 release of 100 kg/s (roughly the emission from a 500 MW coal-fired power plant), a plume composed of 2.2 cm diameter composite particles with 16% reaction efficiency would sink about 1000 m, approximately 10 times the individual particle sinking depth. A plume composed of similar particles, but with a diameter of 5 cm, would sink about 2000 m (~5 times the individual particle depth), while plumes composed of larger particles, or particles exhibiting higher reaction efficiency, would reach the seafloor (as would the individual particles).
Two ambient effects reduce the performance of a plume: stratification and ocean currents. Plume sinking is hampered by strong ambient stratification which causes trapping of entrained seawater at intermediate depths below release. Density stratification weakens at depths below 1500 m , so from the perspective of reduction of plume trapping, regions of the ocean deeper than 1500 m are potentially favourable for depositing CO2 .
3. Environmental impacts/challenges
Some of the concepts relevant to the impacts of OCS by direct injection (e.g. ocean acidification) are presented in this section. The reader is directed to [1,11] for a more detailed and comprehensive summary of the causes and effects of ocean acidification.
3.1. Long term stability of dissolved CO2 in the ocean
Investigations and estimation of the long term stability is described in greater detail in . Numerical ocean models indicate that placing CO2 in the deep ocean would isolate most of the CO2 from the atmosphere for several centuries, but over longer times the ocean and atmosphere would equilibrate.
Relative to direct atmospheric release, direct injection of CO2 into the ocean could reduce the rise and peak of atmospheric CO2 levels over the next several centuries. After several centuries, the CO2 released in the ocean would be transported back to the ocean surface and interact with the atmosphere again. However, in the new equilibrium, most (66% to 85%) of the injected CO2 would still remain in the ocean despite contacting the atmosphere .
Generally, carbon injected in the deep ocean would equilibrate with the atmosphere over a time scale of 300 to 1000 years, based on radiocarbon and other tracer dating to estimate the age of the deep seawater. The estimated age of the North Pacific deep water is 700 – 1000 years, while the North Atlantic deep water is estimated to be only about 300 years old. A large number of numerical three dimensional ocean general circulation models were used to study CO2 retention. The models generally predict a higher retention time with a deeper injection depth (isolation of CO2 from the atmosphere is nearly complete for 100 years with an injection depth of 3000 m). Consistent with the radioactive tracer dating, many of the models suggest that the Pacific Ocean would retain a larger fraction than the Atlantic Ocean. However, the models vary greatly in their predictions on the actual time taken for CO2 injected at a particular site to once again make contact with the atmosphere [1, 34].
Additionally, other geochemical factors may affect these predictions. For example, a higher ocean temperature, as well as a higher dissolved inorganic carbon concentration may lead to a lower efficiency for the ocean to absorb additional CO2. (See ).
3.2. Potential pH and carbonate system changes from added CO2
As described in Section 2.1, ocean acidification has been occurring since the Industrial Revolution. This section describes the effect of continued ocean acidification on the ocean’s carbon cycle and marine ecosystems. Between 1991 and 2006, North Pacific ocean pHT showed a decrease of 0.06 units over the upper 500 m of ocean. In the Iceland Sea, the trend of pHT decrease between 1985 and 2008 in the surface ocean was 0.0024 units per year, with a corresponding decrease in Ωa of 0.0117 units per year. The decline in pHT below 1,500 m in the Iceland Sea was one-quarter of that on the surface, with a corresponding decrease in Ωa at 0.0009 units per year .
Another consequence of the increased dissolved CO2 in the ocean, as described in Section 2.1.1, is the increase of HCO3- and a decrease of CO32- in the ocean. The decreased CO32-in turn leads to the decrease of the local value of Ω in the ocean. As there is a transition from saturation to undersaturation from Ω = 1, this means that the saturation horizons for both aragonite and calcite would both become less deep with time . The decrease in Ωa caused the aragonite saturation horizon (ASH), the interface between supersaturated waters above and undersaturated waters below, to rise (shoal) at a rate of 4 m per year. The decrease in Ω, and therefore the shoaling rate for the ASH, is predicted to be more pronounced near the poles, and more severe in the Arctic Ocean than the Southern Ocean, partly because the polar oceans have lower initial concentrations of CO32- .
It was proposed  that the addition of CO2 followed by global increase in surface temperature can be compared to that which occurred during the Paleocene-Eocene Thermal Maximum (PETM, ~55 million years ago). During PETM, about 3000 PgC was added to the over an estimated 6000 years. However, the current estimate for expected total anthropogenic carbon addition is a larger rate of carbon input over a shorter period of time, about 5000 PgC over about ~500 years. The next highest global carbon addition was experienced by the earth during the Paleocene-Eocene Thermal Maximum, (~55 million years ago) where about 3000 PgC was added over ~6000 years. During the PETM, the effects of ocean acidification on surface calcifying organisms was limited, but the conditions of the PETM were not identical to the predicted future scenario, notably in that the carbon input rate was still much slower than the modern anthropogenic carbon addition. Nevertheless, studies of the PETM may inform future predictions of the behavior of ocean marine life with a large increase of atmospheric CO2. [3,4].
3.3. Effect of pCO2 increase on organisms
At acute levels CO2 has a narcotic effect on animals and causes respiratory distress and death. The work of [37 – 41] that model the lowered pH on passive marine organisms such as zooplankton that spend varying times in and out of a CO2 plume, and found that minimizing the local dissolved CO2 and pH drops will reduce the mortality rate.
Non-lethal effects have also been observed due to hypercapnia (elevated CO2 exposure) [42-44]. Tamburri et al.  have observed the narcotic effects of increased CO2 levels on mobile deep sea animals in the field; they also observe that while many tend to avoid CO2 plumes, some may risk the narcotic effects to obtain food. They note  that increased partial pressure of carbon dioxide will also have a detrimental effect on marine organisms, such as causing slow respiratory distress and inducing a narcotic effect on fish. Passive marine animals may experience depressed ion exchange capability and metabolism when exposed to lower, chronic levels CO2. Some studies also show slowed growth in mussels and corals, as well as developmental effects on some marine larvae and eggs (brittle stars and bivalves) .
The primary effect of acidified seawater exposure by organisms is acidosis, the decrease of pH in body fluids. Intracellular and extracellular processes have been shown to be disrupted when seawater pH drops to a range of about 6.0 – 7.8. Many marine animals counter acidosis by increasing bicarbonate ion production (e.g. in the gills) . Barry et al. report that organisms that have weaker control of their internal fluid chemistry, and that rely on passive molecular diffusion for gas exchange such as sponges, echinoderms, may have greater sensitivity to ocean acidification .
Some organisms may adapt to hypercapnia (elevated CO2) better than others . For example, tropical fishes, as they live closer to the edge of oxygen limitation than temperate fishes, may make them more sensitive to the combined effects of ocean temperature and ocean acidification than their temperate counterparts. For example, studies on acutely exposed tropical cardinal fishes to 1 week of pCO2 of 1000 μatm resulted in decreases of aerobic scope and critical swimming speeds by about 40 – 50%, but a similar study conducted for Atlantic cod after 12 months of exposure to both 3000 and 6000 μatm did not result in any significant change in swimming capacity.
High CO2 levels (up to a pCO2 of 16,000 ppm  have also been observed in ocean bottom waters and marine sediments where there are high rates organic matter oxidation and low rates of mixing with the overlying seawater. Under these conditions, high CO2 concentrations are often accompanied by low O2 concentrations. Near the surface at night, respiratory fluxes in some relatively confined rock pools of the intertidal zone can produce high CO2 levels. . Portner et al.  report that high pCO2 is found in oxygen minimum layers. They report that elevated pCO2 is linked to acid-base regulation and respiration in fish. However, they also report that coastal and mid-water animals (both pelagic and benthic) regularly experience a large range of pCO2 values (500 to 9400 μatm) in estuaries . “These patterns suggest that in some environments, organisms have evolved to tolerate relatively wide pH oscillations and/or low pH values.” 
Organisms such as the Humboldt squid, although thought not to be able to adapt physiologically to future changes to the oceans oxygen balance, have been observed to thrive in oxygen minimum layers which tend to have low pH and are undersaturated with respect to calcium carbonates .
Deep sea ecosystems depend on sinking particles of organic carbon, made by photosynthesis near the ocean, settling down through the water. Most species living in the deep sea display very low metabolic rates [48, 49], especially in oxygen minimum layers . Organisms living in the deep seawaters have adapted to the energy limited environment by conserving energy stores and minimizing energy turnover. Turley et al. also suggest the depletion of oxygen as a contributing factor to the increased prevalence of harmful algal blooms, though the link between anthropogenic CO2 and algal blooms remains controversial .
Finally, as many marine organisms synthesize and depend on calcium carbonate structures (e.g. shells), the implication of a lowered CO32- and Ω in the ocean is the potential for reduction of their habitats.
As a guide,  uses a pH drop of 0.1 units as the threshold pH drop for insignificant marine life impact; it is also within the observed natural variability in the ocean. The US Environmental Protection Agency proposed that the threshold for open waters at depths greater than the euphotic zone, the pH value should not drop more than 0.2 pH units outside the range of natural variation .  shows that some theoretically modeled scenarios of carbon dioxide releases (for example, releasing sinking CO2 hydrates from a fixed or moving source at 1,500 m, injecting 10 to 1000 kg/s) would result in local pH drops within this guideline threshold in the vicinity of the release point. Others (e.g. Rockstrom et al.) have introduced the concept of planetary boundaries, and for CO2 they have proposed a threshold carbonate ion concentration. As a first estimate, they proposed that the oceanic aragonite saturation state Ωa be maintained at 80% or higher of the average global pre-industrial surface seawater level of 3.44 . As with , these planetary boundaries are guides for a sustainable global environment, and (with the exception of the US Environmental Protection Agency for pH) have not been implemented as a regulatory threshold.
3.3.1. Comparison with naturally occurring ocean CO2 vents
In the ocean, hydrothermal vents are submarine volcanic structures that act as natural sources of CO2 in the ocean. These have been observed as potential natural analogues of OCS direct injection points. Field observations of hydrothermal vents have shown large fluctuations of pCO2 (up to 80,000 ppm), over 100 times that observed in typical deep seawater). Over time, the vents have sustained organisms that are specially adapted to living in elevated pCO2 conditions .
Observations near hydrothermal vents have shown that ocean acidification reduced biodiversity below a mean pHT of 7.8 . While Echinoderms are notably absent from habitats with naturally high CO2 levels such as hydrothermal vents and shallow CO2 vents off the coast of Italy , sponges appeared to tolerate these same sites.
As observed in , “[h]owever, while commonly the literature contains results of short term studies of organism physiology and survival, they may not be indicative of eventual long term consequences of ocean acidification.”
4. Engineering feasibility/challenges
4.1. Site selection for injection
As described in [1,54], to date there are no publications dedicated to site selection for direct ocean injection. Although numerical models have predicted CO2 retention time as a function of the injection location, they have not consistently agreed on any individual location for direct injection. The only agreement appeared to be that a larger depth of injection would result in a longer isolation of CO2 from the atmosphere . In contrast,  presented a study of site selection for deep sea geological storage, highlighting the potential of storage in basalt aquifers along particular seismic and aseismic oceanic ridges. This section therefore discusses factors that should be considered site selection criteria based on to be considered when selecting a site for OCS. Environmental goals of site selection include reducing the likelihood of outgassing, and minimizing acute impacts to ocean organisms, as described in Section 3. Additional considerations include the costs of OCS, applicable international policies (such as regulations regarding disposal and cross border transport) – these factors are presented in Sections 4.2 and 4.3.
4.2. Cost of OCS
Costs were estimated for ship transport of liquid CO2 to an injection platform, with CO2 injection from a vertical pipe, or a ship trailing an injection pipe, to water at 3000m . The cost estimate of ocean storage is the sum of three major components: tank storage of CO2 onshore awaiting shipping; the shipping of CO2; and direct injection of CO2 into the ocean (either via an ocean platform, a moving ship, or a pipeline). The estimated sum of the three components (including an assumption of 3% CO2 emissions from boil off and fuel consumption) is 11.9 and 13.2 US$/ton CO2 net stored from shipping to 100 km and 500 km offshore, respectively . Cost estimates presented do not include transport of CO2 onshore.
The cost for transporting CO2 from a power plant located at the shore through a pipeline running on the sea floor to an injection nozzle was also estimated in . CO2 captured from a pulverized coal fired power plant with a net generation capacity of 600 MWe is transported either 100 or 500 km by a CO2 pipeline for injection at a depth of 3000 m at a cost of 6.2 US$/ton CO2 net stored (100 km case) to 31.1 US$/ton CO2 net stored (500 km case). Other technical challenges that may not be accounted for include: residual chemicals, metals, minerals and oils that may be released during drilling activities; and the fact that liquefied CO2 is highly corrosive, requiring that piping for CO2 delivery would require anti-corrosion coatings, which themselves may pose contamination issues .
There are no published cost estimates specific to the production of a CO2 lake on the sea floor; however, given the dominance of pipeline costs, it is reasonable to assume it to be similar to deep water injection. [1,56].
5. Policy issues/challenges
Since offshore OCS is likely to take place in international waters, several international environmental agreements may apply, mainly those that aim to minimize potential risk s to the marine environment. The main international treaties are the Law of the Sea, the London Convention, London Protocol, and the OSPAR Convention. A succinct background of these treaties is taken directly from :
“International marine environment protection was established in 1972 with the London Convention to regulate the dumping of wastes and other matter at sea. In 1982, this ﬁeld was extended through the adoption of the United Nations Convention on the Law of the Seas (UNCLOS). Being an overarching construction, UNCLOS does not contain detailed operative provisions on most maritime issues; rather, it provides a framework for all areas, including marine protection, and allows other, more targeted treaties to ﬁll in the gaps…With regard to marine pollution, global standards are set by the Convention on the Prevention of Marine Pollution by Dumping of Wastes and other Matter, signed in London in 1972 (London Convention). Beneath the London Convention exist several regional agreements that cover speciﬁc areas of the ocean [Also listed in ]. The most widely known of these is OSPAR, the Convention for the Protection of the Marine Environment of the North-East Atlantic. OSPAR is also notable as its regulations on marine pollution are markedly stricter than those of the London Convention, and its decisions are legally as opposed to politically binding on its Contracting Parties.”
5.1. 1996 London protocol
UN Convention on Climate Change encouraged the use of the oceans as a reservoir for CO2, but the UNCLOS (in force since 1994) did not give clear guidance on OCS . With respect to CO2 storage, the original London Convention (with 80 contracting parties, and in force since 1975) only applied to storage by aircraft and vessels and platforms in the water column. As a result, the London Convention did not apply to storage of CO2 in the seabed or the water column itself .
In November 1996, the London Protocol was established that prohibited the disposal of “industrial waste” into international waters. The list of prohibited substances that were categorized as “industrial waste” were contained in Annex I of the London Protocol. However, in 1996 the London Protocol did not give an opinion whether CO2 was categorized as a “waste material generated by manufacturing or processing operations” . The London Protocol entered into force March 2006 .
5.2. OSPAR convention
In 1992, the OSPAR Commission for the Protection of the Marine Environmental of the North-East Atlantic, was formed which unified the 1972 Oslo and 1974 Paris Conventions. It brought together the governments of Belgium, Denmark, Finland, France, Germany, Iceland, Ireland, Luxembourg, the Netherlands, Norway, Portugal, Spain, Sweden, Switzerland and the United Kingdom, together with the European Community (EC). It is considered the most comprehensive and strict legal framework governing the marine environment. As mentioned above, the contracting parties are legally bound to OSPAR’s decisions [57,58].
5.3. 2007 OSPAR amendments for CO2 storage and implications to OCS
In June 2007, the OSPAR issued two amendments to the OSPAR Convention: the first, a decision to prohibit the storage of CO2 streams in the water column or on the sea bed in the Northeast Atlantic; and the second, a decision to allow the storage of CO2 in subsea sediments. [59,60]
In the first amendment, OSPAR stated that CO2 storage in the water column or on the sea bed “is not a sustainable storage option, is likely to result in harm to living resources and marine ecosystems and is thus neither a viable solution with regard to mitigating climate change nor compatible with the aims of the [OSPAR] Convention.” However, in the first amendment, OSPAR indicated that ocean storage of CO2 in the water column or on the seabed is nevertheless still under consideration in international forums. 
The OSPAR amendments provided a framework for its contracting national governments to develop permitting programs for CO2 storage. For example, a list of the minimum items required in an offshore CO2 storage permit included: a description of the project, including injection rates; types, amounts and sources of CO2; the location of the facility; characteristics of the geological formation; methods of transport; and a risk management plan, with monitoring and verification measures, mitigation steps and a site closure plan .
In July 2011 the contracting parties of the OSPAR Convention ratified the 2007 Amendments to allow for CO2 storage in subsea geological formations .
5.4. 2007 Amendment to the London Protocol
In 2007, an amendment to the London Protocol (Annex 1) allowed for storage of CO2, if the disposal is into a sub-seabed geological formation, if CO2 streams are “overwhelmingly” carbon dioxide, and as long as no wastes are added. This amendment provided that CO2 streams may only be considered if [60,61]:
disposal is into a sub-seabed geological formation;
they consist overwhelmingly of CO2. They may contain incidental associated substancesderived from the source material and the capture and sequestration processes used; and
no wastes or other matter are added for the purpose of disposing of those wastes or other matter.
The amendments to Annex 1 entered into force on 10 February 2007. In contrast to the OSPAR Convention Amendment that only covered the Northeast Atlantic, the 2007 London Protocol Amendment specifically prohibited direct injection of CO2 for OCS for all London Protocol contracting parties.
5.5. 2009 London Protocol amendment for transboundary transport of CO2
Article 6 of the London Protocol (on the export of wastes or other material) was largely interpreted by the contracting parties as prohibiting the export of CO2 from a contracting party for injection into sub-seabed geological formations. In 2009 Article 6 was amended to allow for cross-border transportation of CO2. 
As of 2011, there were 40 contracting parties to the London Protocol. Of these parties, 27 must also accept the 2009 amendment to Article 6 for it to enter into force. However, not all of the parties have been interested in offshore CO2 storage or cross-border movement of CO2, and have placed the ratification of Article 6 as a low priority. Cross-government cooperation will probably be required for ratification to occur. In some countries, the ratification may also be pending other laws and regulations that need to be changed for carbon storage and sequestration in general .
Therefore, although geological carbon sequestration in the ocean has been approved in principle the OSPAR Convention and even the London Protocol, the Article 6 amendment may continue to pose a policy barrier to OCS deployment in the foreseeable future.
5.6. Public outreach: Lessons from Hawaii
It is noteworthy that no field studies demonstrating OCS at a significant scale have been conducted so far prior to its prohibition through the 2007 London Protocol and OSPAR Convention amendments. The largest scale attempt at demonstrating OCS was the Hawaii CO2 direct injection experiment This section outlines the failure of the Hawaii experiment mainly fuelled by a lack of early public outreach, and outlines some lessons learnt from the Hawaii project. [62,63]
In 1997 the US Department of Energy, the New Energy and Industrial Technology Development Organization of Japan (NEDO) and the Norwegian Research Council (NRC) signed an agreement to conduct experiments to evaluate the behaviour of liquid CO2 releases in to the ocean. While the project was announced in Kyoto in 1997, with a high profile to demonstrate the sponsors’ commitment to CO2 mitigation, few resources were subsequently invested in public outreach.
The project scientists and sponsors selected an area off the coast of the Big Island of Hawaii to conduct the pilot CO2 study, based on technical feasibility and existing research infrastructure. However, they did not gauge the public perception prior to site selection. The local population only learnt of the injection project planned in their waters when it was first published in a newspaper article. In an area where the ocean is viewed as a major natural resource, the public perceived of the “dumping” of CO2 as a violation, and strongly opposed its continuation.
Eventually the pilot injection project was abandoned in Hawaii. In order to salvage the project, scientists attempted to instead conduct an injection study in Norway. However, here the actions of Greenpeace stopped any further testing, thus precluding completely any chance of field scale testing of direct-injection OCS.
Although the introduction of OCS was initially high profile the sponsors’ commitment to CO2 mitigation, few resources were subsequently invested in public outreach. Moreover, the sponsors largely did not include the public in their decision to site the pilot injection experiment in Hawaii, nor did they factor public perception of potentially conducting a CO2 injection experiment in an area where the ocean is viewed as a major environmental resource.
Reiner (2008) cited the US National Institute of Standards and Technology (NIST) 2002 workshop for “Best Practices for Communication of Science and Technology to the Public” as a resource that offered key recommendations for public outreach, including:
Illustrating both the scientific process and unresolved scientific questions, rather than showing a result based on a black box model
Using scientists in a public education role for a range of audiences (children and adult)
Incorporating a wide source of knowledge from others so as to avoid parochialism
Presenting the issues from the audiences’ point of view
Using face-to-face communications whenever possible to foster trust
Reaching out beyond the science-attentive public, e.g. presenting at shopping malls, to disadvantaged youth
Using multimedia and illustrations
Providing press releases in forms easily usable to time-strapped journalists
Avoiding perceptions of environmental injustice, bias or conspiracy
Including the public from the start to avoid charges of “sneaking up on us” or less than full disclosure
Avoiding letting the project become a “political football” by creating vocal supporters within the community
In addition, Reiner suggested that early outreach to the public via the internet during developmental stages of a project is important before the project becomes newsworthy and receives attention from mainstream media outlets. .
The lack of outreach is reflected in the low level of understanding that has remained among the public, as well as relatively low public acceptance of carbon capture and sequestration (both geologic and ocean). Reiner summarized the European Commission’s survey of the public from 25 countries of the European Union (the Eurobarometer) that showed that, in 2007 (at the same time as the OSPAR convention and London Protocol amendments), only 21% of those surveyed have heard of carbon capture and storage (geologic or ocean), compared with 53% for hydrogen energy and cars, 41% for fuel cells, and 44% for geothermal energy . In the US in 2004, only 2.5% of 1200 respondents in a web-based survey had previously heard of carbon sequestration. In 2007, Palmgren et al. surveyed 126 community respondents, who ranked OCS less favourable than geological carbon sequestration. Both carbon sequestration options were less favourable to the respondents than nuclear power .
Whether CO2 is introduced intentionally, or passively diffusing from the atmosphere to the ocean, the ocean is and will remain the largest sink of anthropogenic CO2. In addition to climate change implications of elevated atmospheric CO2, a further impact is the acidification of the ocean. Effects of increased acidity and pCO2 in organisms include respiratory distress (but some deep sea organisms take advantage of the CO2/O2 balance). There is also a risk of a reduced habitat as calcium carbonate stability zones decrease. However, further study is required to determine the variability of responses among marine species.
This chapter presented several methods by which direct injection of CO2 into the ocean could be introduced. Some injection technologies were developed that would theoretically, combined with proper siting of injection points, cause a relatively minor impact to marine ecosystems. Some pilot scale field studies began that would have provided more information about environmental impacts, but they were nixed due to public opposition stemming from a lack of extensive and continuous public outreach from the onset. Since 2007, international policies began to prohibit direct discharge of CO2 into the ocean, while favouring deep sea geological sequestration. CO2 leaks (e.g. in the form of droplets ) from geological structures to the ocean water column are however still possible , so continued research and studies about the mechanisms of CO2 leakage and the effects of increased dissolved carbon in the ocean continues to be an important topic of study for carbon sequestration.
This chapter contains work funded by Ocean Carbon Sequestration Program, Biological and Environmental Research (BER), U.S. Dept. of Energy (grant number DE-FG02-01ER63078), the National Energy Technology Laboratory, U.S. Dept. of Energy (grant number DE-FG26-98FT40334) and the Martin Family Fellows for Sustainability.
Intergovernmental Panel on Climate Change (IPCC) (B. Metz B., Davidson O. eds. Carbon Dioxide Capture and Storage: A Special Report of IPCC Working Group III, Cambridge University Press, Cambridge UK; 2005
Caldeira, K., Wickett, ME. Anthropogenic carbon and ocean pH. Nature 2003;425, 365-365.
R. Zeebe R., Rigwell A. Past changes in ocean carbonate history. In: Gattuso J-P., Hansson L., eds; Ocean acidification. Oxford; 2010 p.21-40.
Orr JC. Past and recent changes in the ocean carbonate system. In: Gattuso J-P., Hansson L., eds; Ocean acidification. Oxford; 2010 p.41-66.
Bigalke N., RehderG., Gust G. Experimental investigation of the rising behavioe of CO2 droplets in seawater under hydrate-forming conditions. Environmental Science and Technology 2008;(42)5241 – 5246.
Morel FMM., Hering JG. Principles and Applications of Aquatic Chemistry. Wiley-Interscience, 1993.
Alendal G., Drange H. Two-phase, near field modeling of purposefully released CO2 in the ocean. Journal of Geophysical Research, 2001;106(C1):1085–1096.
Lavigne and Gattuso. In: Gattuso J-P., Hansson L., eds; Ocean acidification. Oxford; 2010.
Haugen P., Drange H. Sequestration of CO2 in the deep ocean by shallow injection. Nature 1992;357(28):1065–1072.
Dickson G., Goyet C., editors. Handbook of Methods for the Analysis of the Various Parameters of the Carbon Dioxide System in Sea Water. ORNL/CDIAC-74. 1994.
Gattuso J-P., Hansson L., eds; Ocean acidification. Oxford; 2010.
Herzog HJ., Adams EE., Auerbach D., Caulfield J. Environmental impacts of ocean disposal of CO2. Energy Conversion and Management, 1996;37(6-8):999–1005.
Brewer PG., Peltzer ET., Walz P., Aya I., Yamane K., Kojima R., Nakajima Y., Nakayama N., Haugan P., Johannessen T. Deep ocean experiments with fossil fuel carbon dioxide: creation and sensing of a controlled plume at 4 km depth. Journal of Marine Research, 2005;63(1):9–33.
Adams EE., Golomb D., Zhang XY., Herzog HJ. Confined release of CO2 into shallow sea water. In Direct Ocean Disposal of Carbon Dioxide, TERRAPUB 1995; Tokyo p.153–164.
Sato T., Kajishima T., Naguosa R. CO2 sequestration at sea by gas-lift system of shallow injection and deep releasing. Environmental Science and Technology, 2000:34:4140–4145.
Nakanishi N., Ohsumi T., Shitashima K. Sequestering of CO2 in a deep ocean. Technical Report, Central Research Institute of Electric Power Industry, 1994; 1646 Abiko, Abiko-City, Chiba 270-11, Japan.
Caulfield JA., Adams EE. Auerbach DI., Herzog HJ. Impacts of ocean CO2 disposal on marine life: II. probablistic plume exposure model used with a time-varying dose-response analysis. Environmental Modeling and Assessment 1997; 2:345–353.
Sloan ED. Gas hydrates: Review of physical/chemical properties. Energy & Fuels, 1998;12(2):191–196.
Lee S., Liang L., Riestenberg D., West OR., Tsouris C., Adams E. CO2 hydrate composite for ocean carbon sequestration. Environmental Science and Technology, 2003; 37:3701–3708.
Rehder G, Kirby SH., Durham WB, Stern LA., Peltzer ET., Brewer PG. Dissolution rates of pure methane hydrate and carbon dioxide hydrate in undersaturated seawater at 1000m depth. Geochimica et Cosmochimica Acta 2004;68:285–292.
Holder G., Mokka L., Warzinski R. Formation of hydrates from singlephase aqueous solutions and implications for ocean sequestration of CO2. In: Preprints of Spring 2000 National Meeting in San Diego, CA. ACS Division of Fuel Chemistry, 2001.
Chen B. A numerical prediction on plume structure of liquid CO2 in the ocean - a near field model. In: Proceeding of the 5th International Conference on Greenhouse Gas Control Technologies. 2001; p. 417–422, 2001.
Tsouris C., McCallum S., Aaron D., Reistenberg D., Gabitto J., Chow A., Adams E. Scale-up of a continuous-jet hydrate reactor for CO2 ocean sequestration. AiChE Journal 2007; 53(4):1017–1027.
Sato T., Hama T. Numerical simulation of dilution process in CO2 ocean sequestration. In: Proceedings of the 5th International Conference on Greenhouse Gas Control Technologies. 2001; p. 475–480.
Crounse B., Wannamaker EJ., Adams EE.. Integral model of a multiphase plume in quiescent stratification. Journal of Hydraulic Engineering, 2007;133(1):70–76.
Socolofsky SA., Adams EE. Multi-phase plumes in uniform and stratified crossflow. Journal of Hydraulic Research, 2002;40(6):661–672.
Socolofsky SA., Adams EE. Liquid volume fluxes in stratified multiphase plumes. Journal of Hydraulic Engineering, 2003;129(11):905 – 914.
Riestenberg, D., Tsouris C., Brewer PG., Peltzer ET., Walz P., Chow A., Adams E. Field Studies on the Formation of Sinking CO2 Particles for Ocean Carbon Sequestration: Effects of Injector Geometry on Particle Density and Dissolution Rate and Model Simulation of Plume Behavior. Environmental Science and Technology, 2005:39, 7287-7293.
Chow A., Adams EE., Israelsson PH., Tsouris, C. Carbon dioxide hydrate particles for ocean carbon sequestration. Energy Proceedia, 2009;1(1), 4937-4944.
Chow AC., Adams, EE. Prediction of Drag Coefficient and Secondary Motion of Free-Falling Rigid Cylindrical Particles with and without Curvature at Moderate Reynolds Number. Journal of Hydraulic Engineering 2011; 137(11)1406 – 1414.
Wannamaker EJ., Adams EE. Modeling descending carbon dioxide injections in the ocean. Journal of Hydraulic Research, 2006; 44(3):324–337.
R. Schlitzer. Electronic atlas of WOCE hydrographic and tracer data now available http://www.ewoce.org. Eos Trans. AGU, 2000; 81(5):45.
Chow A., Adams EE. Particle laden flows through an inverted chimney with applications to ocean carbon sequestration. Environmental Fluid Mechanics 2012; 12(1) 3 – 21.
Orr, JC. Modelling of ocean storage of CO2---The GOSAC study, Report PH4/37, International Energy Agency, Greenhouse Gas R&D Programme, Cheltenham, UK, 2004; 96 pp.
Blackford J., Widdicombe S., Lowe D., Chen B. Environmental risks and performance assessment of carbon dioxide (CO2) leakage in marine ecosystems. In: Maroto-Valer MM., editor. Developments and innovation in carbon dioxide (CO2) capture and storage technology. 2010, CRC Press.
Turley C., Blackford J., Harman-Mounford N., Litt E., Llewellyn C., Lowe D., Miller P., Nightingale P., Rees A., Smyth T., Tilstone G., Widdcombe S.. Carbon uptake, transport and storage by oceans and the consequences of change. In: Hester RE., Harrison RM., Carbon Capture, Sequestration and Storage. Royal Society of Chemistry, 2010.
Auerbach I., Caulfield JA., Adams EE., Herzog HJ. Impacts of ocean CO2 disposal on marine life: I. a toxicological assessment integrating constant-concentration laboratory assay data with variable concentration field exposure. Environmental Modeling and Assessment, 1997;2:333–343.
Caulfield JA., Adams EE., Auerbach DI., Herzog HJ.. Impacts of ocean CO2 disposal on marine life: II. Probablistic plume exposure model used with a time-varying dose-response analysis. Environmental Modeling and Assessment, 1997;2:345–353.
Israelsson PH., Chow AC., Adams EE. An updated assessment of the acute impacts of ocean carbon sequestration by direct injection. International Journal of Greenhouse Gas Control 2010;4(2): p. 262-271.
Israelsson PH. Studies of Lagrangian Modeling Techniques with Applications to Deep Ocean Carbon Sequestration. PhD thesis. Massachusetts Institute of Technology; 2008.
Sato, T. Numerical Simulation of Biological Impact Caused by Direct Injection of Carbon Dioxide in the ocean. Journal of Oceanography 2004;60, 807-816.
Tamburri MN., Peltzer ET., Friederich GE, Aya I., Yamane K., Brewer PG. A field study of the effects of CO2 ocean disposal on mobile deep-sea animals. Marine Chemistry 2000; 72:95–101.
Kita J., Watanabe Y. Impact assessment of high-CO2 environment on marine organisms. In: Proceedings of the Eighth International Conference on Greenhouse Gas Control Technologies, 2006.
Kikkawa T., Sato T., Kita J., Ishimatsu A. Acute toxicity of temporally varying seawater CO2 conditions on juveniles of japanese sillago (Sillago japonica). Marine Pollution Bulletin, 2006; 52:621–625.
Barry JP, Widdicombe S, Hall-Spencer JM. Effects of ocean acidification on marine biodiversity and ecosystem function. In: Gattuso J-P., Hansson L., eds; Ocean acidification. Oxford; 2010, p.192-209.
Pörtner, H.-O., Gutowska, M., Ishimatsu, A., Lucassen, M., Meizner, F. and Seibel, B.A. (2010). Effects of ocean acidification on nektonic organisms. In: Gattuso J-P., Hansson L., eds; Ocean acidification. Oxford; 2010, p.-154-175.
Knoll AH., Bambach RK., Lykkeboe G. Blood gas transport in the cephalopod, Sepia officinalis. Journal of Experimental Biology 1982;99:331-8.
Childress, JJ. Are there physiological and biochemical adaptations of metabolism in deep-sea animals? Trends in and Evolution Ecology 1995;10(1), 30-36.
Riebesell U., Tortell, PD. Effects of ocean acidification on pelagic organisms and ecosystems. In: Gattuso J-P., Hansson L., eds; Ocean acidification. Oxford; 2010, p.99-121.
Rockström, J., Steffen W., Noone K., Persson Å., Chapin FS, Lambin E., Lenton TM, Scheffer M., Folke C., Schellnhuber H., Nykvist B., De Wit CA., Hughes T., van der Leeuw S.,. Rodhe H., Sörlin S., Snyder PK., Costanza R., Svedin U., Falkenmark M., Karlberg L., Corell RW., Fabry VJ, Hansen J., Walker B., Liverman D., Richardson K., Crutzen P., Foley. M. Planetary boundaries:exploring the safe operating space for humanity. Ecology and Society 2009.;4(2): 32. [online] URL: http://www.ecologyandsociety.org/vol14/iss2/art32/
Seibel BA., Thuesen EV., Childress JJ., Gorodezky LA. Decline in pelagic cephalopod metabolism with habitat depth reflects differences in locomotory efficiency. Biological Bulletin 1997;192(2) 262-278.
Vetter EW., Smith CR. Insights into the ecological effects of deep ocean CO2 enrichment: the impacts of natural CO2 venting at Loihi seamount on deep sea scavengers. Journal of Geophysical Research 2005;110(C09S13).
Hall-Spencer JM., Rodolfo-Metalpa R., Martin S. Volcanic carbon dioxide vents show ecosystem effects of ocean acidification. Nature 2008; 454:96-9.
Herzog H., Caldeira K., Reilly J. An issue of permanence: assessing the effectiveness of ocean carbon sequestration. Climatic Change 2003;59(3), 293-310.
Goldberg D., Slagle AL. A global assessment of deep-sea basalt sites for carbon sequestration. Energy Proceedia 2009;1:3675-3682.
Akai M., Nishio N., Iijima M., Ozaki M., Minamiura J., Tanaka T.. Performance and Economic Evaluation of CO2 Capture and Sequestration Technologies. Proceedings of the Seventh International Conference on Greenhouse Gas Control Technologies, 2004.
International Energy Agency (IEA) and Organisation for Economic Co-operation and Development (OECD). Legal Aspects of Storing CO2, 2007.
OSPAR Commission for the Protection of the Marine Environment of the North-East Atlantic, Press release. Ratification of OSPAR carbon capture and storage measures. October 28, 2011. http://www.ospar.org/html_documents/ospar/news/ospar_pr_11_ratification_of_ccs_measure_en.pdf. Accessed August 6, 2013.
4th Kyoto, Japan. Oslo and Paris Commission (OSPAR). OSPAR Decision 2007/1 to Prohibit the Storage of Carbon Dioxide Streams in the Water Column or on the Sea-bed. 25-29 June, 2007.
International Energy Agency (IEA), 2008. CO2 capture and storage: a key abatement option. 266 pp. http://www.iea.org/publications/freepublications/publication/name,35329,en.html. Accessed October 16, 2013.
International Energy Agency (IEA). Carbon Capture and Storage and the London Protocol. Options for Enabling Transboundary CO2 Transfer. 2011.
De Figueiredo MA., Reiner DM., Herzog HJ. Ocean carbon sequestration: A case study in public and institutional perceptions. Proceedings of the Sixth International Conference on Greenhouse Gas Control Technologies, 2002.
Reiner DM. A Looming Rhetorical Gap: A Survey of Public Communications Activities for Carbon Dioxide Capture and Storage Technologies. 2008; http://www.eprg.group.cam.ac.uk/wp-content/uploads/2008/11/eprg08012.pdf. Accessed Accessed August 6, 2013.
Palmgren CR., Morgan MG., de Bruin WB., Keith DW. Initial Public Perceptions of Deep Geological and Oceanic Disposal of Carbon Dioxide. In: Wilson EJ, Gerard. D., eds. Carbon Capture and Sequestration, Blackwell Publishing, Ames, Iowa; 2007.
Chen B., Nishio M, Song Y., Akai M. The fate of CO2 bubble leaked from seabed. In Gale J, Herzog H., Braitch J., eds. Greenhouse Gas Control Technologies 9, Proceedings of the Ninth International Conference on Greenhouse Gas Control Technologies (GHGT-9), Energy Proceedia 2009:1:4969-4976.